3.3.3 Aquatic Resources

Transcription

1 3.3.3 Aquatic Resources The discussion of aquatic resources is divided into five sections. The affected environment is discussed in Section and the environmental effects of the Project are discussed in Section Cumulative effects are described in Section Proposed measures are discussed in Section , and unavoidable adverse effects are addressed in Section Where existing, relevant, and reasonably available information from YCWA s PAD (YCWA 2010) was not sufficient to determine the potential effects of the Project on aquatic resources, YCWA conducted 21 studies: 1) Study 3.1, Aquatic Macroinvertebrates Upstream of Englebright Reservoir; 2) Study 3.2, Aquatic Macroinvertebrates Downstream of Englebright Dam; 3) Study 3.3, Special-Status Aquatic Mollusks; 4) Study 3.4, Special-Status Amphibians Foothill Yellow-legged Frog Surveys; 5) Study 3.5, Special-Status Amphibians Foothill Yellow-legged Frog Habitat Modeling; 6) Study 3.6, Special-Status Turtles Western Pond Turtle; 7) Study 3.7, Reservoir Fish Populations; 8) Study 3.8, Stream Fish Populations Upstream of Englebright Reservoir; 9) Study 3.9, Non-ESA-Listed Fish Populations Downstream of Englebright Dam; 10) Study 3.10, Instream Flow Upstream of Englebright Reservoir; 11) Study 3.11, Entrainment; 12) Study 3.12 New Colgate Powerhouse Ramping; 13) Study 3.13, Special-Status Amphibians - Focused 2013 Foothill Yellow-Legged Frog Surveys; 14) Study 3.14, Special-Status Turtles Focused 2013 Western Pond Turtle Surveys; 15) Study 7.2, Narrows 2 Powerhouse Intake Extension; 16) Study 7.8, ESA/CESA-Listed Salmonids Downstream of Englebright Dam; 17) Study 7.9, Green Sturgeon Downstream of Englebright Dam; 18) Study 7.10, Instream Flow Downstream of Englebright Dam; 19) Study 7.11, Fish Behavior and Hydraulics Near Narrows 2 Powerhouse; 20) Study 7.11a, Radio Telemetry Study of Spring- and Fall-run Chinook Salmon Downstream of Narrows 2 Powerhouse; 21) Study 7.12, Evaluation of Project Effects on Daguerre Point Dam and Hallwood-Cordua Fish Facilities; and 22) Study 7.13, Fish Stranding Associated with Shutdown of Narrows 2 Powerhouse Partial Bypass. With the exceptions of the studies described below, the studies are complete (Table 1.4-3): 1 Study 7.11, Fish Behavior and Hydraulics Near Narrows 2 Powerhouse. The study required YCWA to perform: 1) observations of fish behavior, including from onshore, snorkeling and using Dual-frequency Identification Sonar (DIDSON ) during changes in operations of the Narrows 2 Powerhouse; 2) pressure calculations at the Narrows 2 Powerhouse outlet; and 3) velocity measurements at a range of flows downstream of the powerhouse. YCWA has completed all the tasks for Study 7.11 and posted to the relicensing Website an Interim Technical Memorandum that was combined with the interim technical memorandum for Study 7.11a on March 3, YCWA anticipates 1 Studies 7.8, 7.9, 7.10, 7.11, 7.11a, 7.12 and 7.13 were conducted primarily with a focus on ESA-listed fishes and fall-run Chinook salmon in the Yuba River downstream of Englebright Dam. The results of these studies are summarized in Section to the extent needed to provide context to the overall aquatic resources in the basin, but with regards to ESA-listed species, these studies are discussed in detail in YCWA s Applicant-Prepared Draft BA. With regards to salmon, these studies are also discussed in detail in YCWA s Applicant-Prepared Draft EFH Assessments. The Applicant-Prepared Draft BA and Applicant-Prepared Draft EFH Assessment are included in Volume IV of YCWA s Application for New License. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

2 the study will be complete by March 31, 2016 when YCWA will file with FERC, as directed by FERC, a joint final technical memorandum for Studies 7.11 and 7.11a. Study 7.11a, Radio Telemetry Study of Spring- and Fall-run Chinook Salmon Downstream of Narrows 2 Powerhouse. The study requires YCWA to: 1) consult with Relicensing Participants regarding appropriate equipment to track Chinook salmon near Narrows 2 Powerhouse and test up to three types of equipment; and 2) capture, tag and track Chinook salmon movement near Narrows 2 Powerhouse. YCWA has completed the first task and posted to the relicensing Website an interim technical memorandum that is combined with the interim technical memorandum for Study 7.11 on March 31, 2016 that includes the results of the collaboration on which equipment would be tested and the testing. Work to be completed includes the second task, capturing, tagging and tracking Chinook salmon movement near Narrows 2 Powerhouse. The task was originally scheduled to occur in 2014 but due to an anomalous dry water year in 2014, YCWA was granted by FERC in a letter dated March 5, 2014 a one year extension to complete the study. The task will now occur in 2015, contingent on receiving the necessary agency permits. YCWA anticipates the study will be complete by March 31, 2016 when YCWA will file with FERC, as directed by FERC, a final joint technical memorandum for Studies 7.11 and 7.11a Affected Environment This section describes the condition of existing aquatic resources in eleven general areas: 1) fish populations; 2) fish entrainment into Project intakes; 3) fish behavior and hydraulics near Narrows 2 powerhouse; 4) fish stranding; 5) fish habitat versus flow relationships; 6) Daguerre fish facilities assessment; 7) amphibians; 8) aquatic turtles; 9) mollusks; 10) benthic macroinvertebrates; and 11) aquatic invasive species Fish Populations Information on fish populations in this document was primarily derived from current YCWA studies and syntheses of results of previous studies. Substantial information on the fish populations in the Yuba River downstream of Englebright Dam was obtained from the Yuba Accord M&E Program Draft Interim Report (RMT 2013). Fifty fish species have been reported to occur in the Yuba River watershed within the Project Area (Table ). Forty-four of these species occur within the stream reaches downstream of Englebright Dam 2 ; five of these species are found only within the reservoirs or impoundments upstream of Englebright Dam; and seven fish species have been observed in the stream environments upstream of Englebright Dam. Thirty-nine of the fish species that occur in the vicinity of the Project are resident and 11 are anadromous; 32 are warmwater species; and 18 are coldwater species. 2 Englebright Dam and Reservoir and surrounding federal land are administered by USACE. Exh. E - Environmental Report Application for New License April 2014 Page E ,

3 Table List of fish species that have been reported to occur in the Yuba River watershed within the Project Area. Common Name Fish Species Origin Life History Coldwater (C) Scientific Native (N) or Warmwater (W) Name Introduced (I) Anadromous (A) Resident (R) Status Upstream of Englebright Reservoir Stream Distribution Downstream of Englebright Dam Our House Diversion Dam Reservoir or Impoundment Distribution Log Cabin Diversion Dam New Bullards Bar Reservoir American shad Alosa sapidissima I W/A ,2,3,4,6,7, Bigscale logperch Percina macrolepida I W/R Black bullhead Ameiurus melas I W/R Black crappie Pomoxis nigromaculatus I W/R ,21,22 21,22 Bluegill Lepomis macrochirus I W/R ,2,3,4,5,6,7, ,21,22 20,21,22 Brook trout Salvelinus fontinalis I C/R ,22 21,22 Brown bullhead Ameiurus nebulosus I W/R ,5,6,7, ,20,22 -- Brown trout Salmo trutta I C/R -- 18,24 10, ,22 19,20,21,22 California roach Hesperoleucus symmetricus N W/R CSC -- 1,2,3,4,5,6,7, Channel catfish Ictalurus punctatus I W/R ,22 19,21,22 Common carp Cyprinus carpio I W/R ,21, ,21,22 Chinook salmon, Central Valley Spring Run Oncorhynchus tshawytscha N C/A FT, ST -- 1,2,3,4,5,6,7, Chinook salmon, Central Valley Fall- Late-fall Run O.tshawytscha N C/A NMFS-SC, CSC -- 1,2,3,4,5,6,7, Chum salmon O. keta N C/A CSC Cutthroat trout O. clarkia I C/R ,21, Fathead minnow Pimephales promelas I W/R ,22 -- Golden shiner Notemigonus crysoleucas I W/R ,5,6,7, ,22 -- Green sturgeon Acipenser medirostris N C/A FT Green sunfish Lepomis cyanellus I W/R -- 1,2,3,4,5,6,7, , 21,22 20 Hardhead Mylopharodon conocephalus N W/R CSC, USFS-S -- 1,2,3,4,5,6,7, ,21,22 Hitch Lavinia exilicauda N W/R Inland silverside Menidia beryllina I W/R Kokanee Oncorhynchus nerka I C/R ,21,22 19,21,22 Lake trout Salvelinus namaycush I C/R ,22 Largemouth bass Micropterus salmoides I W/R ,5,6,7, ,22 19 Mosquitofish Gambusia affinis I W/R ,2,3,4,5,6,7, Pacific lamprey Entosphenus [Lampetra] tridentatus N C/A USFWS-SC -- 1,2,3,4,5,6,7, Pink salmon Oncorhynchus gorbuscha N C/A CSC Prickly sculpin Cottus asper N C/R ,2,4,5,6,7, Rainbow trout Oncorhynchus mykiss N C/R -- 15,17,18,20,23,24 1,2,3,4,5,6,7, ,21,22 19,20,21,22 Redear sunfish Lepomis microlophus N W/R ,2,3,4,5, ,22 20 Riffle sculpin Cottus gulosus N C/R ,2,3,4,5,6,7, River lamprey Lampetra ayresii N A CSC -- 6, Sacramento blackfish Orthodon microlepidotus N W/R , Sacramento pikeminnow Ptychocheilus grandis N W/R -- 15,18,23 1,2,3,4,5,6,7, ,21,22 19,20,21,22 Sacramento splittail Pogonichthys macrolepidotus N W/R CSC Sacramento sucker Catostomus occidentalis N W/R -- 15,17,18,20,23 1,2,3,4,5,6,7, ,21,22 19,20,21,22 Smallmouth bass Micropterus dolomieu I W/R -- 17,18,23 1,2,3,4,5,6,7, ,22 19,20,21,22 Speckled dace Rhinichthys osculus N C/R ,2,3,4,5,6,7, Spotted bass Micropterus punctulatus I W/R , 21, 22 19,20,21,22 Steelhead trout, Central Valley DPS Oncorhynchus mykiss N C/A FT -- 1,2,4,5,6,7, Striped bass Morone saxatilis I W/A ,2, Threadfin shad Dorosoma petenense I W/R , ,22 -- Tule perch Hysterocarpus traskii N W/R ,2,3,4,5,6,7, Wagasaki Hypomesus nipponensis I W/R Warmouth Lepomis gulosus I W/R ,5, ,22 -- White catfish Ameiurus catus I W/R ,6,7, ,21,22 -- White crappie Pomoxis annularus I W/R ,7, ,21,22 21,22 White sturgeon Acipenser transmontanus I C/A Yellow perch Perca flavensis I W/R FT = Listed as threatened under the ESA; ST = Listed as threatened under the California Endangered Species Act; NMFS-S = Listed as a species of concern by the NMFS; USFWS-S - Listed as a species of concern by the USFWS; CSC = Listed as a species of special concern by the Cal Fish and Wildlife; USFS-S = Listed as Sensitive on US Forest Service land by the Forest Service. Sources of information reporting species occurrence: 1 = Beak (1989); 2= CDFG (1991); 3=Koslowski (2004); 4= Campos and Massa (2010a); 5= Campos and Massa (2010b); 6=Massa and Campos (2006); 7=Massa and McKibbin (2005); 8=Massa (2004); 9=Cramer Fish Sciences (2011); 10=RMT VAKI database; 11= Massa pers. comm. August 2012; 12=CALFISH (UC Davis 2012) (anecdotal); 13=Schilling (2003); 14=Campos pers. comm.. November 2012; 15=PGE NID 2010; 16=CDFG (2007); 17=Stillwater 2011; 18=YCWA Study 3.8 (2013); 19=DWR 2006; 20-YCWA Study 3.7; 21= CDFG 2008; 22=Rowan CDFW 2012 Pers. Comm.; 23=Gast et al. (2005); 24=YCWA Study 3.11 (2011). Englebright Reservoir April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

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5 The following discussion of fish populations includes species listed under the ESA and other special-status fish species 3,4 occurring in the Yuba River drainage. The discussion specifically describes fish populations in reservoirs and impoundments (i.e., Our House Diversion Dam Impoundment, Log Cabin Diversion Dam Impoundment, New Bullards Bar Reservoir, and Englebright Reservoir) and fish populations in stream reaches from upstream to downstream in the Yuba River drainage. The following geographic areas are addressed: 1) stream reaches upstream of the Project; 2) stream reaches and impoundments located within the Project; and 3) the Yuba River downstream of Narrows 2 Powerhouse, including fish populations in the Feather River from the confluence with the Yuba River to the Sacramento River. ESA-Listed Fish Species Three ESA-listed fish species occur in the Yuba River basin, all of which occur downstream of Englebright Dam and are listed as threatened. These are: 1) Central Valley spring-run Chinook salmon ESU; 2) Central Valley steelhead DPS; and 3) the North American green sturgeon southern DPS. These ESA-listed species are discussed in YCWA s Applicant-Prepared Draft BA, and EFH for salmon is discussed in YCWA s Applicant-Prepared Draft EFH Assessment. Special-Status Fish Species Eight fish species that occur in the Yuba River have been identified as special-status species (Table ). Each of these is described below. Hardhead (CSC) Hardhead (Mylopharodon conocephalus) is a large (i.e., up to 60 cm standard length [SL]), long-lived (i.e., ten years plus) minnow that is native to the Sacramento-San Joaquin River watersheds of Central California. Historically, the hardhead was considered a widespread and locally abundant species within its range. However, substantial alteration of its relatively specialized habitat requirements and predation, as well as competition from introduced black bass and other centrarchids, have resulted in population declines and isolated populations (Moyle 2002). Today, the species is still widely distributed in the Sacramento-San Joaquin drainage, as well as in the Russian River drainage, although abundance is considered to be substantially reduced. The current range of hardhead extends from the Kern River (Kern County), in the south to the Pit River (south of the Goose Lake drainage, Modoc County), in the 3 For the purpose of Exhibit E, a special-status fish species is considered one that is found on NFS land and listed by the Forest Service as Sensitive; listed by NMFS or USFWS as a Species of Concern; listed by Cal Fish and Wildlife as a Species of Special Concern; or a combination of the above but not listed as threatened or endangered on the ESA. Fish species listed as endangered or threatened under the ESA are discussed in Volume IV of YCWA s Application for New License. 4 No fish species Proposed for or a Candidate for listing as threatened or endangered under the ESA occur in the Yuba River. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

6 north. In the Sacramento River drainage, hardhead are present in most of the larger tributary streams as well as the Sacramento River. Considered a riverine species, hardhead have become well established in mid-elevation reservoirs, including reservoirs on the San Joaquin River in Fresno County, and the Pit River in Shasta County. The initial establishment of hardhead in recently impounded reservoirs is probably the result of residual populations of juvenile fish growing to large sizes before populations of predatory centrarchids, primarily black bass, were established (Moyle et al 1995). Hardhead is typically found within larger mid- and low-elevation streams where summer mean daily water temperatures exceed 20 C (Moyle and Nichols 1973, Moyle and Daniels 1982). The elevation range of hardhead is 10-1,448 m (30-4,750 ft) (Reeves 1964). Optimal summer temperatures appear to range between 24 and 28 C (Knight 1985). Hardhead are relatively intolerant of low DO levels, especially at higher temperatures, a factor which may limit their distribution to well oxygenated streams and the surface water of reservoirs (Cech et al. 1990). Adult hardhead generally rear in clear, deep (>1 m) pools with sand-gravel-boulder substrates and slow water velocities (<25 cm sec-1) (Moyle and Nichols 1973, Knight 1985, Moyle and Baltz 1985). Adult hardhead tend to remain in the lower portion of the water column; they rarely move into the upper water column (Knight 1985). Juvenile hardhead concentrate in shallow water close to the stream margin (Moyle and Baltz 1985). Spawning occurs during the spring (March-May), when hardhead migrate upstream to gravel riffles, often within tributary streams. Hardhead are bottom feeders that forage for benthic invertebrates and aquatic plant material in quiet water. Smaller, younger hardhead (<20 cm SL) feed primarily on mayfly and caddisfly larvae, and small snails (Reeves 1964). Larger, older hardhead feed more on aquatic plants (especially filamentous algae), as well as crayfish and other large invertebrates (Moyle et al 1995). Hardhead mature following their second year. Within Yuba County, hardhead have been reported to occur in the upper Yuba River, the lower Bear, Feather, and Yuba rivers, and the Honcut Creek headwaters (U.C. Davis 2012). Hardhead is the only special-status fish species confirmed 5 during YCWA s fish population surveys to occur in the area of the Project upstream of Englebright Dam. YCWA fish population studies downstream of Englebright Dam also confirmed that hardhead occur in the lower Yuba River, downstream of Englebright Dam (YCWA 2013a). Upstream of Englebright Dam, YCWA found hardhead only in Englebright Reservoir where the species was documented at all four gillnet locations and four of the five electrofishing sites (YCWA 2012c). Both juvenile and adult hardhead were captured in Englebright Reservoir where hardhead comprised 13.5 percent of the total number of fish collected. Gast and others (2005) observed adult hardhead in the South Yuba River at RM 3.9, approximately 0.3 mi downstream of the confluence with Owl Creek. They also observed hardhead during snorkel surveys within the Middle Yuba River between Our House Diversion Dam and the confluence of 5 Sacramento-San Joaquin Roach is reported to occur in the upper Yuba River watershed; however, the source does not provide any documentation. Exh. E - Environmental Report Application for New License April 2014 Page E ,

7 Oregon Creek (Gast et al. 2005). Hardhead may occur in the North Yuba River and potentially in any tributaries associated with the Project; however, none were observed or collected within these streams during any of YCWA s studies (YCWA 2012d). Adult and juvenile hardhead have also been documented in the Yuba River downstream of Englebright Dam during various surveys conducted since the late 1980s (Beak 1989; Kozlowski 2004; JSA 2003, 2008, 2009, 2010; RMT 2013; YCWA 2012a). Juvenile hardhead were routinely collected during juvenile salmon emigration studies on the Yuba River between 1999 and 2009 (YCWA 2012a, RMT 2013). Rotary screw traps (RST) operating near RM 7.2 ( ) 6 annually collected downstream migrating juvenile hardhead. Juvenile hardhead were also routinely observed between Englebright Dam and the Feather River during snorkel and electrofishing surveys conducted between 1985 and However, no hardhead were observed during the recent RMT snorkel survey in 2012 (RMT 2013). Adult and juvenile (< 20 cm SL) hardhead have been observed migrating past Daguerre Point Dam (RM 11.6), during the VAKI Riverwatcher TM migration survey 7 (Figure , YCWA 2012a). Both upstream and downstream migration was observed. Upstream migration occurred between January and October, but was concentrated during the May-June spawning migration period (Figure ). Downstream migration was observed between March and August, with the majority (66%) of downstream migration occurring during June. Figure Size distribution and direction of migrating hardhead observed using a VAKI Riverwatcher TM fish monitoring system at Daguerre Point Dam fishways (RM 11.6) between January 2004 and February RST surveys were ended in VAKI Riverwatcher surveys have continued through Reportable results are only available through April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

8 Figure Temporal distribution and direction of migrating hardhead observed using a VAKI Riverwatcher TM fish monitoring system at Daguerre Point Dam fishways (RM 11.6) between January 2004 and February Central Valley Fall- and Late Fall-run Chinook Salmon ESU 8 (FSC & CSC) Although fall- and late-fall-run Chinook salmon (Oncorhynchus tshawytscha) are considered a single species by the NMFS, this ESU in the Yuba River is essentially comprised entirely of fall-run-central Valley Chinook salmon. Fall-run Chinook salmon 9 has the classic ocean type life history in that adults enter rivers as mature individuals, migrate to spawning grounds and usually spawn 1-2 months after entry. The RMT (2013) developed representative temporal distribution estimates for fall-run Chinook salmon lifestages through review of previously conducted studies as well as recent and ongoing data collection activities of the M&E Program. The life stage-specific periodicities for fall-run Chinook salmon in the lower Yuba River are summarized in Table , and are discussed below. 8 Spring-run Chinook salmon is listed as threatened under both ESA and CESA. 9 The fall- and late-fall-run Chinook salmon in the Yuba River is essentially comprised entirely of fall-run-central Valley Chinook salmon. Exh. E - Environmental Report Application for New License April 2014 Page E ,

9 Table Life stage-specific periodicities for fall-run Chinook salmon in the Yuba River (shaded boxes indicate temporal utilization of the Yuba River). Life stage Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec Adult Immigration & Staging Spawning Embryo Incubation Fry Rearing Juvenile Rearing Juvenile Downstream Movement Fall-run Chinook salmon adult abundance has been estimated based on carcass surveys between 1953 and 2003 and counts of adults passing Daguerre Point Dam made with the VAKI Riverwatcher TM system from 2004 to present. JSA (2006) reported that the average spawning escapement estimate for was 24,563 fish, which was substantially higher than the average of 13,809 for the preceding period between 1972 and Overall, the average spawning escapement reported for the pre- and post-reservoir periods ( and ) was 12,906 and 16,050 fish, respectively (JSA 2006). For the period during which VAKI Riverwatcher TM data are available ( ) 10, the annual number of fall-run Chinook salmon estimated to have passed upstream of Daguerre Point Dam ranged from 1,022 in 2007 to 7,782 in 2005, with an average of 4,343 fish. The abundance of fall-run Chinook salmon during the past four years has been substantially higher since the low-point in abundance observed in For the last three consecutive years, an estimated total of 14,864 fall-run Chinook salmon have passed upstream of Daguerre Point Dam, with an average of 4,955 fish per year. For more detailed information regarding Central Valley fall-run Chinook salmon refer to the Applicant-prepared Draft EFH Assessment. 11 Low escapement in the Yuba River was consistent with record low escapement estimated throughout the Central Valley during this time period. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

10 Chum Salmon (CSC) Chum salmon (Oncorhynchus keta) has the widest natural geographical distribution of the Pacific salmons, ranging from Korea up along the Arctic coast of Russia, and from the Mackenzie River on the Canadian Arctic coast of North America southward into central California. Historically, the species was reported to occur in all streams from San Francisco to the Bering Straits, and was said to be abundant in the fall, from Sacramento northward (Moyle et al. 1995). Chum salmon have an anadromous life history that is typically completed in 3-5 years. The freshwater life stage is very short as chum fry immediately swim downstream upon emergence, migrating quickly to the estuary. In North America, there is a northern (early-run) stock that spawns from June through September and a southern (late-run) stock that spawns from August through January. In Washington, Oregon, and California, all stocks are late-run. The early-run fish generally spawn in main stems of streams, while the late-run fish spawn in smaller streams which have more favorable winter temperatures. Adults show strong homing behavior to their natal streams. They can spawn at 2-7 years of age, but primarily spawn at ages 3-5. Presently in California, chum salmon are rarely encountered. A few adults and juveniles are regularly observed in the Klamath River (Moyle et al. 1995). Adult chum salmon have also been reported in Humboldt Bay, the Eel River (Redwood Creek, Humboldt County), the South Fork Trinity River, the Smith River drainage, and in Mill Creek (Del Norte County). The southernmost freshwater occurrence of chum salmon recorded was in the San Lorenzo River (Santa Cruz County) in the early 1900s. In the 1880s, chum salmon were a minor portion of the salmon catch in the Sacramento River system along with pink, coho, and Chinook salmon (Moyle et al. 1995). Sixty-eight chum salmon were observed during a ten-year ( ) survey of the Sacramento River. Since then, a few fish have been observed in the Sacramento drainage, including one chum in the Yuba River in the mid-1970s, five at the Feather River Hatchery over the last 25 years, and several at Nimbus Fish Hatchery on the American River up until One adult chum salmon was recorded passing Daguerre Point Dam in November 2008 during the ongoing, VAKI Riverwatcher TM survey. None of the previously conducted or currently ongoing juvenile monitoring studies in the Yuba River have observed chum salmon. Exh. E - Environmental Report Application for New License April 2014 Page E ,

11 Pink Salmon (CSC) Pink salmon (Oncorhynchus gorbuscha) occur around the Pacific Rim of Asia and North America. However, the spawning distribution of pink salmon is much more restricted, extending from Puget Sound, Washington to Norton Sound, Alaska in North America and from North Korea to Anadyr Gulf, Russia (Moyle et al. 1995). Pink salmon live for two years. Adults move into fresh water between June and September and spawn from mid-july to late October, depending on the geographic location. Spawning in California has only been recorded in October (Fry 1967). Most pink salmon spawn in the intertidal or lower reaches of streams and river. Embryos hatch after 4-6 months of incubation, presumably in February and March in California. The alevins emerge from the gravel in April or May, after which the fry immediately begin to migrate downstream into the estuary. Juvenile migration is rapid and fish spawned within the lower reaches of the river usually reach the estuary in one night. Once in the estuary they form large schools and remain in the inshore areas for several months before moving out to sea. California is the southern extent of pink salmon range and although the species was probably never common in California, they have occurred in noticeable numbers in the past (Moyle et al. 1995). In the late 1880s, pink salmon were reported to occur in the Sacramento River system as well as in Humboldt County waters, and pinks were included in the salmon catch sent from the northern coast to San Francisco markets (U.S. Comm. Fish and Fisheries 1892). During the late 1800s, pink salmon were reported to occur in the Sacramento River, usually in October. During the 1930s, commercial fishermen on the Sacramento River reportedly captured a dozen or more pink salmon in some seasons (Hallock and Fry 1967). Thirty-eight pink salmon were reportedly observed in the Sacramento River system during the period from , with fish taken near Redding, in Mill Creek, and at Nimbus Fish Hatchery on the American River (Hallock and Fry 1967). Recent occurrences of pink salmon in the Sacramento River basin have been infrequent. Several pink salmon were observed in the American River during the early 1990s. Spawning does occur on occasion in the Sacramento-San Joaquin River system. Juvenile pink salmon were identified at the state J.E. Skinner Fish Protective Facility near Tracy in 1990 (Moyle et al 1995). Adult pink salmon have been observed in the lower Yuba River during the ongoing VAKI Riverwatcher TM survey at Daguerre Point Dam (RM 11.6) (Table ). So far, during the nine years that the survey has been ongoing ( ), nine observations of adult pink salmon have been recorded, all between April and September Altogether, seven adults were observed migrating upstream past Daguerre Point Dam, and two were observed passing downstream of the dam. Table Summary of pink salmon observed migrating past Daguerre Point Dam (RM 13.6) in the Yuba River during the VAKI Riverwatcher TM monitoring study from 2004 through Date Observed Length (cm) Direction 4/25/ Upstream 8/28/ Upstream April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

12 Table (continued) Date Observed Length (cm) Direction 9/9/ Upstream 9/16/ Downstream 9/16/ Upstream 9/16/ Downstream 9/16/ Upstream Sacramento-San Joaquin Roach (CSC) The Sacramento-San Joaquin roach (Lavinia symmetricus) is part of the California roach complex, which is comprised of various subspecies. The Sacramento-San Joaquin roach is found in the Sacramento and San Joaquin River drainages (except the Pit River), as well as tributaries to San Francisco Bay. Sacramento-San Joaquin roach are generally found in small, warm intermittent streams, and are most abundant in mid-elevation streams in the Sierra foothills and in the lower reaches of some coastal streams (Moyle 2002; Moyle and Daniels 1982). Assuming that the Sacramento-San Joaquin roach is indeed a single taxon, which is unlikely (Moyle 2002), it is abundant in a large number of streams, although it is now absent from a number of streams and stream reaches where it once occurred (Moyle 2002). Roach are tolerant of relatively high temperatures (30 to 35 C) and low oxygen levels (1 to 2 mg/l) (Taylor et al. 1982). However, they are habitat generalists, also being found in cold, well-aerated, clear "trout" streams (Taylor et al. 1982); in human-modified habitats (Moyle 2002; Moyle and Daniels 1982); and in the main channels of rivers. Reproduction of roach occurs from March through early July, depending on water temperature (Moyle 2002). Murphy (1943, as cited in CDFG 2008) states that spawning is determined by water temperature, which must be approximately 16 C for spawning to be initiated. During the spawning season, schools of fish move into shallow areas with moderate flow and gravel/rubble substrate (Moyle 2002). Within Yuba County, Sacramento-San Joaquin roach have been reported to occur in the upper Yuba River, the lower Bear and Feather rivers, the Middle Fork of the Feather River, and the Honcut Creek headwaters (U.C. Davis 2012). In addition, Sacramento-San Joaquin roach have been documented during the RST monitoring (Casey Campos, PSMFC, 2009 pers. comm. as cited in YCWA 2010). Sacramento Splittail (CSC) The Sacramento splittail (Pogonichthys macrolepidotus), a minnow, was federally listed as threatened on February 8, 1999, and delisted on September 22, 2003 (USFWS 2003a). Sacramento splittail is designated as a CSC (CDFG 2009, 2011). Exh. E - Environmental Report Application for New License April 2014 Page E ,

13 Splittail are large cyprinids, growing in excess of 30 cm and are adapted to living in freshwater and estuarine habitats as well as alkaline lakes and sloughs (Moyle 2002). Historically, splittail inhabited sloughs, lakes, and rivers of the Central Valley with populations extending upstream to Redding in the Sacramento River, to the vicinity of the Colusa- Sacramento River State Recreation Area, in Butte Creek/Sutter Bypass, to Oroville in the Feather River, to Folsom in the American River, and to Friant in the San Joaquin River (Moyle et al. 2004, USFWS 2003b). The current distribution is limited by dams and other barriers. Currently, the species is known to migrate up the Sacramento River to Red Bluff and up the San Joaquin River to Salt Slough in wet years as well as into the lower reaches of the Feather and American rivers (USFWS 2003b). Splittail have been documented in the Feather River watershed as far upstream as Oroville (upstream of the confluence with the Yuba River) (Moyle et al. 2004). The University of California Fish Website (UC Davis 2012) lists the Yuba River downstream of Englebright Dam among the watersheds where splittail occur, although no reference is provided for this determination. Sacramento splittail are typically found in water temperatures between 5 C and 24 C. However, fish acclimated to higher temperatures (29 C to 33 C) reportedly can survive rapid changes in water temperature for short periods of time (Moyle 2002). In laboratory studies conducted at the University of California at Davis, mean critical thermal minima (CTmin) and maxima (CTmax) for age-2 fish was 7 C and 29 C, respectively (Young and Cech 1996). The onset of Sacramento splittail spawning reportedly is associated with increasing water temperatures of 14 C to 19 C (Moyle 2002). Sacramento splittail reportedly prefer to spawn in water temperatures that range from 9 C to 20 C (Caywood 1974). Sacramento splittail have been suggested to occur in the Yuba River downstream of Englebright Dam (UC Davis 2012); however, YCWA could not find any verified observations of splittail. Pacific Lamprey (USFWS-SC) The Pacific lamprey (Entosphenus tridentatus) is not listed under the ESA or CESA; however, the species is identified as a Federal species of concern. A petition to list Pacific lamprey under the ESA was reviewed in 2003, with insufficient information to warrant listing (USFWS 2004d). The habitat requirements of Pacific lamprey have not been well studied in Central Valley streams. Much of the understanding of Pacific lamprey life history habitat and population traits is based on collective observations and evaluations of Pacific lamprey elsewhere throughout its range. Adult Pacific lampreys require clean, gravel-rich riffles in perennial streams to spawn successfully; these requirements are thought to be similar to those of salmonids. Pacific April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

14 lampreys spend well over half of their total life cycle in freshwater. The adult migration into freshwater towards upstream spawning areas primarily begins between early March and late June (Moyle 2002). Nests are built on gravel substrate, with moderately swift current, water temperatures typically from C, and at depths ranging from m (Moyle 2002). Adults typically die after spawning. Larval lampreys (ammocoetes) rear in sand and mud substrates, gradually moving downstream over the rearing period. Ammocoetes require water temperatures that are lower than 25 C (Moyle 1995). Meeuwig et al. (2004) found significant death or deformation of eggs and early stage ammocoetes in water with temperatures greater than 22 C. Following ammocoete metamorphosis, downstream migration coincides with high flow events in late-winter and early spring (Moyle 2002). The Pacific lamprey is anadromous (though some landlocked forms exist) and has two very distinct parts of its life cycle. Eggs hatch into larvae known as ammocoetes, usually within a freshwater stream. Ammocoetes burrow tail first into mud or soft substrate where they filter feed on algae and organic matter. The larval lampreys often move around the stream in their 5-7 year stay in freshwater. When the ammocoetes reach a length of around cm TL, they begin a drastic change in physiology and physical appearance, assuming a silvery form with large eyes and a sucking disc. The newly morphed lampreys swim downstream to the Pacific Ocean where they take on a new predatory lifestyle in an estuarine or saltwater environment, although rarely straying far from the mouth of their home stream. Pacific lampreys attack and feed on fish, including salmon and flatfish. Their stay at sea usually lasts 3-4 years in Canada, but may be shortened in more southern populations. Like salmon, the lamprey return to freshwater and migrate upstream to spawn and die. Most upstream movement occurs during the night under high flow conditions. Some streams have different runs of lamprey. Runs may be different in the timing of entry to freshwater or in the amount of time spent in freshwater before breeding occurs. Within the lower Yuba River, the Pacific lamprey is abundant and well distributed (YCWA 2012a). Snorkel and electrofishing surveys of the Yuba River downstream of Englebright Dam (RM 24) documented that juvenile lamprey occur throughout most of this reach (RM 0 to RM 22). Juvenile Pacific lamprey were the fourth most abundant species (out of 25 species) captured during downstream migration surveys conducted at RM 7.2 from 1999 through Juvenile Pacific lamprey downstream migration occurred throughout the year with the peak of migration occurring between December and February (YCWA 2012a). River Lamprey (CSC) The river lamprey (Lampetra ayresii) occurs along most of the Pacific Coast, from just north of Juneau, Alaska, to San Francisco Bay in California. However, detailed information on their distribution and abundance is lacking. River lampreys are associated with large river systems such as the Fraser, Columbia, Klamath, Eel, and Sacramento rivers. Beamish (1980) and others have noted that river lamprey appear to be concentrated only in particular rivers, and only in the lower portions of these large rivers. A petition to list river lamprey under the ESA was reviewed in 2003, with insufficient information to warrant listing (USFWS 2004d). Exh. E - Environmental Report Application for New License April 2014 Page E ,

15 Little information is available on river lamprey life history. According to Moyle (2002), their life span is six to seven years. Adult lampreys spawn in gravel bottomed streams, at the upstream end of riffle habitat. Both sexes construct the nests, often moving stones with their mouths. River lampreys lay 11,400 to 37,300 eggs per adult female. Adults typically die after the eggs are deposited and fertilized. After the eggs hatch, young ammocoetes drift downstream to areas of low velocity and silt or sand substrate. They remain burrowed in the stream bottom, living as filter feeders on algae and detritus for two to seven years. Metamorphosis from the ammocoete to macropthalmia life stage occurs between July and April. At this time, macropthalmia are thought to live deep in the river channel, which may explain why they are rarely observed. As adults, their oral disc develops just before they enter the ocean between May and July. During the approximately ten weeks they are at sea in the parasitic phase, they remain close to shore, feeding primarily on smelt and herring near the surface. After the adult feeding phase, river lamprey migrate to spawning areas and cease feeding. Their degree of fidelity to their natal streams is unknown. Riffle and side channel habitats are important for spawning and for ammocoete rearing. Because lamprey ammocoetes colonize areas and are relatively immobile in the stream substrates, good water quality is essential for rearing. Adults feed in nearshore marine and estuarine habitat. River lampreys were consistently observed emigrating past the RSTs survey site near Hallwood Boulevard (RM 7.2) between 1999 and 2010 (YCWA 2013a). A total of 340 juvenile river lampreys were counted at the RST sites during the survey period. Reservoir/Impoundment Fish Populations Fish populations were assessed in four impoundments in the Yuba River watershed: Our House Diversion Dam Impoundment; Log Cabin Diversion Dam Impoundment; New Bullards Bar Reservoir; and Englebright Reservoir. Our House and Log Cabin impoundments were assessed in 2012 in association with YCWA s Study YCWA conducted Study 3.7 at New Bullards Bar Reservoir and at Englebright Dam in 2012 to supplement information previously collected and reported by Cal Fish and Wildlife. Our House Diversion Dam Impoundment YCWA is unaware of any existing historical information regarding fish populations in the Our House Diversion Dam Impoundment. YCWA s Study 3.11 conducted fish sampling in the fall of 2012 utilizing backpack and boat electrofishing, gill netting, and hook-and-line from the impoundment upstream 1.3 mi. Sampling only in the impoundment, resulted in the capture of 94 rainbow trout (Oncorhynchus mykiss), representing all life stages and two brown trout (Salmo trutta). A mark recapture estimate done for YCWA s Study 3.11 resulted in a rainbow trout population estimate for the Our House Diversion Dam impoundment of 150 fish, with a 95 percent confidence interval of 124 to 189 fish.the only other fish species observed during the tagging effort were Sacramento sucker and Sacramento pikeminnow. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

16 Log Cabin Diversion Dam Impoundment YCWA is unaware of any existing historical information regarding fish populations in the Log Cabin Diversion Dam Impoundment. YCWA s Study 3.1 conducted fish sampling from the impoundment upstream 1.7 mi. Within the Log Cabin Diversion Dam Impoundment only, a total of five rainbow trout were captured using hook-and-line sampling. No other fish species were found. New Bullards Bar Reservoir New Bullards Bar Reservoir has a long history of fish stocking activities by Cal Fish and Wildlife dating back to 1959 (Central Valley Fish Hatchery 1959; CDFG 2008). Salmonid species have been the primary fishes planted in the reservoir over the years. These have included rainbow trout, kokanee (Onchorhynchus nerka), brook trout (Salvelinus fontinalis), and cutthroat trout (Onchorhynchus clarkii). Table provides relative stocking numbers by species where information was available from 1969 through Table Known stocked fish species in New Bullards Bar Reservoir from 1969 through Fish Species Year(s) Estimated Estimated Common Name Scientific Name Planted Yearly Mean Total Rainbow trout (various origin) Onchorhynchus mykiss ,000 1,800,000 Eagle Lake rainbow trout O. mykiss aquilarum 1979, 1982,1983, 1985, 1999, 2000, 2001, 2007, 2008 & , Kamloops rainbow trout O. mykiss kamloops Unknown Kokanee O. nerka ,000 5,200,000 Cutthroat trout O. clarkia Brook trout Salvelinus fontinalis ,215 40,215 Spotted bass Micropterus punctulatus Sources: CDFG 2008; J. Rowan, CDFG, personal communication, 2012 YCWA conducted Study 3.7 at New Bullards Bar Reservoir in 2012 to supplement and update known historical fisheries information. Sampling included gill netting at eight sites and boat electrofishing at ten sites, both performed once in January 2012 and once in June Sampling sites were distributed at representative locations throughout the reservoir. At each gill netting site, four adult-sized mesh nets and four juvenile-sized mesh nets were deployed. Boat electrofishing sites were each approximately 1,000-meters in length. New Bullards Bar Reservoir supports a diverse assemblage of cold and warm water fishes, including sport and nongame fishery resources. Study 3.7 documented 11 fish species over the two sampling events, compared to 22 fish species that have been previously documented in the reservoir (Table and ). No new species were found. Spotted bass (Micropterus punctulatus) was the most common species (n=644) collected by YCWA, accounting for 66.3 percent of the total and 65.7 percent of the biomass. Other common centrarchids were bluegill (Lepomis macrochirus) (n=79, 8.1% of total) and green sunfish (Lepomis cyanellus) (n=63, 6.5% of total). Salmonid species were represented by rainbow trout (n=49, 5.0% of total) and kokanee (n=47, 4.8% of total), which have been historically stocked in the reservoir by Cal Fish and Wildlife. Other warmwater species included common carp (Cyprinus carpio) (n=56, 5.8% of total; and 21.8% of biomass), Sacramento sucker (Catostomus occidentalis) (n=18, 1.9% of total), and Sacramento pikeminnow (Ptychocheilus grandis) (n=9, 0.9% of total). Less common warm-water species documented included white catfish (Ameiurus catus), brown bullhead Exh. E - Environmental Report Application for New License April 2014 Page E ,

17 (Ameiurus nebulosus), and white crappie (Pomoxis annularis). Largemouth bass (Micropterus salmoides) and smallmouth bass (Micropterus dolomieu) (historically documented) were not found in the current study. Table Summary of relative abundance, length, and weight of all fish species collected at New Bullards Bar Reservoir in January and June 2012 in order of abundance. Fish Species Percentage Length (mm) Weight (g) Mean Common Scientific N of Total Name Name (%) Min Max Mean Min Max Mean Micropterus Spotted bass , punctulatus Bluegill Lepomis macrochirus Green sunfish Lepomis cyanellus Common carp Cyprinus carpio ,100 1, Rainbow trout Oncorhynchus mykiss Kokanee Oncorhynchus nerka Sacramento sucker Catostomus occidentalis Relative Condition , Sacramento pikeminnow Ptychocheilus grandis , White catfish Ameiurus catus Brown bullhead Ameiurus. nebulosus ,300 1, White crappie Pomoxis annularis Key: N = number g = grams mm = millimeters 1 Species with poor fit regressions did not have a reportable condition factor. The mean relative condition factor of all game species was at least 1.0 (i.e., fish in average or better condition). Although spotted bass were collected at all sampling sites, almost half of all rainbow trout captured by electrofishing were found at the upper end of the reservoir. Gillnet catches were highest in nets set near shore, and catch was lowest at the site closest to the dam. Only one kokanee and one spotted bass were captured in deep-water nets that were set closest to the deep-water intakes at the dam. YCWA also assessed 13 tributaries of New Bullards Bar Reservoir for upstream passage in 2012 as a component of Study 3.7. The sections of streams assessed were within the normal maximum water surface elevation (NMWSE) of the reservoir when the reservoir was at low pool. Of the 13 tributaries, four were determined to be inaccessible due to waterfalls over bedrock and very steep gradients combined with low flows. The remaining nine streams were considered accessible and were walked to document potential barriers to adfluvial spawning fish. The nine streams included: North Yuba River; and Slate, Deadwood, Indian/Slapjack, Bridger, Willow, Mill, Little Oregon, and Burnt Bridge creeks. Four of the nine accessible tributaries (i.e., Deadwood, Bridger, Mill, and Burnt Bridge creeks) had potential barriers to fish passage. Seven of the eight potential barriers were leaping barriers and one was a shallow water barrier. Only one potential leaping barrier in Mill Creek would not be fully inundated by the reservoir at normal maximum water surface elevation. Fish species found in the accessible tributaries were brown trout (Salmo trutta) (Mill Creek only), rainbow trout, and Sacramento sucker. Six of the nine tributaries contained only rainbow trout. The North Yuba River and Willow Creek contained both rainbow trout and Sacramento sucker. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

18 Englebright Reservoir Englebright Reservoir was planted extensively from 1950 through Rainbow trout was the most commonly planted fish species over this period with about 756,000 fish planted from 1965 through 2007 (CDFG 2008) and additional plants from 2011 through The most recent plants ( ) were triploid (sterile) rainbow trout. Other species with sporadic or isolated plantings from 1965 through 2008 included brown trout,black crappie (Pomoxis nigromaculatus), brook trout,kokanee, lake trout (Salvelinus namaycush), and white crappie (Pomoxis annularis ). No species other than rainbow trout or brown trout have been planted since Table provides relative stocking numbers by species, where information was available, from 1965 through Table Known stocked fish species in Englebright Reservoir from 1965 through Fish Species Year(s) Estimated Estimated Common Name Scientific Name Planted Yearly Mean Total Brown trout Salmo trutta 1965, 1969, 1973, 1981, 1983, 1984, 1986, 1997, 2006, 2007 & ,459 38,000 Rainbow trout(various origin) Onchorhynchus mykiss , 2011 & ,000 Eagle Lake rainbow trout O. mykiss aquilarum , Kokanee O. nerka 1965, 1966 & ,107 40, ,000 Brook trout Salvelinus fontinalis Lake trout S. namaycush 1965 & ,487 3, Black crappie Pomoxis nigromaculatus White crappie P. annularis Source: CDFG 2008; J. Rowan, CDFG, personal communication, 2012 As a component of Study 3.7, YCWA conducted fish population sampling at Englebright Reservoir in 2012 to supplement and update known historical fisheries information. Sampling included gill netting at four sites and boat electrofishing at five sites, performed once in June YCWA s Study 3.7 documented 10 fish species, compared to 18 fish species found at least once previously (Table ). Two species not previously documented, redear sunfish (Lepomis microlophus) and green sunfish (Lepomis cyanellus), were found in Sacramento sucker (n=114, 31.5%) and spotted bass (n=96, 26.5%) were the more common species collected, followed by hardhead (n=49, 13.5%), rainbow trout (n=30, 8.3%), bluegill (n=27, 7.5%), and Sacramento pikeminnow (n=25, 6.9%) (Table ). Sacramento sucker, Sacramento pikeminnow, hardhead, spotted bass, and rainbow trout catches included individuals from an exceptionally wide range of size classes. No species accounted for the majority of biomass (total weight); however, biomass of Sacramento sucker was more than double that of any other species. Table Summary of relative abundance, length, and weight of all fish species collected at Englebright Reservoir in June 2012 in order of abundance. Species Percentage Length (mm) Weight (g) Mean Common Scientific N of Total Relative Min Max Mean Min Max Mean Name Name (%) Condition 1 Sacramento sucker Catostomus occidentalis , Spotted bass Micropterus punctulatus , Hardhead Mylopharodon conocephalus , Rainbow trout Oncorhynchus mykiss Bluegill Lepomis macrochirus Exh. E - Environmental Report Application for New License April 2014 Page E ,

19 Table (continued) Species Percentage of Total (%) Length (mm) Weight (g) Mean Relative Min Max Mean Min Max Mean Condition 1 Common Scientific N Name Name Sacramento pikeminnow Ptychocheilus grandis , Common carp Cyprinus carpio ,775 6,500 3, Brown trout Salmo trutta Smallmouth bass Micropterus dolomieu Green sunfish Lepomis cyanellus Redear sunfish L. microlophus Key: N = number g = grams mm = millimeters 1 Species with poor fit regressions did not have a reportable condition factor. Mean relative condition factor of all species was at least 1.0. Bass, including spotted bass, smallmouth bass, and largemouth bass, accounted for about 28 percent of the reported sport catch in Englebright Reservoir in (DWR 2006). These same species also represented about 28 percent of the fish collected in the 2012 study. Stream Fish Populations Stream fish populations within the vicinity of the Project are discussed by reach, beginning in the uppermost portion of the watershed and extending downstream to the confluence of the Feather River and the Sacramento River. The reaches are: Middle Yuba River Upstream of Our House Diversion Dam. North Yuba River Upstream of New Bullards Bar. South Yuba River Upstream of Englebright Reservoir. Oregon Creek Upstream of Log Cabin Diversion Dam. Middle Yuba River, Our House Diversion Dam Reach. Oregon Creek, Log Cabin Diversion Dam Reach. Middle Yuba River, Oregon Creek Reach. North Yuba River, New Bullards Bar Dam Reach. Yuba River, North Yuba River/Middle Yuba River Reach. Yuba River, New Colgate Powerhouse Reach. Yuba River Narrows Reach Downstream of Englebright Dam downstream to Narrows 1 and Narrows 2 powerhouses. Yuba River Garcia Gravel Pit Reach Downstream of Narrows Reach to Daguerre Point Dam. Daguerre Point Dam Reach, Downstream to terminus of the Yuba Goldfield. Simpson Lane Reach Downstream to the confluence with the Feather River. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

20 Feather River Reach (i.e., the Feather River) Downstream of the Yuba River to the Sacramento River. Figure provides a spatial reference for the reaches identified above. Exh. E - Environmental Report Application for New License April 2014 Page E ,

21 Figure Study area reaches. Note: the Feather River Reach (Feather River downstream of the Yuba River) eventually flows into the Sacramento River. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

22 Information regarding fish populations on stream reaches in the Middle Yuba River upstream of Our House Diversion Dam, the South Yuba River, and on the North Yuba River upstream of New Bullards Bar Reservoir was derived from recent relicensing studies by NID and PG&E) (PG&E and NID 2010). Historical stocking records from Cal Fish and Wildlife are discussed where available. Additional information on fish distribution in the Middle Yuba River upstream of Our House Dam was derived from fisheries studies conducted in support of YCWA s proposed Sediment Pass-Through Program (Stillwater 2011). 12 YCWA also conducted Study 3.8 and Study 3.7. Study 3.8 was conducted upstream of Englebright Reservoir and included a site on the Middle Yuba River upstream of Our House Diversion Dam and a site on Oregon Creek upstream of Log Cabin Diversion Dam. Study 3.7 included an assessment of tributary fish populations in the North Yuba River upstream of New Bullards Bar Reservoir. Information regarding fish populations on stream reaches in the mid-region of the watershed (i.e., between the diversions in the upper watershed and Englebright Dam) was largely derived from YCWA s relicensing studies. Additional information on fish distribution in the Project Area is derived from fisheries studies conducted in support of YCWA s Sediment Pass-Through Program (Stillwater 2011) and historical fish distribution snorkel surveys (Gast et al., 2005). YCWA s Study 3.8 included four sites on the Middle Yuba River below Our House Dam, one site on the North Yuba River downstream of New Bullards Bar Dam, one site on Oregon Creek downstream of the Log Cabin Diversion Dam, and three sites on the Yuba River above Englebright Reservoir. Information on fish populations in the Yuba River downstream of Englebright Dam was identified based on results of Study 3.9 (YCWA 2013a), Study 7.8 and Study 7.9. Information on fish populations in the Feather River, downstream of the Yuba River were primarily obtained from studies conducted as part of the Oroville Facilities Project, which is the subject of the Final Environmental Impact Statement for the Oroville Facilities (P ) issued May 18, Upstream of Englebright Reservoir A transition fishery occurs in the stream reaches of the Project and the surrounding vicinity. Fish distribution information obtained from historical accounts and recent studies by YCWA identified six fish species that occur in project reaches. Table provides an overview of fish species present in the Project area based on historical reports and YCWA s Study The Sediment Pass-through Program is in the permitting phase and has not been implemented. Exh. E - Environmental Report Application for New License April 2014 Page E ,

23 Table Overview of fish species present from YCWA s Study 3.8 conducted in 2012 and 2013, as well as documented species presence from historical reports. Project Reach Site RM Rainbow Trout Brown Trout Sacramento Pikeminnow Sacramento Sucker Smallmouth Bass Kokanee Speckled Dace Middle Yuba River Upstream of Our House Diversion Dam Oregon Creek Upstream of Log Cabin Diversion Dam Middle Yuba River, Our House Diversion Dam Reach Oregon Creek, Log Cabin Diversion Dam Reach Middle Yuba River, Oregon Creek Reach North Yuba New Bullards Bar Dam Reach Yuba River, North Yuba River/Middle Yuba River Reach Yuba River, New Colgate Powerhouse Reach Source: Gast et al. 2005; NID & PG&E 2010, YCWA 2013 Middle Yuba River Upstream of Our House Dam Oregon Creek Upstream of Log Cabin Diversion Dam Middle Yuba River Downstream of Our House Dam Middle Yuba River Upstream of Oregon Creek Oregon Creek Upstream of Middle Yuba River Middle Yuba River Downstream of Moonshine Creek Middle Yuba River Downstream of Yellowjacket Creek North Yuba River Upstream of Middle Yuba River Yuba River Downstream of Middle Yuba River Yuba River Upstream of New Colgate Powerhouse Yuba River Downstream of New Colgate Powerhouse Key: = Present in YCWA s Study 3.8; Shaded cells = reported to be present, but might or might not have been found by YCWA. Middle Yuba River Upstream of Our House Diversion Dam Cal Fish and Wildlife does not stock fish in this area of the Middle Yuba River. The fishery in this reach is transitional 13 from the trout-dominated, coldwater fishery of higher elevations to a warm water fishery. Fish density estimates based on multi-pass snorkeling about 1.3 mi upstream of Our House Diversion Dam in 2008 and 2009 by PG&E and NID (2010) indicated that Sacramento sucker was most abundant (318 1,885 fish-per-mile [fish/mi]), followed by rainbow trout ( fish/mi), and Sacramento pikeminnow (0 68 fish/mi). YCWA s Study 3.8 included one electrofishing site upstream of Our House Diversion Dam at RM 13.3, which was comprised of low-gradient riffle and glide habitat. Spawning gravel suitable for resident trout, fish passage impediments, and large woody material (LWM) were not 13 A transition fishery is one that includes both coldwater and warmwater fishes and is typically found in the Sierra in lower elevations where the fish community transitions from a coldwater fishery dominated by trout in the higher elevations to a warm water fishery in the lower elevations. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

24 observed at this site. The results of data collected in 2012 included estimated fish densities similar to previous surveys for Sacramento sucker (917 fish/mi), rainbow trout (409 fish/mi), and Sacramento pikeminnow (131 fish/mi). In 2013, fish densities were estimated to be 160 fish/mi for Sacramento sucker and 16 fish/mi for pikeminnow. Rainbow trout were not captured in Several sampled fish were found to be carrying an unidentified species of parasitic anchor worm (i.e., a copepod of the genus Lernaea, possibly L. cyprinacea) upstream of Our House Dam. Aside from small lesions at the point of attachment, these fish were vigorous and healthy in appearance. Results of the two year study are summarized in Table YCWA s fry emergence assessment (a component of Study 3.8) indicated that rainbow trout spawned from April 12 to May 19 in Emergence was calculated to have occurred between May 30 and June 20, Table Summary of 2012 and 2013 fish population information collected by quantitative electrofishing for the Middle Yuba River upstream of Our House Diversion Dam (RM 13.3). Species Rainbow Trout Sacramento Pikeminnow Sacramento Sucker Abundance Fork length (mm) Biomass Condition factor Age class frequency in fish/mile (% of total) 1 Year no. collected by pass (total) (23) (0) (8) (1) (53) (10) % of fish collected 27.4% 0.0% 9.5% 9.1% 63.1% 90.9% estimated section abundance % confidence interval Relative Stock Density 17 NA 1 NA NA 2 NA fish/100m fish/mi mean (range) (57-258) (62-82) (106) (56-162) (62-126) weight of fish collected (g) mean weight (g) (range) ( ) ( ) (9) ( ) estimated section biomass (g) g/100m lbs/ac kg/ha (3.3-23) relative condition range NA (80%) (100%) 0 (0.0%) 753 (82.1%) 112 (70.0%) 1 0 (0%) -- 0 (0.0%) 16 (100.0%) 147 (16.1%) 48 (30.0%) 2 and older 82 (20%) -- 0 (0.0%) 0 (0.0%) 16 (1.8%) 0 (0.0%) Not applicable because of small sample size. Electrofishing conducted in 2011, as a component of YCWA s proposed Sediment Pass-Through Program, resulted in capture of similar species as other studies (Stillwater Sciences 2011). Twenty-three rainbow trout and five Sacramento sucker made up the catch above Our House Diversion Dam. Rainbow trout ranged from 60 to 120 mm fork length (FL). Age class distribution could not be assessed for rainbow trout at this site due to low capture frequency; however, the age class structure upstream of Our House Dam is likely to be similar to the age class structure downstream of Our House Dam, thus rainbow trout captured were estimated to Exh. E - Environmental Report Application for New License April 2014 Page E ,

25 fall between the 0+ and 1+ age classes. High stream flows at this site prevented a multiple-pass regressions analysis and prohibited population analyses beyond identifying species composition. As part of Study 3.11, YCWA conducted backpack electrofishing, gillnetting, and hook-and-line sampling in the fall of Sampling began at Our House Diversion Dam and concluded approximately 1.3 mi upstream. The effort resulted in the capture of 187 rainbow trout, representing all lifestages, and two adult brown trout. Other fish species observed during the tagging effort were Sacramento sucker and Sacramento pikeminnow. North Yuba River Upstream of New Bullards Bar Quantitative fish sampling utilizing snorkeling and electrofishing occurred at three sites on the North Yuba River upstream of New Bullards Bar Reservoir in 2008 and 2009 (PG&E and NID 2010). The assessment indicated that rainbow trout were most abundant (1,602 4,566 fish/mi), followed by Sacramento sucker and low numbers of Sacramento pikeminnow and brown trout. The relative species composition by number in the North Yuba River changes in a downstream progression from almost entirely trout to a community of trout, sucker, and pikeminnow at elevations below approximately 915 m. In general, trout density and biomass in the North Yuba River decreased with elevation. Trout captured by electrofishing ranged from mm FL, with an average of 112 mm. The size classes of trout observed during snorkeling surveys ranged from 0 50 mm to mm, with a majority of the trout in the mm size classes. Rainbow trout ages in the North Yuba River ranged from zero to four years and brown trout ages ranged from zero to five years. Age-0 and age-1 trout were the most abundant age classes of rainbow and brown trout. During YCWA s Study 3.7, snorkel surveys were conducted in the North Yuba River from the confluence with New Bullards Bar Reservoir upstream approximately 610 m. Snorkelers primarily observed rainbow trout (n=23) followed by Sacramento sucker (n=15). Rainbow trout averaged 260 mm FL and Sacramento sucker averaged 361 mm FL. South Yuba River Upstream of Englebright Reservoir Fish stocking in the South Yuba River has occurred at Washington, Highway 80, and Bridgeport. Stocking in the Washington area occurred from 1951 through 2003, accounting for total plants of about 354,000 rainbow trout, 10,300 brown trout, and 1,620 rainbow trout (Kamloops and Coleman strains) (CDFG 2007). At the Highway 80 location, nearly 903,000 rainbow trout were released between 1950 and 1978, the last recorded planting at this location (CDFG 2007). About 990 eastern brook trout and 4,000 brown trout also were stocked at this location. Only three stocking events are documented at the Bridgeport site, all between 1998 and 2000, and 2,350 rainbow trout were released during this period (CDFG 2007). The South Yuba River near Englebright Reservoir is at a relatively low elevation (161 m [528 ft]) and supports a predominantly warmwater fishery. Snorkeling surveys conducted in 2004 upstream of Englebright Reservoir observed only pikeminnow at a sampling site approximately 3.5 mi upstream and first encountered rainbow trout at the next upstream sampling location (RM 4) (Gast et al 2005). Snorkeling surveys were conducted in 2009, on the South Yuba River at RM 0.8 (PG&E and NID 2010). Results April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

26 indicated smallmouth bass was most abundant species (estimated 845 fish/mi), followed by Sacramento pikeminnow (114 fish/mi), rainbow trout (16 fish/mi), and green sunfish (8 fish/mi). Multiple age classes of smallmouth bass were observed, with age-0 fish representing 58 percent of the total. The few rainbow trout observed were age-2 or older. Limited electrofishing resulted in collection of three rainbow trout and one smallmouth bass. Oregon Creek Upstream of Log Cabin Diversion Dam YCWA found limited historical information regarding the fish community in Oregon Creek upstream of Log Cabin Diversion Dam. Historical samples indicate that there was a hardhead fish population in the diversion pool as recent as 2001 (personal communication, Dan Teater, Forest Service). Cal Fish and Wildlife does not stock Oregon Creek. YCWA s Study 3.8 included one 89-m-long electrofishing site 0.4 mi upstream of Log Cabin Diversion Dam, which was comprised of low-gradient riffle, run, and pool. No fish passage impediments were observed. Approximately nine sq m of gravel suitable for spawning resident trout and eight pieces of LWM were observed in In 2013, three sq m of spawning gravel was observed and four pieces of LWM were documented. Species composition at the site was the same in 2012 and Sacramento sucker was numerically dominant, followed by rainbow trout and Sacramento pikeminnow over both years of the survey. Given the lack of statistical rigor in the 95 percent confidence interval for Sacramento sucker abundance in 2012 (17-239), the results of estimated metric calculations are statistically unreliable and are not discussed. Extrapolated density estimates of rainbow trout numbers was 72 fish/mi in 2012 and 263 fish/mi in Sacramento pikeminnow were estimated at 18 fish/mi in 2012, and 38 fish/mi in Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information collected by quantitative electrofishing for the Oregon Creek upstream of Log Cabin Diversion Dam Site (RM 4.5). Species Rainbow Trout Sacramento Pikeminnow Sacramento Sucker Abundance Fork length (mm) Biomass Year no. collected by pass (total) (4) (14) (1) (2) (17) (16) % of fish collected 18.2% 43.8% 4.5% 6.3% 77.3% 50.0% estimated section abundance % confidence interval Relative Stock Density NA 2 14 NA NA NA NA fish/100m fish/mi mean (range) (67-143) (54-158) (140) ( ) (30-115) (40-96) weight of fish collected (g) mean weight (g) (range) ( ) ( ) (27.5) ( ) ( ) estimated section biomass (g) g/100m lbs/ac kg/ha ( ) Exh. E - Environmental Report Application for New License April 2014 Page E ,

27 Table (continued) Species Rainbow Trout Sacramento Pikeminnow Sacramento Sucker Condition factor Age class frequency in fish/mile (% of total) 1 2 Year relative condition range NA NA NA (75.0%) 207 (78.6%) 0 (0.0%) 0 (0.0%) 865 (94.1%) 263 (87.5%) 1 18 (25.0%) 0 (0.0%) 18 (100.0%) 38 (100.0%) 54 (5.9%) 38 (12.5%) 2 and older 0 (0.0%) 56 (21.4%) 0 (0.0%) 0 (0.0%) 0 (0.0%) 0 (0.0%) Irregular depletion of Sacramento sucker in the second pass led to a poor 95 percent confidence interval and, therefore, results of estimated metrics are improbable. Not applicable because of small sample size. Fish sampling for YCWA s Study 3.11 was conducted in the fall of 2012 from the diversion dam upstream 1.7 mi. Electrofishing, seine netting, and hook-and-line sampling resulted in the capture of 437 rainbow trout, representing all lifestages. The only other fish species observed during the tagging effort was Sacramento sucker. Rainbow trout fry emergence was assessed upstream of Log Cabin Diversion Dam as a component of YCWA s Study 3.8. Results indicated that rainbow trout spawned from May 6 to May 19 in Emergence was calculated to have occurred from June 11 to 20, Middle Yuba River (Our House Diversion Dam Reach) There are few known studies of fish populations in the Middle Yuba River from downstream of Our House Diversion Dam to the confluence of Oregon Creek. Gast et al. (2005) reported snorkeling survey results at two sites, with observations of rainbow trout, Sacramento sucker, Sacramento pikeminnow, hardhead, and smallmouth bass. Rainbow trout fry were found incidentally near Oregon Creek (RM 4.8). Tributaries of the Middle Yuba River, including Oregon Creek, may provide cool-water habitat for rainbow trout in summer. Electrofishing was conducted in 2011 as a component of YCWA s Sediment Pass-Through Program (Stillwater Sciences 2011). Sampling occurred on the Middle Yuba River approximately 0.25 mi downstream of Our House Dam. One-hundred-threefish representing three species were captured; rainbow trout were the most abundant fish captured (n=82) followed by Sacramento sucker (n=14) and smallmouth bass (n=7). Rainbow trout density was approximately 1,905 fish/mi, biomass was estimated to be lbs/acre, and catchable trout (trout >152 mm) were estimated at 250 fish/mi. Rainbow trout were estimated to be between 0+ and 3+, with representatives observed in each intervening age class. The mean condition factor for captured rainbow trout was YCWA s Study 3.8 included sampling of two sites on the Middle Yuba River, Our House Diversion Dam Reach at RMs 12.5 and 5.0. Because of deep water (up to 3 m) at the RM 12.5 site, sampling was by quantitative snorkeling, whereas the RM 5.0 site was electrofished. Fish at both sites were in good condition. The RM 12.5 site was comprised of run, pocket-water, and pool habitats. LWM and fish passage impediments were absent at this site. Approximately six and 8.8 sq m of gravel suitable for resident trout were observed in 2012 and 2013, respectively. Rainbow trout made up 83.7 April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

28 percent of observed fish in 2012 and smallmouth bass made up 59.6 percent of the same in Rainbow trout abundance at the site over the 2 years of data collection stayed relatively similar with density estimates of 453 fish/mi in 2012, and 450 fish/mi in Density of smallmouth bass was estimated to be 88 fish/mi in 2012, and 708 fish/mi in In 2013, two additional species were documented that were not identified in 2012: Sacramento pikeminnow and Sacramento sucker. These additional species made up a relatively small portion of total observed fish with an estimated density of 11 fish/mi for both species. Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information from quantitative snorkeling observations for the Middle Yuba River Downstream of Our House Diversion Dam Site (RM 12.5). Abundance Fork length (51 mm size groups) Species Rainbow Smallmouth Sacramento Sacramento Trout Bass Pikeminnow Sucker Year no. counted by pass % of total fish counted 83.7% 38.4% 16.3% 59.6% 0.0% 1.0% 0.0% 1.0% estimated section abundance % confidence interval Relative Stock Density fish/100m fish/mi min max mean Condition relative condition factor 1 range NA Age class (0.8%) (0.0%) (8.3%) (21.4%) (0.0%) (0.0%) frequency in fish/mile (23.4%) (54.6%) (70.8%) (58.3%) (0.0%) (0.0%) (% of total) and older (75.8%) (45.4%) (20.8%) (20.3%) (100.0%) (100.0%) 1 Condition factor for snorkeled sites was calculated from fish captured by qualitative electrofishing at the site. In some instances, a species was observed by snorkeling, but not captured during electrofishing and therefore a condition factor was not calculated. 2 Not applicable because of small sample size. The site upstream of the Oregon Creek confluence, at RM 5.0, was comprised of pocket-water and pools. Approximately 3.6 sq m of gravel suitable for spawning resident trout was observed in 2012, whereas none were documented in No impediments to fish passage or LWM were documented in either 2012 or Results of quantitative electrofishing are summarized in Table Smallmouth bass made up the majority of the catch in both 2012 and 2013, most of which were age-0 fish (over 80.0% in both years). Smallmouth bass extrapolated density was estimated to be 1,915 fish/mi in 2012, and 1,282 fish/mi in Rainbow trout and Sacramento sucker were also present but only made up 7.9 and 7.1 percent of the total fish captured in 2012, and 8.2 and 4.1 percent of the total captured in 2013, respectively. Rainbow trout density was estimated to be 155 fish/mi in 2012 and 90 fish/mi in Several sampled fish were found to be carrying an unidentified species of parasitic anchor worm downstream of Our House Dam. Aside from small lesions at the point of attachment, these fish were vigorous Exh. E - Environmental Report Application for New License April 2014 Page E ,

29 and healthy in appearance. In 2013, special attention was given to examining fish for indication of these parasites as well as other disease or signs of pathology. Two Sacramento sucker carrying the unidentified anchor worm were captured at RM 5.0. Several rainbow trout were also described as having the small lesions associated with these anchor worms at RM However, despite these few noted parasites, fish collected during electrofishing for Study 3.8 and Study 3.11 were vigorous, free of parasites, and in good condition. Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information collected by quantitative electrofishing for the Middle Yuba River site at RM 5.0. Species Rainbow Trout Sacramento Sucker Smallmouth Bass Abundance Fork length (mm) Biomass Condition factor Age class frequency in fish/mile (% of total) Year no. collected by pass (total) (11) (6) (10) (3) (119) (64) % of fish collected 7.9% 8.2% 7.1% 4.1% 85.0% 87.7% estimated section abundance % confidence interval Relative Stock Density fish/100m fish/mi ,915 1,282 mean (range) ( ) ( ) (49-294) ( ) (42-181) (55-195) weight of fish collected (g) mean weight (g) (range) ( ) ( ) ( ) ( ) ( ) ( ) estimated section biomass (g) , ,219.8 g/100m , ,143.0 lbs/ac kg/ha relative condition range (0.0%) 0 (0.0%) 42 (30.0%) 0 (0.0%) 1,577 (82.4%) 1,102 (86.0%) 1 14 (9.1%) 15 (16.7%) 28 (20.0%) 15 (33.3%) 322 (16.8%) 140 (10.9%) 2 and older 141 (90.9%) 75 (83.3%) 70 (50.0%) 30 (66.7%) 16 (0.8%) 40 (3.1%) Oregon Creek (Log Cabin Diversion Dam Reach) YCWA is unaware of existing historical information regarding fish populations in Oregon Creek downstream of Log Cabin Diversion Dam. Cal Fish and Wildlife does not stock Oregon Creek. YCWA s Study 3.8 included sampling of fish populations at one site on Oregon Creek located 4.0 mi downstream of Log Cabin Diversion Dam at RM 0.3. The site was comprised of step-run and pool habitat in roughly even proportions. Approximately 1.2 sq m of gravel suitable for spawning resident trout was observed in 2012, whereas none was documented in Likewise, one unit of LWM was observed in 2012 that was not observed again in Fish sampling was conducted by three-pass depletion electrofishing, with results summarized in Table Rainbow trout were numerically dominant in 2012 (92.0%) and 2013 (80.3%), followed by Sacramento sucker (7.0 in 2012 and 17.1% in 2013), and smallmouth bass (one fish April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

30 in 2012, two in 2013). The estimated rainbow trout density in 2012 was 2,266 fish/mi and the age class distribution of rainbow trout indicated population recruitment (many aged-0 fish). In 2013, the estimated rainbow trout density was lower at 1430 fish/ mi with a similar preponderance of aged-0 fish. Several sampled fish were found to be carrying an unidentified species of parasitic anchor worm. A single Sacramento sucker was captured during sampling at RM 0.3 which was found to be carrying a single anchor worm. This was one of three fish observed with this parasite during The host fish appeared generally unharmed by the parasite. Results of the two years of sampling are summarized in Table Table Summary results of 2012 and 2013 fish population information collected by quantitative electrofishing for the Oregon Creek downstream of Log Cabin Diversion Dam Site (RM 0.3). Species Rainbow Trout Sacramento Sucker Smallmouth Bass Abundance Fork length (mm) Biomass Year no. collected by pass (total) (92) (61) (7) (13) (1) (2) % of fish collected 92.0% 80.3% 7.0% 17.1% 1.0% 2.6% estimated section abundance % confidence interval Relative Stock Density 3 7 NA NA fish/100m fish/mi 2,266 1, mean (range) (56-171) (49-168) (79-132) (78-158) (75-95) weight of fish collected (g) 1, mean weight (g) (range) 11.8 ( ) 12.4 ( ) 20.5 ( ) 19.1 ( ) 69.2 (69.2) estimated section biomass (g) 1, g/100m 1, , lbs/ac kg/ha ( ) Condition relative condition factor range NA NA Age class 0 1,355 (59.8%) 820 (57.4%) 0 (0.0%) 75 (30.8%) 0 (0.0%) 22 (50.0%) frequency in (31.5%) 446 (31.1%) 169 (100.0%) 150 (61.5%) 24 (100.0%) 22 (50.0%) fish/mile (% of total) 2 and older 197 (8.7%) 164 (11.5%) 0 (0.0%) 19 (7.7%) 0 (0%) 0 (0.0%) Not applicable because of small sample size. 1 Middle Yuba River (Oregon Creek Reach) Gast et al. (2005) reported snorkeling survey results at four sites on the Middle Yuba River between Oregon Creek and the confluence with the North Yuba River. Rainbow trout, Sacramento sucker, Sacramento pikeminnow, and smallmouth bass were documented. The same report identified natural, low flow-only barriers to small fish passage at RM 0.2 and 3.2, and an estimated 13-foot-high cascade at RM 0.4 that would be a major obstacle to upstream migration. At this location, several very large boulders blocking the narrow bedrock channel created the barrier, and sediment has filled in upstream of the boulders forming a dam. Although large fish may be able to pass at certain flows, the height of the cascade and narrowness of the canyon is expected to at least impede passage at all flows. Exh. E - Environmental Report Application for New License April 2014 Page E ,

31 YCWA s Study 3.8 included two sites downstream of the confluence with Oregon Creek on the Middle Yuba River at RM 3.3 (downstream of Moonshine Creek) and at RM 1.0 (downstream of Yellowjacket Creek). The RM 3.3 site, comprised of run and pool habitat, was sampled by quantitative snorkeling because of overall deep water up to 3.6 m. The site was devoid of LWM and fish passage impediments. Approximately 61 sq m of suitable spawning gravel for resident trout was observed in 2012, but was not documented in The RM 1.0 site was partially sampled by snorkeling a deep pool and the rest of the site which included high-gradient riffle and glide habitats, was electrofished. LWM and fish passage impediments were absent. Suitable spawning gravel for resident trout was not observed in 2012; however, 61 sq m of gravel was documented in At RM 3.3, rainbow trout was numerically dominant in both years of sampling (73.5 and 55.7% of total count in 2012 and 2013, respectively), followed by smallmouth bass (15.3 and 34.3%) and Sacramento sucker (11.2 and 10.0%). The extrapolated density estimate of rainbow trout in 2012 was 613 fish/mi in 2012 and 350 fish/mi in Density estimates of smallmouth bass at the site were 126 fish/mi in 2012 and 212 fish/mi in Estimated density of Sacramento sucker was 91 and 65 fish/mi in 2012 and 2013, respectively. Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information from quantitative snorkeling observations for the Middle Yuba River downstream of Moonshine Creek Site (RM 3.3). Species Rainbow Trout Sacramento Sucker Smallmouth Bass Year no. counted by pass % of total fish counted 73.5% 55.7% 11.2% 10.0% 15.3% 34.3% estimated section abundance Abundance 95% confidence interval Relative Stock Density fish/100m fish/mi Fork length (51 min mm size max groups) mean Condition condition factor Factor 2 range NA Age class 0 86 (14.0%) 6 (1.7%) 9 (9.4%) 0 (0.0%) 80 (63.6%) 38 (18.1%) frequency in (54.9%) 41 (11.9%) 77 (84.4%) 30 (45.5%) 40 (31.8%) 74 (34.7%) fish/mile (% of total) 2 and older 191 (31.2%) 303 (86.4%) 6 (6.3%) 35 (54.5%) 6 (4.5%) 100 (47.2%) 1 The lower range of the 95 percent confidence interval was less than the lowest pass and as a result, the lowest pass was used. 2 Condition factor for snorkeled sites was calculated from fish captured by qualitative electrofishing at the site. In some instances, a species was observed by snorkeling, but not captured during electrofishing and therefore a condition factor was not calculated. 3 Not applicable because of small sample size. At the RM 1.0 site, smallmouth bass were the most numerous fish captured in both years (50.0and 97.3% of total count in 2012 and 2013, respectively). Extrapolated density estimates of smallmouth bass were 520 fish/mi in 2012, and 1,345 fish/mi in The estimated density of rainbow trout was 470 fish/mi in 2012, and 38 fish/mi in Sacramento pikeminnow were April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

32 observed in 2012 (40 fish/mi), but were absent in Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information from quantitative snorkeling observations for the Middle Yuba River Downstream of Yellowjacket Creek Site (RM 1.0). Species Rainbow Trout Sacramento Pikeminnow Smallmouth Bass Abundance Fork length (51 mm size groups) Age class frequency in fish/mile (% of total) 1 2 Year no. counted by pass % of total fish counted 46.2% 2.7% 3.8% 0.0% 50.0% 97.3% estimated section abundance % confidence interval Relative Stock Density 1 30 NA 3 NA fish/100m fish/mi ,345 min max mean (19.1%) 0 (0.0%) 0 (0.0%) (58.2%) 918 (68.2%) (36.2%) 38 (100.0%) 40 (100.0%) (35.8%) 339 (25.2%) 2 and older 210 (44.7%) 0 (0.0%) 0 (0.0%) (16.0%) 88 (6.6%) Relative stock density was calculated for the entire site (snorkeling and electrofishing combined). The lower range of the 95 percent confidence interval was less than the lowest pass and, as a result, the lowest pass was used. 3 Not applicable because of small sample size. Electrofishing results for the rest of the site at RM 1.0 are summarized in Table Smallmouth bass were numerically dominant in both years; however, almost all were age-0. Population numbers were 1,922 fish/mi and 2,297 fish/mi in 2012 and 2013, respectively. Rainbow trout were captured in 2012 (633 fish/mi), but were absent in Sacramento sucker were not previously documented at the site in 2012, but two were captured in Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information collected by quantitative electrofishing for the Middle Yuba River Downstream of Yellowjacket Creek Site (RM 1.0). Species Rainbow Trout Sacramento Sucker Smallmouth Bass Abundance Fork length (mm) Year no. collected by pass (total) (19) (0) (0) (2) (61) (109) % of fish collected 23.8% 0.0% 0.0% 1.8% 76.2% 98.2% estimated section abundance % confidence interval Relative Stock Density NA fish/100m fish/mi ,922 2,297 mean (range) (68-225) (76-105) (62-185) (57-179) Exh. E - Environmental Report Application for New License April 2014 Page E ,

33 Table (continued) Species Rainbow Trout Sacramento Sucker Smallmouth Bass Biomass Condition factor Age class frequency in fish/mile (% of total) 1 2 Year weight of fish collected (g) , mean weight (g) (range) ( ) ( ) ( ) ( ) estimated section biomass (g) , g/100m 1, , ,459.8 lbs/ac kg/ha relative condition (range) (52.6%) (50.0%) 1,796 (93.4%) 3,704 (97.2%) (26.3%) (50.0%) 63 (3.3%) 35 (0.9%) 2 and older 133 (21.1%) (0.0%) 63 (3.3%) 70 (1.9%) Relative stock density was calculated for the entire site (snorkeling and electrofishing combined). Not applicable because of small sample size. North Yuba River (New Bullards Bar Dam Reach) YCWA is unaware of any prior study of fish populations in the North Yuba River downstream of New Bullards Bar Reservoir. YCWA s Study 3.8 included sampling of one site at RM 0.2, which was comprised of pocketwater and pools, with a maximum depth of 8 ft. Due to the deeper depths at this site, quantitative snorkeling was employed rather than electrofishing. The site was devoid of both suitable spawning gravel for resident trout, and LWM. A single fish passage impediment was observed at the bottom of the site. In 2012, Sacramento sucker was the numerically dominant fish observed (85% with an estimated density of 3,203 fish/mile), followed by rainbow trout (15% with an estimated density of 543 fish/mi). In 2013 sampling, rainbow trout made up the majority of fish observed (74.6% with an estimated density of 534 fish/mi), whereas Sacramento sucker was estimated at 181 fish/mi (25.4% of the total count). One Sacramento pikeminnow was observed at the site in 2012 and none were observed in All of the Sacramento suckers observed in 2012 were age-0 fish. Rainbow trout were predominantly age-0 fish, with low numbers of older fish. Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information from quantitative snorkeling observations for the North Yuba River Upstream of Middle Yuba River Site (RM 0.2). Species Rainbow Trout Sacramento Sucker Sacramento Pikeminnow Abundance Year no. counted by pass % of total fish counted 15.0% 74.6% 84.6% 25.4% 0.4% 0.0% estimated section abundance % confidence interval April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

34 Table (continued) Species Rainbow Trout Sacramento Sucker Sacramento Pikeminnow Year Relative Stock Abundance Density 2 3 NA 3 NA (cont.) fish/100m fish/mi , Fork length (51 min mm size max groups) mean Condition condition factor factor 2 range NA -- Age class (95.8%) 460 (86.3%) 3,203 (100.0%) 172 (95.2%) 0 (0.0%) -- frequency in 1 14 (2.5%) 56 (10.5%) 0 (0.0%) 9 (4.8%) 0 (0.0%) -- fish/mile (% of total) 2 and older 9 (1.7%) 17 (3.2%) 0 (0.0%) 0 (0.0%) 14 (100.0%) -- The lower range of the 95% confidence interval was less than the lowest pass and as a result, the lowest pass was used. Condition factor for snorkeled sites was calculated from fish captured by qualitative electrofishing at the site. In some instances, a species was observed by snorkeling, but not captured during electrofishing and therefore a condition factor was not calculated. Not applicable because of small sample size Yuba River (North Yuba River/Middle Yuba River Reach) YCWA is unaware of any prior study of fish populations in the Yuba River downstream of the North Yuba and Middle Yuba rivers confluence. YCWA s Study 3.8 included sampling fish populations at two sites on the Yuba River upstream of New Colgate Powerhouse: at RM 39.6, below the confluence of Middle Yuba and North Yuba rivers; and at RM 35.0, upstream of New Colgate Powerhouse. The predominance of deep habitats at these sites required sampling by quantitative snorkeling rather than electrofishing. The site at RM 39.6 was comprised mostly of pool habitats up to 4.9 m deep, with smaller areas of glide habitat. The site was devoid of suitable spawning gravel for resident trout, LWM, and fish passage impediments. In 2012, rainbow trout made up 61.2 percent of observed fish assemblage followed by smallmouth bass (38.1%), and Sacramento pikeminnow (0.7%). In addition, two Sacramento suckers were collected during qualitative electrofishing at the stream margins. In 2013, smallmouth bass (78.5% of the total) and rainbow trout (21.5%) were the only species found. Extrapolated density estimates for rainbow trout were 543 fish/mi in 2012, and 243 fish/mi in The same metric for smallmouth bass was 337 fish/mi in 2012, and 889 fish/mi in Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information from quantitative snorkeling observations for the Yuba River Downstream of Middle Yuba River Site (RM 39.6) Species Rainbow Trout Sacramento Pikeminnow Smallmouth Bass Abundance Year no. counted by pass % of total fish counted 61.2% 21.5% 0.7% 0.0% 38.1% 78.5% estimated section abundance % confidence interval Relative Stock Density NA Exh. E - Environmental Report Application for New License April 2014 Page E ,

35 Table (continued) Species Rainbow Trout Sacramento Pikeminnow Smallmouth Bass Year Abundance fish/100m (cont.) fish/mi Fork length (51 min mm size max groups) mean Condition condition factor factor 1 range NA NA NA Age class 0 58 (10.7%) 4 (1.8%) 0 (0.0%) (62.9%) 184 (20.7%) frequency in (36.7%) 55 (22.8%) 13 (100.0%) (35.2%) 320 (36.0%) fish/mile (% of total) 2 and older 286 (52.7%) 184 (75.4%) 0 (0.0%) -- 6 (1.9%) 384 (43.3% Condition factor for snorkeled sites was calculated from fish captured by qualitative electrofishing at the site. In some instances, a species was observed by snorkeling, but not captured during electrofishing and therefore a condition factor was not calculated. Not applicable because of small sample size. 1 2 The site at RM 35.0 was comprised of pocket-water and pools, with a maximum depth of 2.1 m7 ft. Approximately 3 sq m of suitable resident trout spawning gravel was identified in the site in 2012, and slightly more in 2013 (15.2 sq m). In both years, the site was devoid of LWM and fish passage impediments. Smallmouth bass made up 93.2 percent of fish observed, which resulted in an estimated density of 1,409 fish/mi in In 2013, smallmouth bass were also numerically dominant (98.7% of observed fish and 1,257 fish/mi). In both years, rainbow trout comprised the remainder of the sample with 108 fish/mi (6.8% of total) and 16 fish/mi (1.3%) in 2012 and 2013, respectively. Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information from quantitative snorkeling observations for the Yuba River Upstream of New Colgate Powerhouse Site (RM 35.0). Species Rainbow Trout Smallmouth Bass Year no. counted by pass % of total fish counted 6.8% 1.3% 93.2% 98.7% estimated section abundance Abundance 95% confidence interval Relative Stock Density fish/100m fish/mi ,409 1,257 min Fork length (51 max mm size groups) mean Condition factor 1 condition factor range NA 2 NA Age class (67.9%) 563 (44.8%) frequency in 1 15 (13.6%) (23.0%) 645 (51.3%) fish/mile (% of total) 2 and older 93 (86.4%) 16 (100.0%) 128 (9.1%) 49 (3.9%) 1 Condition factor for snorkeled sites was calculated from fish captured by qualitative electrofishing at the site. In some instances, a species was observed by snorkeling, but not captured during electrofishing and therefore a condition factor was not calculated. 2 Not applicable because of small sample size. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

36 Yuba River (New Colgate Powerhouse Reach) YCWA is unaware of any prior study of fish populations in the Yuba River downstream of New Colgate Powerhouse. YCWA s Study 3.8 included sampling of fish populations at one site on the Yuba River (RM 33.7) between New Colgate Powerhouse and Englebright Reservoir. Deep habitats required sampling by quantitative snorkeling. The site was comprised of low gradient riffle, high gradient riffle, run, step, and pools, with a maximum depth of 1.8 m. Approximately 25.2 sq m of suitable spawning gravel for resident trout was identified in the site in 2012, whereas a greater amount (68.6 sq m) was documented in No LWM or fish passage impediments were documented in either year. Except for one large brown trout, only rainbow trout were observed in The extrapolated density estimate for rainbow trout in 2012 was 323 fish/mi. Rainbow trout were numerically dominant again in 2013, and estimated density was 560 fish/mi. Brown trout were not documented at the site in 2013; however, a single Sacramento sucker was observed. Results of the two years of sampling are summarized in Table Table Summary of 2012 and 2013 fish population information from quantitative snorkeling observations for the Yuba River Downstream of New Colgate Powerhouse Site (RM 33.7) 1 Species Rainbow Trout Brown Trout Sacramento Sucker Year no. counted by pass % of total fish counted 97.7% 98.5% 2.3% 0% 0% 1.5% estimated section Abundance abundance¹ % confidence interval fish/100m fish/mi Fork length (51 min mm size Max groups) Mean Condition condition factor factor 2 range NA 3 NA NA NA Age class 0 0 (0.0%) 83 (14.8%) 0 (0.0%) (0.0%) frequency in 1 3 (1.0%) 140 (25.0%) 0 (0.0%) (100.0%) fish/mile (% of total) 2 and older 320 (99.0%) 337 (60.2%) 8 (100.0%) (0.0%) In 2012, four passes were completed at this site, but the first pass was an outlier and was omitted to better refine statistical confidence. No species were excluded as a result of omitting the first pass. Condition factor for snorkeled sites was calculated from fish captured by qualitative electrofishing at the site. In some instances, a species was observed by snorkeling, but not captured during electrofishing and therefore a condition factor was not calculated. Not applicable because of small sample size In addition to survey results, several carcasses of adult kokanee were incidentally observed in 2012 below New Colgate Powerhouse proximal to the stream fish population site during the New Colgate Ramping Study (Study 3.12). These fish had presumably migrated upstream from Englebright Reservoir, where kokanee are stocked. Exh. E - Environmental Report Application for New License April 2014 Page E ,

37 Downstream of Englebright Dam Study 3.9 (YCWA 2013a), Study 7.8 and Study 7.9 each used results of previous and ongoing studies to describe the various fish populations that occur downstream of Englebright Dam. The description includes whether the fish species was native or introduced, resident or anadromous, and included temporal and spatial distribution within the lower Yuba River (Table ). YCWA found reliable, documented occurrences of 41 fish species and anecdotal unverified reports of three species, for a total of 44 fish species. 14 Twenty-one species (48% of the total fish species), nine of which are anadromous, are native to California. Twenty-three species (52% of the total fish species), two of which are anadromous, were introduced to California waters. None of the fish species documented in the area are catadromous, and none are reported as endemic to the Yuba River basin. Relative abundance, temporal and spatial distribution, and habitat utilization of the reported fish species were derived primarily from two studies conducted between 1986 and 2001 (Beak 1991, Kozlowski 2001), and several ongoing studies that are being conducted by the RMT (RMT 2013). Spatial distribution was characterized by stream reach to be consistent with the distribution as reported in the source documents (e.g., CDFG 1991 in TM 3.9). The reach designations within the source documents were intended to represent longitudinal variations in channel morphology, temperature and flow. The four reach designations, as shown in Figure , are: Narrows Reach. Extends from Englebright Dam at RM 24.3 to the downstream side of the Narrows 1 and Narrows 2 powerhouses at RM 24 Garcia Gravel Pit Reach. Begins downstream of the Narrows Reach at RM 22 and extending to the Daguerre Point Dam at approximately RM 11.6 Daguerre Point Dam Reach. Extends to the downstream terminus of the Yuba Goldfield at approximately RM 3.5 Simpson Lane Reach. Approximately RM 3.5 to the confluence with the Feather River at RM 0 in the town of Marysville (Beak 1989). Table shows the fish species distribution in the four reaches. Table Fish species distribution in the Yuba River downstream of Englebright Dam. Common Name California roach Hardhead Hitch Prickly sculpin Riffle sculpin Sacramento blackfish Sacramento pikeminnow Scientific Name Narrows NATIVE RESIDENT SPECIES Hesperoleucus symmetricus Mylopharodon conocephalus Lavinia exilicauda Cottus asper Cottus gulosus Orthodon microlepidotus Ptychocheilus grandis Garcia Gravel Pit Reach 1 Daguerre Point Dam Simpson Lane 14 In Technical Memorandum 3.9, Non-ESA Listed Fish Downstream of Englebright Dam, fish populations identified under an ESU or DPS are considered separate species. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

38 Table (continued) Common Name Sacramento splittail Sacramento sucker Speckled dace Rainbow trout Tule perch Fall-run Chinook salmon Spring-run Chinook salmon ESU Chum salmon Pink salmon Steelhead trout Pacific lamprey River lamprey Green sturgeon White sturgeon Black bullhead Black crappie Bluegill Brown bullhead Brown trout Carp Channel catfish Fathead minnow Golden shiner Green sunfish Inland silverside Largemouth bass Redear Sunfish Smallmouth bass Threadfin shad Wagasaki Warmouth White catfish White crappie Bigscale logperch Mosquitofish American shad Striped bass 1 Legend: Based on direct observation Based only on VAKI Riverwatcher data Based only on rotory screw trap (RST) data Scientific Name Garcia Narrows Gravel Pit NATIVE RESIDENT SPECIES (continued) Pogonichthys macrolepidotus Catostomus occidentalis Rhinichthys osculus Oncorhynchus mykiss Hysterocarpus traskii NATIVE ANADROMOUS SPECIES Oncorhynchus tshawytscha Oncorhynchus tshawytscha Oncorhynchus keta Oncorhynchus gorbuscha Oncorhynchus mykiss Entosphenus tridentatus Lampetra ayresii Acipenser medirostris Acipenser transmontanus INTRODUCED RESIDENT SPECIES Ameiurus melas Pomoxis nigromaculatus Lepomis macrochirus Ameiurus nebulosus Salmo trutta Cyprinus carpio Ictalurus punctatus Pimephales promelas Notemigonus crysoleucas Lepomis cyanellus Menidia beryllina Micropterus salmoides Lepomis microlophus Micropterus dolomieu Dorosoma petenense Hypomesus nipponensis Lepomis gulosus Ameiurus catus Pomoxis annularus Percina macrolepida Gambusia affinis INTRODUCED ANADROMOUS SPECIES Alosa sapidissima Morone saxatilis Reach 1 Daguerre Point Dam Simpson Lane YCWA also compared the results of this study with summaries of similar information reported for the lower Feather River, the lower American River, and the lower Tuolumne River. Species composition in the Yuba River downstream of Englebright Dam compared with that reported for these other Central Valley tributaries indicates that the fish fauna in the Yuba River downstream of Englebright Dam is as diverse as in the other Central Valley streams and Exh. E - Environmental Report Application for New License April 2014 Page E ,

39 includes several fish species that, in the recent past, have only been reported in the Yuba River downstream of Englebright Dam (e.g., chum salmon, pink salmon). Additionally, the Yuba River downstream of Englebright Dam includes fish assemblages not found in the lower reaches of these other Central Valley streams (e.g., rainbow trout assemblage). The Yuba River downstream of Englebright Dam serves as a transition zone that provides habitat suitable for both cold- and warm-water fish species. Fish species and life stage distribution are influenced by variations in environmental conditions and by the habitat requirements, life history, daily and seasonal movements, and behavior of each species. The distribution of common native fishes in the river reflects the historical distribution of common native fishes in the larger Central Valley drainages. Central Valley streams have headwaters in mountain areas and flow through steep canyons and deep pools in the foothills before flowing into slow-moving rivers on the valley floor. The habitats found in reaches flowing through mountains, foothills, and valley floors contain distinct assemblages of fish that have wide or narrow zones of overlap, depending on the gradient of the stream and other environmental conditions, such as temperature and flow regimes. The overlap among regions with distinct assemblages, often called zones, is fairly broad. Four assemblages can usually be recognized in Central Valley streams: the rainbow trout assemblage, the pikeminnow-hardhead-sucker assemblage, the California roach assemblage, and the deep-bodied fish assemblage (Moyle 2002). Fish Species Composition 15 The Yuba River downstream of Englebright Dam contains all four fish assemblages typically associated with west slope streams of the Sierra Nevada, as described above. The Yuba River downstream of Englebright Dam is primarily occupied by the pikeminnow-hardhead-sucker and California Roach assemblages, bounded by the rainbow trout assemblage in the uppermost reach and the deep-bodied assemblage in the lowermost reach. Table lists the native species occurring in the Yuba River downstream of Englebright Dam and the associated fish assemblage. Table Native fish species and associated assemblages of the Yuba River watershed downstream of Englebright Dam. Common and Scientific Name Assemblage Habitat SUCKERS (CATASTOMIDAE) Sacramento sucker (Catostomus occidentalis) Pikeminnow-hardhead-sucker Lowlands, foothills SCULPINS (COTTIDAE) Riffle sculpin (Cottus gulosus) Rainbow trout High elevation, lowlands, foothills Prickly sculpin (Cottus asper) Pikeminnow-hardhead-sucker Lowlands, foothills MINNOWS (CYPRINIDAE) Hitch (Lavinia exilicauda) Deep-bodied fishes Lowlands, foothills Sacramento roach (L. symmetricus) California roach Foothills Sacramento hardhead (Mylopharodon conocephalus) Pikeminnow-hardhead-sucker Lowlands, foothills Sacramento pikeminnow (Ptychocheilus grandis) Pikeminnow-hardhead-sucker Lowlands, foothills Sacramento speckled dace (Rhinichthys osculus ssp) Rainbow trout High elevation, lowlands, foothills 15 Additional information on the fish species collected during the VAKI Riverwatcher surveys, the RST surveys, including size composition (including for lamprey) are reported Technical Memorandum 3-9, Non-ESA-Listed Fish Populations Downstream of Englebright Dam, in Appendix E6 of Exhibit E. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

40 Table (continued) Common and Scientific Name Assemblage Habitat MINNOWS (CYPRINIDAE) (continued) Sacramento black fish (Orthodon microlepidotus ) Deep-bodied fishes Lowlands Sacramento splittail (Pogonichthys macrolepidotus) Deep-bodied fishes Lowlands SURFPERCHES (EMBIOTOCIDAE) Tule perch (Hysterocarpus traskii) Deep-bodied fishes Lowlands, foothills STICKLEBACK (GASTEROSTIEDAE) Three-spined stickleback (Gasterosteus aculeatus) Pikeminnow-hardhead-sucker Lowland, foothills LAMPREYS (PETROMYZONTIDE) Pacific lamprey (Entosphenus tridentata) Anadromous Anadromous, foothills, lowlands River lamprey (Lampetra ayersi) Anadromous Anadromous, coastal streams, lowlands TROUTS AND SALMON (SALMONIDAE) Central Valley steelhead (Oncorhynchus mykiss) Anadromous Anadromous, lowlands, foothills Central Valley Chinook salmon (spring-run) (O. tshawytscha) Anadromous Anadromous, high elevation, foothills, lowlands Central Valley Chinook salmon (fall-run) (O. tshawytscha) Anadromous Anadromous, foothills, lowlands Rainbow trout (O. mykiss) Rainbow trout Resident, foothills, high elevation The greatest diversity of fish species observed during fish surveys conducted on the lower Yuba River was associated with the downstream migration surveys conducted with RSTs near Hallwood Boulevard ( ) (YCWA 2012a). The RST samples included a combined 34 species (Table ). Electrofishing and snorkel surveys conducted by Beak (1989) and Kozlowski (2004) identified 15 and 16 species, respectively (Table ). Migration monitoring at Daguerre Point Dam using VAKI Riverwatcher TM identified 13 species (Table ). Observation of fish behavior near the Narrows 2 Powerhouse included six species (YCWA 2012b) (Table ). Overall, 45 different fish species were observed during the execution of these studies. Both the native and introduced groups of fish included anadromous and resident species (Table ). Six native anadromous species and two introduced anadromous species were observed. Numerically, nearly all of anadromous fish observed in all surveys were native, mostly Chinook salmon and steelhead juveniles observed during the snorkeling, electrofishing and downstream trapping (RST) surveys. Few juvenile introduced anadromous fish were observed during the reported surveys. Most of the observed introduced anadromous fish were adults, documented during the VAKI Riverwatcher TM migration survey. Similarly, there were 11 native resident fish species and 21 introduced resident fish species observed during the reported surveys. However, the majority (numerical abundance) of fish observed during the snorkeling, electrofishing and RST surveys were native juveniles. Several introduced species were rare, only observed a few times and usually in the RST surveys. These species included wakasagi (Hypomesus nipponensis), golden shiner (Notemigonus crysoleucas), fathead minnow (Pimephales promelas), brown trout, and crappie. These species are typical of introduced resident fish stocked in the upstream reservoirs, or typical bait fish that have likely been introduced by anglers into the upstream reservoirs. Exh. E - Environmental Report Application for New License April 2014 Page E ,

41 Species Diversity Species diversity can be characterized in a variety of ways including total number of species by origin (i.e., native or introduced), assemblages present and completeness of representative species in the assemblage, relative abundance of species, anadromous versus resident, and seasonal versus perennial. Results of each of the studies consistently show that although the total number of introduced species was greater than the number of native species, the native species were more abundant than introduced species. When the number of native anadromous fish peaked, primarily juvenile Chinook salmon between February and March, native species comprised over 90 percent of the number of fish observed among the referenced studies. The non-anadromous population, however, appears to contain a more balanced proportion of introduced and native fishes. The combined results of the RST surveys for 2007 through 2009 (Figure ) indicate that the most abundant species was threadfin shad (Dorosoma petenense), an introduced species, followed by sculpin (Cottus spp.), pikeminnow, largemouth bass, and Sacramento sucker. Figure Non-anadromous species composition collected by RSTs in the Yuba River downstream of Englebright Dam during the and RMT surveys. (Asterisk indicates introduced species). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

42 Another measure of diversity can be made through comparison of the fish assemblage composition that presently occurs in the river against the expected composition (e.g., based on historical assemblage and species compositions in similar streams). Comparison with the expected, historical composition, as described by Moyle (2002), indicates that the composition of the rainbow trout assemblage and pikeminnow, hardhead, sucker composition is complete (Table ). However, the deep-bodied fish assemblage is lacking one delegate species (splittail). The absence of splittail in observations made during the referenced studies could mean that they no longer occur in the Yuba River Downstream of Englebright Dam or that they were not observed due to the sampling techniques utilized. Table Fish species composition related to fish assemblages in the Yuba River downstream of Englebright Dam. Fish Species Fish Assemblage 1 Common Name Scientific Name California roach Hesperoleucus symmetricus Hardhead Mylopharodon conocephalus Hitch Lavinia exilicauda Prickly sculpin Cottus asper Riffle sculpin Cottus gulosus Sacramento blackfish Orthodon microlepidotus Sacramento pikeminnow Ptychocheilus grandis Sacramento splittail Pogonichthys macrolepidotus Sacramento sucker Catostomus occidentalis Speckled dace Rhinichthys osculus Rainbow trout Oncorhynchus mykiss Tule perch Hysterocarpus traskii River lamprey Lampetra ayresii Chinook salmon Oncorhynchus tshawytscha Green sturgeon Acipenser medirostris Pacific lamprey Entosphenus tridentatus Steelhead Oncorhynchus mykiss White sturgeon Acipenser transmontanus 1 Legend: Expected and observed Expected but not observed Deep-bodied Pikeminnow- Hardhead- Sucker California Roach Rainbow Trout Anadromous The native anadromous fish population observed during the reference studies suggest that both green and white sturgeon (Acipenser transmontanus) are absent. A few green sturgeon adults were reportedly observed just downstream of Daguerre Point Dam during 2011 (Cramer Fish Sciences 2011), but have not been observed in subsequent surveys in 2012 or Exh. E - Environmental Report Application for New License April 2014 Page E ,

43 Relative Abundance The surveys reported by Beak (1989) and Kozlowski (2004) provided information on relative abundance of fish species associated with specific locations and conditions. In contrast, the RST and VAKI Riverwatcher TM surveys provided information on relative abundance of fish moving through the survey site. If the results of the surveys reported by Beak and Kozlowski are used to infer standing crop (i.e., number per unit length or area of stream), the overall relative abundance of surveyed units (e.g., reach) can be described in the Yuba River downstream of Englebright Dam. Numerous assumptions, such as equal susceptibility of all species and lifestages to the survey methods, representativeness of survey sites, and other factors that are necessary to characterize the adequacy of the measure of relative abundance, are not likely to be met. However, these data can be considered useful measures of the relative magnitude of fish species present in the study reach. The results of electrofishing and snorkeling reported by Beak (1989) and Kozlowski (2004) show that relative abundance is temporally and spatially influenced (Figures through ). Chinook salmon dominate all four reaches during the winter-spring period. However, during the summer, after most of the Chinook salmon juveniles have left the river, relative fish species abundance varies with reach. Steelhead juveniles and Sacramento sucker dominate the uppermost reaches, while Sacramento pikeminnow and speckled dace abundance are higher in the lower reaches. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

44 Figure Simpson Lane Reach-specific species relative abundance observed by electrofishing and snorkeling based on the combined study results of Beak (1989) and Kozlowski (2004). Exh. E - Environmental Report Application for New License April 2014 Page E ,

45 Figure Daguerre Point Dam Reach-specific species relative abundance observed by electrofishing and snorkeling based on the combined study results of Beak (1989) and Kozlowski (2004). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

46 Figure Garcia Gravel Pit Reach-specific species relative abundance observed by electrofishing and snorkeling based on the combined study results of Beak (1989) and Kozlowski (2004). Exh. E - Environmental Report Application for New License April 2014 Page E ,

47 Figure Narrows Reach-specific species relative abundance observed by electrofishing and snorkeling based on the combined study results of Beak (1989) and Kozlowski (2004). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

48 Results of RST surveys also show that juvenile Chinook salmon is clearly the most abundant species-lifestage moving through the lower river (i.e., greater than 98% cumulative catch for ) (Table ). VAKI Riverwatcher results show adult Chinook salmon to be the most abundant species-lifestage migrating past Daguerre Point Dam (Table ). Table Relative abundance in descending order for fish collected from 1999 through 2009 by RST surveys in the Yuba River near Hallwood Boulevard (RM 7.2). Common Name Scientific Name Total Catch Percent of Catch Chinook salmon Oncorhynchus tshawytscha 2,413, % Steelhead trout Oncorhynchus mykiss 6, % Sacramento sucker Catostomus occidentalis 6, % Pacific lamprey Entosphenus tridentatus 4, % Sacramento pikeminnow Ptychocheilus grandis 3, % Riffle sculpin Cottus gulosus 2, % Golden shiner 1 Notemigonus crysoleucas 2, % Largemouth bass 1 Micropterus salmoides 1, % Threadfin shad 1 Dorosoma petenense 1, % Prickly sculpin Cottus asper 1, % Speckled dace Rhinichthys osculus 1, % Brown bullhead 1 Ameiurus nebulosus % Bluegill 1 Lepomis macrochirus % Hardhead Mylopharodon conocephalus % Redear sunfish 1 Lepomis microlophus % River lamprey Lampetra ayresii % Mosquitofish Gambusia affinis % Tule perch Hysterocarpus traskii % California roach Hesperoleucus symmetricus % Green sunfish 1 Lepomis cyanellus % American shad 1 Alosa sapidissima % Warmouth 1 Lepomis gulosus 96 <0.01% Hitch Lavinia exilicauda 54 <0.01% Smallmouth bass 1 Micropterus dolomieu 41 <0.01% Inland silverside 1 Menidia beryllina 23 <0.01% Black crappie 1 Pomoxis nigromaculatus 6 <0.01% White catfish 1 Ameiurus catus 6 <0.01% Fathead minnow 1 Pimephales promelas 4 <0.01% Wakasagi 1 Hypomesus nipponensis 4 <0.01% Channel catfish 1 Ictalurus punctatus 2 <0.01% White crappie 1 Pomoxis annularus 2 <0.01% Bigscale logperch 1 Percina macrolepida 1 <0.01% Black bullhead 1 Ameiurus melas 1 <0.01% Brown trout 1 Salmo trutta 1 <0.01% Common carp 1 Cyprinus carpio 1 <0.01% Native Total 14 2,441, % Introduced Total 21 8, % Native and Introduced Total 35 2,449, % Introduced fish species. 1 Exh. E - Environmental Report Application for New License April 2014 Page E ,

49 Table Relative abundance in descending order for fish observed by VAKI Riverwatcher TM passing through the fishways at Daguerre Point Dam on the Yuba River (RM 11.6) from 2008 through Common Name Scientific Name Catch (year) Total Catch Percent of Catch Chinook salmon Oncorhynchus tshawytscha 1,324 2,387 4,316 8, % Steelhead trout O. mykiss , % Sacramento sucker Catostomus occidentalis ,256 2, % Sacramento pikeminnow Ptychocheilus grandis % Hardhead Mylopharodon conocephalus % Total 5 2,914 3,662 6,372 12, % Temporal Distribution Both resident and anadromous fish in the Yuba River downstream of Englebright Dam exhibited temporal distributions that appear to be primarily related to spawning migrations. Chinook salmon exhibit the greatest variation in temporal occurrence, followed by steelhead. Details of migration and other life history information regarding these two anadromous species are discussed in the Applicant-Prepared Draft BA in Volume IV of YCWA s Application for New License. The temporal distribution of these two species, especially juvenile Chinook salmon, strongly influences overall species composition. Between February and May, the presence of juvenile Chinook salmon abundance is much greater than all other species, representing essentially nine out of ten fish observed by electrofishing, snorkeling, and RST surveys (Figure ). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

50 Relative Abundance of Fish Species Collected by RST at the Hallwood SIte (RM 7) on the Lower Yuba River, ,000, ,000 10,000 1, Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec American shad (Alosa sapidissima) Bluegill (Lepomis macrochirus) Black crappie (Pomoxis nigromaculatus) Brown Bullhead (Ameiurus melas) California Roach (Hesperoleucus symmetricus) Channel Catfish (Ictalurus punctatus) Chinook Salmon (O.tshawytscha) 897, , ,478 80,083 53,799 9,322 1, , ,913 Fathead Minnow (Pimephales promelas) Green Sunfish (Lepomis cyanellus) Golden Shiner (Notemigonus crysoleucas) Hardhead (Mylopharodon conocephalus) Hitch (Lavinia exilicauda ) Largemouth Bass (Micropterus salmoides) Mosquito Fish (Gambusia affinis) O. mykiss Pacific Lamprey (Lampetra tridentata) Prickly Sculpin (Cottus asper) Riffle Sculpin (Cottus gulosus) River Lamprey (Lampetra ayresii) Sacramento Pikeminnow (Ptycochelius grandis) Sacramento Sucker (Catostomus occidentalis) Smallmouth Bass (Micropterus dolomieu) Speckled Dace (Rhinichthys osculus) Threadfin shad (Dorosoma petenense) Tule Perch (Perca flavensa) Warmouth (Lepomis gulosus) Figure Temporal distribution of fish species observed during the RST surveys Similarly, adult Chinook salmon comprise over 80 percent of the fish observed with the VAKI Riverwatcher TM between August and September (Figure ). Sacramento sucker, Sacramento pikeminnow, and hardhead make up the majority of non-salmonid adults observed during the VAKI Riverwatcher TM surveys. These fish primarily migrate in spring from February through May (Figure ), with some adults moving in January, June and July. Exh. E - Environmental Report Application for New License April 2014 Page E ,

51 Figure Temporal distribution of primary species observed passing Daguerre Point Dam RM 11.6) during the VAKI Riverwatcher surveys from 2007 through The snorkel and electrofishing surveys conducted by Beak (1989) and Kozlowski (2004) only encompassed a few months (February and May for Beak, and July August for Kozlowski). These results show Chinook salmon to be dominant during the early spring (typically 80 percentplus) in all observed reaches. As juvenile Chinook salmon leave, the relative abundance of the resident fishes increase; however, the distribution does not appear to change. Spatial Distribution During both the Beak (1989) and Kozlowski (2004) studies, more species were observed downstream of Daguerre Point Dam than were observed upstream of the dam (Table ). Native species dominated the fish fauna, but consistent with species distribution, most of the introduced species observed in the Yuba River downstream of Englebright Dam occurred downstream of Daguerre Point Dam. The longitudinal pattern of species assemblages in the Yuba River downstream of Englebright Dam is influenced by several factors, including channel gradient, substrate, and seasonal water temperature. Higher densities of rainbow trout observed in upstream reaches is consistent with their preference for cold, swift-water habitats (Moyle 2002). Higher densities of non-salmonid April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

52 species in lower river reaches is consistent with their known preferences for lower velocity habitats and warmer water temperatures (except for sculpins; Moyle 2002). In general, slower water habitats prevail in the downstream reaches where the gradient is flat, compared to upstream reaches where the gradient is steeper. Additionally, an apparent selective barrier to migration created by Daguerre Point Dam appears to influence the broad-scale distributional pattern of species in the Yuba River downstream of Englebright Dam. Based on VAKI Riverwatcher TM survey results, species that navigate Daguerre Point Dam during their annual migrations in the Yuba River downstream of Englebright Dam include steelhead, Chinook salmon, Sacramento sucker, Sacramento pikeminnow, hardhead, American shad (Alosa sapidissima) and black bass. Although only one adult Pacific lamprey and no river lamprey were observed during the VAKI Riverwatcher TM survey, Pacific lamprey and river lamprey both spawn upstream of Daguerre Point Dam, as evidenced by the number and temporal distribution of juvenile Pacific and river lampreys observed in RST surveys. Fishes that make substantial inriver movements, but appear to be most affected by the presence of Daguerre Point Dam, include striped bass (Morone saxatilis) (and potentially green and white sturgeon). 16 Results of the referenced studies also suggest that upstream movement of other species, such as sculpins, may be affected by the presence of Daguerre Point Dam. Feather River Downstream of the Yuba River The Yuba River joins the Feather River at Yuba City (RM 28 of the Feather River), about half way between the confluence of the Feather and Sacramento rivers at Verona (RM 0) and Oroville Dam 17 (RM 67). The Feather River downstream from the Yuba River confluence is an alluvial stream flowing through sedimentary deposits of clay, silt, sand, and gravel. Historical hydraulic mining of Eocene gold bearing gravel deposits has caused the largest impact on the Feather River channel. Massive amounts of erosional debris, including cobbles, gravel, sand, silt, and clay, were washed into the river. Mining debris still profoundly affects the present day Feather River. Human modified cobble and clay banks have increased bank stability. Between the cities of Oroville and Gridley, cobbles and coarse gravel dredge tailings constitute most of the banks, slowing the bank erosion process. Flows into the lowermost 28 mi of the Feather River are a combination of releases from Oroville Dam directly into the Feather River at RM 67, releases from Oroville Dam indirectly through Thermalito Afterbay Outlet (TAO) at RM 59, and from the Yuba River and Honcutt Creek (Figure ). The Feather River reach from Oroville Dam to the TAO is termed the Low Flow Channel (LFC) (Cavallo et al. 2003); the river reach downstream of the TAO to the Sacramento River is called the High Flow Channel (HFC). The Bear River enters the reach about 20 miles downstream of the Yuba River confluence. Releases from TAO vary according 16 Anecdotal information on green and white sturgeon observed at the base of Daguerre Point Dam (pers. comm. Duane Massa). 17 Oroville Dam is part of the Oroville Facilities Project, which is the subject of the Final Environmental Impact Statement for the Oroville Facilities (P ) issued May 18, Exh. E - Environmental Report Application for New License April 2014 Page E ,

53 to operational requirements. In a normal year, total flow in the lower reach ranges from 1,750 cubic feet per second (cfs) in fall to 5,000 8,000 cfs in spring. Water temperature in winter is similar to the LFC, but increases to 23.3 C in summer. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

54 Figure Map of the Feather River in the vicinity of the confluence with the Yuba River. Exh. E - Environmental Report Application for New License April 2014 Page E ,

55 A variety of both native and introduced fish species occur in the Feather River downstream of the Yuba River, including federal and state listed species and species of concern. Native species that occur in the reach include green and white sturgeon, tule perch (Hysterocarpus traskii), Pacific and river lamprey, Chinook salmon, steelhead, two species of sculpin, hardhead, Sacramento sucker, Sacramento splittail, and Sacramento pikeminnow. The reach supports spawning and rearing for the resident, native species and is essentially a migratory route to upstream spawning and rearing for the native anadromous species. Introduced fish include six species of black bass, channel catfish (Ictalurus punctatus), white catfish, common carp, mosquitofish (Gambusia affinis), black and white crappie, two species of sunfish, American shad and striped bass. Special-status fish that can occur in this reach include Central Valley springrun and fall- late fall-run Chinook salmon, Central Valley steelhead, pink and chum salmon, green sturgeon, Pacific and river lamprey, hardhead and Sacramento splittail (Cavallo et al. 2003) (Table ) Fish Entrainment into Project Intakes To document the potential incidence of entrainment at Project intakes, YCWA conducted Study The intakes evaluated were: 1) Lohman Ridge Diversion Tunnel at Our House Diversion Dam; 2) the Camptonville Diversion Tunnel at Log Cabin Diversion Dam; 3) the New Colgate Power Tunnel at New Bullards Bar Dam; and 4) the Narrows 2 Power Tunnel at Englebright Dam. To measure entrainment at the intakes of the Lohman Ridge and Camptonville diversion tunnels during 2012 and 2013 diversions, YCWA utilized passive integrated transponder (PIT) technology. The primary goal of this component of the study was to determine if the withdrawal of water at the diversion tunnel intakes is likely to have adverse effects on trout and western pond turtle (WPT, Actinemys marmorata) populations. The assessment was based on detection of fish and WPT that were collected upstream of the diversions and implanted with PIT tags. For this purpose, YCWA installed a calibrated PIT-tag detection grid at the entrance of each tunnel. For a detection to occur, a PIT tagged fish or WPT would have to pass through the intake trash rack and be in the immediate vicinity of the detection grid. Entrainment was not directly measured at the New Colgate and Narrows 2 power tunnels. The potential for entrainment to occur at these intake structures was assessed utilizing YCWA s Study 3.7. The assessment used results of gill-netting information to characterize the occurrence of fish in the vicinity of the power tunnel intakes. The nets were set as close as possible to the intakes. Lohman Ridge and Camptonville Diversion Tunnels Fish collection for PIT-tagging took place from September 24 29, October 1 5, and October 16 18, Electrofishing was the primary mode of capture; however, gillnetting, hook-andline sampling, and seining were also used. Backpack electrofishing units were utilized on both streams and a boat electrofishing unit was used at Our House Diversion Dam Impoundment during day and night sampling efforts. Boat electrofishing was not feasible at Log Cabin Diversion Dam Impoundment due to seasonal low water conditions. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

56 In the Middle Yuba River, 189 rainbow trout and two brown trout were captured within the Our House Diversion Dam Impoundment (Zone 1) and from the impoundment upstream approximately 1.3 mi. Of the captured trout, 159 of the rainbow trout and both brown trout were PIT-tagged. Table summarizes effort by method, number of trout captured, and size of tag embedded in trout in each 0.1 mi zone. A majority of the fish tagged (60.9%) were from Zone 1. The only other fish species observed during the tagging effort were Sacramento sucker and Sacramento pikeminnow. Table Effort, number tagged, and total catch by 0.1 mi interval zone on the Middle Yuba River, upstream of Our House Diversion Dam. Zone 1 E-Fish Hook/Line Gillnet Trout tagged Total Not Total (seconds) (hours) (hours) 12 mm tag 23 mm tag Tagged Tagged 2 Catch , , , , , , , , Total Effort 42, Total Catch Zone 1 was Our House Diversion Dam impoundment; upstream of the impoundment, each zone was approximately 0.1 mi in length. 2 Not tagged due to size (i.e., generally less than 60 mm FL). 3 Fish tagged in Zone 1 included two brown trout. The remaining fish were all rainbow trout. WPT was not included as a focus species at this site for the study because there were no detections at Our House Diversion Dam Impoundment during YCWA s Study 3.6, Western Pond Turtle. In Oregon Creek, 436 rainbow trout were captured, of which 379 were tagged. Fish sampling was conducted within the Log Cabin Diversion Dam Impoundment (Zone 1) and from the impoundment upstream approximately 1.7 mi. Table presents a summary of effort by method, number of rainbow trout captured, and size of tag implanted in fish by zone. No brown trout were observed. Few rainbow trout were collected in Zone 1. Most of the fish (74% of the catch and 70.2% of tagged fish) were from Zone 11 and further upstream. The only other fish species observed during the tagging effort was Sacramento sucker. Exh. E - Environmental Report Application for New License April 2014 Page E ,

57 Table Effort, number of tagged fish (rainbow trout), and total fish catch by zone on Oregon Creek. Zone 1 E-Fish Hook/Line Seine Trout tagged Total Not Total (seconds) (hours) (passes) 12 mm tag 23 mm tag Tagged Tagged 2 Catch , , , , , , , Total Effort 16, Total Catch Zone 1 was the Log Cabin Diversion Dam Impoundment; upstream of the impoundment, each zone was approximately 0.1 m in length; Zone 7, 8, and 9 were inaccessible due to steep gradient. 2 Not tagged due to size (i.e., generally less than 60 mm FL). WPT was included as a focus species at Log Cabin Diversion Dam Impoundment after survey observations were recorded. Efforts to capture WPT for PIT-tagging using baited hoop nets and basking traps occurred from July 23 to 28, 2012, in the Log Cabin Diversion Dam Impoundment and 0.3 mi upstream of the impoundment. One adult male and one adult female WPT were captured in the pool 0.3 mi upstream of the impoundment. The individuals were measured, PITtagged, and released. YCWA also employed snorkeling on August 21, 2012 in an attempt to capture one WPT repeatedly observed in the impoundment in However, the snorkeling effort did not result in capture. The PIT monitoring system commenced operation at both diversion tunnels on October 22, 2012, at 10:00 a.m. Of the 5,613.5 hours of diversion flows in 2013, the Lohman Ridge Diversion Tunnel antenna array was installed and monitoring for 5,588 hours and was inoperable for 25.5 hours. The average time the array was not operating was 1.6 hours, and ranged from four minutes to 5.6 hours. Of the 5,587.6 hours of diversion flows in 2013, the Camptonville Diversion Tunnel antenna operated for 5,557.4 hours and was inoperable for 30.2 hours. The average time out per event was 2.2 hours, and ranged from 35 minutes to 5.6 hours. Antennas operated 99.7 and 98.0 percent of the monitoring period at the Lohman and Camptonville diversion tunnel antenna arrays, respectively. Tunnel maintenance and antenna repair led to removal of the arrays on several occasions. The Lohman Ridge Diversion Tunnel array was inoperable for a total of 97.5 hours and Camptonville Diversion Tunnel array was inoperable for hours in total (Table ). Entrainment could not be monitored during these periods. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

58 Table Date, duration, and discharge when antennas at Lohman Ridge Diversion Tunnel and Camptonville Diversion Tunnel were out of service. Lohman Ridge Diversion Tunnel Camptonville Diversion Tunnel Date Minutes Hours Discharge (cfs) Date Minutes Hours Discharge (cfs) 10/25/ /25/ /18/ /1/ /29/ /18/ /1/ /29/ /5/ /5/ /7/ /11/ /7/ /18/ /11/ /28/ /11/ /8/ /13/ /11/ /18/ /15/ /20/ /3/ /28/ /4/ /8/ /12/13-6/14/13 4, /25/ /30/13 9/01/13 2, /3/ /02/13-9/3/13 2, ¹ 6/12/13 6/14/13 4, Total 11, Total 5, ¹ Mean discharge during outage, mean daily discharge September 2 and September 3, 2013 was 16.6 cfs and 40.1 cfs, respectively. Both antenna arrays were turned off from June 12 through June 14, 2013 because the tunnels were not diverting. In addition, the Camptonville Diversion Tunnel antenna array was turned off during non-diversion from August 30 September 1, Several monitoring periods were identified as having less than optimal antenna performance during the data collection process. Reduced performance of the antennas was caused by a variety of complications including a faulty tag reader, reduced detection efficiency which included preferential tunning for the lower antennas, and radio interference from malfunctioning marker tags. The dates of potentially reduced performance included: December 5 20, 2012 at the Lohman Ridge diversion tunnel and the periods from December 28, 2012 January 8, 2013 and January 16 February 3, 2013 at the Camptonville diversion tunnel. Additionally, the middle antenna of the Camptonville tunnel array experienced efficiencies less than 80 percent and was wetted during: January 1 6, January 8 14, January 22 31, February 1 9, March 6, and March 20 April 17, These periods were examined in detail during the quality assurance and quality control process, to verify operation of the antennas. Specifically, consistent detections of both the marker tags and detections of tagged fish indicated that the antennas were operating correctly and collecting data, but may have failed to detect all fish passing through the array. The detections made during the periods described above are valuable data that should be included in the results of the study. However, at the request of Cal Fish and Wildlife, the Forest Service, and the Foothill Water Network, these periods were excluded from the calculation of entrainment metrics and alternate values are presented in parentheses in Table and Table This exercise resulted in the exclusion of 24 fish from the Middle Yuba River detected at the Lohman Ridge antenna and three fish from Oregon Creek detected at the Exh. E - Environmental Report Application for New License April 2014 Page E ,

59 Camptonville antenna. These detections provide valuable information to the study and YCWA stands by the originally reported numbers. A summary of the total numbers of individual fish detected at PIT arrays is presented in Table Overall, the efficiency of both systems was greater than 80 percent. On a single occasion, a fish from the Middle Yuba was detected at the Camptonville Tunnel without being detected at the Lohman Ridge Tunnel. The greatest number of fish detections was from the Middle Yuba River and 62.5 percent of those fish were later detected at the Camptonville Diversion Tunnel. Table Detections, number of fish, and origin of fish detected at Lohman Ridge and Camptonville diversion tunnels. 1 2 Detection Station Detections Individual fish detected Middle Yuba origin Oregon Creek origin Fish per Day Lohman Ridge Diversion Tunnel 65(35) 49 (25) 1 48 (24) (0.13) Camptonville Diversion Tunnel 155(131) 39(31) 30(25) 8(5) 0.03 (0.01) Total 2 220(166) 58(34) 48 (24) 9(7) -- Values in parentheses were calculated in response to Cal Fish and Wildlife, the Forest Service, and Foothills Water Network, requests to eliminate selected monitoring periods with questionable antenna performance. The total is not the sum of the two tunnels because in some cases, fish passed through both tunnels, and returned back through tunnels. Some totals in parentheses cannot be totaled because some fish were lost in the elimination of certain monitoring periods at the request of Cal Fish and Wildlife, the Forest Service, and the Foothills Water Network. Sixty-five detections occurred at the Lohman Ridge Diversion Tunnel, representing 49 individual fish. One fish tagged in Oregon Creek traveled up the tunnel and was detected at the antenna array. Of the 161 fish tagged in the Middle Yuba River, 48 (29.8%) were detected in the tunnel. Most detections (n=49) occurred early in the study, prior to December 31, 2012 (Figure ). The remaining 16 detections occurred between January 1, 2013 and June 19, The most fish detected on one day (twelve fish or 25% of all detected fish in Lohman Diversion Tunnel), were recorded on December 15, 2012 at a flow of 197 cfs. Most detections (67.7%) occurred at flows less than or equal to 200 cfs, which were the most common diversion rates (79.1% of total) throughout the study. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

60 Figure Summary of detection and rate of diversion at Lohman Ridge Diversion Tunnel. A total of 155 detections occurred at the Camptonville Diversion Tunnel, representing 39 individual fish. Most fish detected (n=30) in the tunnel were of Middle Yuba River origin. Of the 379 fish tagged in Oregon Creek, only eight fish (2.1% of total) were detected in the tunnel. Detections were well distributed throughout the study, although the highest frequency of detections (n=58) occurred in April 2013 (Figure ). One detection occurred on June 29, The most fish detected (n=5) on a single day at Camptonville Diversion Tunnel occurred December 16, 2012 at a mean daily flow of 237 cfs. Of the five fish detected, four were tagged in Oregon Creek. Most detections (63.8%) occurred at diversion rates less than or equal to 250 cfs, which were the most common (79.1% of total) diversion rate throughout the study. Exh. E - Environmental Report Application for New License April 2014 Page E ,

61 Figure Summary of detection and rate of diversion at Camptonville Diversion Tunnel. A number of unique detection scenarios unfolded over the course of the study. Multiple detections at an array in no more than a 24-hour period by the same fish, an indicator of milling behavior, were observed at both antenna arrays (Table ). At the Lohman Ridge array two fish approximately 165 mm FL were detected multiple times at flows ranging from cfs. Multiple detections in a 24-hour period were more common at the Camptonville array. Five fish ranging from mm FL were detected multiple times at flows ranging from cfs. Some fish were observed holding in the turbulent water downstream of debris against the trash racks at the Camptonville tunnel, but similar debris conditions were not observed at the Lohman Ridge Tunnel. Table Summary of fish that generated multiple detections with no more than a 24-hour period between detections. PIT tag ID Length (mm) Period # Detections Mean Daily Flow (cfs) LOHMAN RIDGE PIT ARRAY DETECTIONS ACCAB3B 167 4/23/2013 4/24/ ACCABF /14/ /15/ CAMPTONVILLE PIT ARRAY DETECTIONS ACCAB9B /16/ /2/2013 1/3/ ACCABF /10/2013 4/15/ /17/2013 5/2/ /5/2013 1/6/ /30/2013 1/31/ ACCAC2F 349 2/5/2013 2/6/ /18/2013 2/20/ /25/ /14/2013 3/15/ April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

62 Table (continued) PIT tag ID Length (mm) Period # Detections Mean Daily Flow (cfs) CAMPTONVILLE PIT ARRAY DETECTIONS (continued) ACCAC /11/ EA81B9C 80 6/6/2013 6/7/ Detections also documented the occurrence of five fish moving upstream through the Lohman Ridge tunnel (Table ). Four of these fish were documented making a round trip from the Middle Yuba River to Oregon Creek and back. These four fish were each detected at least once at the Lohman Ridge antenna, followed by sequential detections at the Camptonville and Lohman Ridge antennas. The duration of these movements ranged from weeks to months. The fifth fish was tagged 1.1 mi upstream of Log Cabin Dam and was detected six times in June at the Lohman Ridge antenna. This fish was never detected at the Camptonville antenna. Table Summary of fish that moved up the Lohman Ridge Tunnel. PIT Tag ID Length (mm) # Detections Detection History ACCAB9B ACCABB ACCABF ACCAC2F EA81B9C 80 6 Fish was tagged in Middle Yuba River on 10/2/2012 and initially detected during a flow of 197 cfs at Lohman array on 12/15/2012. It was then detected at Camptonville array from 12/16/2013 to 5/15/ times at flows ranging cfs. It was last detected at Lohman array on 5/15/2013 at a flow of 41 cfs. Fish was tagged in Middle Yuba River on 10/16/2012 and initially detected during flow of 460 cfs at Lohman array on 12/17/2012 then again at 181 cfs on 1/3/2013. It was then detected at Camptonville array during a flow of 336 cfs on 1/29/2013 and 61 cfs on 5/13/2013. It was last detected at Lohman array on 5/14/2013 at a flow of 59 cfs. Fish was tagged in Middle Yuba River on 10/3/2012 and initially detected during flow of 460 cfs at Lohman array on 12/17/2012. It was then detected at Camptonville array from 4/5/2013 to 5/5/ times at flows ranging cfs. It was last detected at Lohman array on 6/19/2013 at a flow of 10 cfs. Fish was tagged in Middle Yuba River on 10/3/2012 and initially detected during flow of 775 cfs at Lohman array on 12/1/2012. It was then detected at Camptonville array from 1/5/2013 to 3/15/ times at flows ranging cfs. It was last detected at Lohman array on 5/21/2013 at a flow of 32 cfs. Fish was tagged on 10/1/2012 in Oregon Creek and was then detected at the Lohman array six times from 6/6/2013 to 6/7/2013 at a flows ranging from 2 4 cfs. Study 3.11 resulted in an estimated rate of rainbow trout entrainment into the Lohman Ridge Diversion Tunnel of 0.56 fish per day, and an estimated rate of rainbow trout entrainment into the Camptonville Diversion Tunnel of 0.03 fish per day (Table ). Exh. E - Environmental Report Application for New License April 2014 Page E ,

63 Table Estimated entrainment of rainbow trout into the Lohman Ridge and Camptonville diversion tunnels based on 2012/2013 Entrainment Study. Site Number of Tagged Fish in Sampled Area Rainbow Trout Tagged in Sampled Area 1 Number of % of Tagged Fish Tagged Fish Entrained Rate of Tagged Fish Entrained 4 Number of Fish in Sampled Area Rainbow Trout in Sampled Area Assumed Number of Fish in Sampled Area Entrained 8 Rate of Fish in Sampled Area Entrained 9 Entrained 3 LOHMAN RIDGE DIVERSION TUNNEL MIDDLE YUBA RIVER Our House Dam Impoundment 89 35(18) ( (0.07) fish/day (30) 0.22(0.12) fish/day Middle Yuba River Upstream of Our House 72 13(6) 18.1( (0.02) fish/day (41) 0.34 (0.16) fish/day Diversion Dam Impoundment Subtotal (24) 29.8(14.9) 0.18(0.10) fish/day (96) 0.56 (0.38) fish/day CAMPTONVILLE DIVERSION TUNNEL OREGON CREEK Oregon Creek 379 8(5) 2.1(1.3) 0.03(0.03) fish/day (6) 0.04(0.03) fish/day Upstream of Log Cabin Dam The sampled area in the Middle Yuba River included the Our House Diversion Dam impoundment and 1.3 mi upstream of the impoundment. The sampled area in Oregon Creek included 1.7 mi upstream of Log Cabin Dam (i.e., the dam did not create an impoundment during the sampling period, and 0.3 mi were not sampled due to steep terrain). Values in parentheses were calculated in response to comments on the DLA from Cal Fish and Wildlife, the Forest Service, and Foothills Water Network. From October 22, 2012 through November 7, 2013, during the periods that the antenna arrays were operating, water was diverted into the Lohman Ridge Diversion Tunnel and the Camptonville Diversion Tunnel for 265(249) days and 253(182) days, respectively. Calculated by dividing the number of tagged fish entrained by the total number of days that water was diverted and the antenna array was operating. Based on mark-and-recapture calculations. Based on multiplying the estimated 409 fish/mi found during YCWA s Study 3.8, Stream Fish Populations, times the 1.2-mi length of stream sampled. Since the tagging effort caught substantially more fish per mile (257 fish/mi) than estimated during YCWA s Study 3.8, Stream Fish Populations, (72 fish/mi), YCWA used the larger number in this entrainment calculation. Note that YCWA collected 436 fish, but tagged 379 because some fish were too small to tag. Calculated by multiplying the percent of tagged fish entrained by the number of fish in the sampled area. Calculated by dividing the assumed number of fish in sampled area entrained by the total number of days that water was diverted and the antenna array was operating April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

64 New Colgate Power Tunnel The potential for fish entrainment into New Colgate Power Tunnel was assessed using gillnet data from a Study 3.7 site (Site 1) located as close as feasible to the dam and the deepwater intake. Over the time period that the nets were fished near the intake, the diversion rate fluctuated from 50 to 2,341 cfs (average 490 cfs) in January and 49 to 3,189 cfs (average 1,517 cfs) in June. Catch at this site was the lowest of the eight sites surveyed in New Bullards Bar Reservoir. Catch in the deepwater nets (30 m below the surface) at Site 1 was limited to one kokanee (211 mm) and one spotted bass (482 mm), which represented 11 percent of all fish collected at the site (Table ). All but one of the remaining fish, a spotted bass caught mid-water, were collected near the surface, which was the general trend throughout the reservoir. During the sampling periods, the power tunnel intake depth was at least 65 m. Table Summary of catch by gillnet depth at Site 1 near New Bullards Bar Dam in January and June Species January 2012 June 2012 Shore Floating Mid-water Deep 1 Shore Floating Mid-water Deep 1 Kokanee Rainbow trout Spotted bass Green sunfish Total Deepwater nets fished at approximately 30 m, but the intakes were never shallower than 65 m throughout both sampling events. In 2012, New Bullards Bar Reservoir reached its lowest elevation of m (1,874 ft) on January 19, which also corresponded with the last day of gillnet sampling. The water surface elevation peaked, for the year, on May 22, 2012 at m (1,954 ft), just under a month before the June 18 sampling event. Sampling was as deep as 30 m, but the power tunnel intake used exclusively since 1993 was never shallower than 65 m throughout both sampling events. Narrows 2 Power Tunnel YCWA used gillnet data from Study 3.7 to assess the potential for entrainment from the reservoir into the Narrows 2 Power Tunnel. The Study 3.7 site (Site 1) was located as close as feasible to the dam and its deepwater intake. Over the time period that the nets fished near the intake, the diversion rate fluctuated from 1,125 to 1,151 cfs (average 1,139 cfs). Catch at this site was the lowest of the four sites in Englebright Reservoir. The depth of the intake ranged from 17.3 to 21.8 m from January through early July of YCWA was able to set gillnets at these depths to characterize fish presence and the potential for entrainment. The deepwater-net catch included two rainbow trout and one brown trout, representing 20 percent of all fish collected at Site 1 (Table ). Brown trout and rainbow trout were both recently stocked in the reservoir. All other fish were found near the surface, which was the general trend throughout the reservoir. Exh. E - Environmental Report Application for New License April 2014 Page E ,

65 Table Summary of catch by gillnet depth at Site 1 near Englebright Dam from June 22-24, Species Shore Floating Midwater Deep 1 Brown trout Rainbow trout Spotted bass Green sunfish Hardhead Sacramento pikeminnow Sacramento sucker Total Deepwater nets fished at the same depth of the intake which ranged from approximately 18-21m. Historic Project operations show a consistent mildly-fluctuating reservoir elevation throughout the year. Coordinated operations of New Colgate and Narrows 2 powerhouses, and coordination between PG&E and YCWA in operating Narrows 1 and 2 powerhouses, minimize fluctuations in the river downstream for the protection of fish and reservoir elevations in Englebright Reservoir. Reduced reservoir fluctuations limit adverse effects to recreation and results in annual total fluctuations of less than 4.5 m (15 ft) in reservoir stage. Mild fluctuations occurred during the 2012 sampling period and were generally representative of normal operations Fish Behavior and Hydraulics Near Narrows 2 Powerhouse Review of historical data addressed historical operations, salmonid periodicity and a 3-year long telemetry study at Narrows 2 Powerhouse. Operations of Englebright Dam, Narrows 1, and Narrows 2 powerhouses from WY 2009, following installation of the Full Bypass, to the current WY 2012 depended on water quantity and subsequent water year type. In wet years, like WY 2011, Narrows 1 Powerhouse operated at a predictable and steady rate. The 2009 dry water year also showed relatively steady operations from Narrows 1 Powerhouse, but in WY 2010 (below normal) operations were more variable. Narrows 2 Powerhouse releases fluctuated with the upstream hydrograph, passing upstream flows, and ramping up during potential spill events. Spill events were frequent in wet years (WY 2011). Historical periodicity showed that steelhead migration typically occurred August through March, whereas fall-run Chinook salmon migration occurred September through January. Spring-run Chinook salmon migrated from April through August (USACE 2011). Telemetry monitoring of adult spring-run Chinook salmon occurred from 2009 to The site closest to the Narrows 2 Powerhouse (RM ) represented only 4.6 percent of total detections. At RM , the earliest detected fish was in July 2009, but generally fish began to appear in September (Figure 3.2-1). At the RM , fish were still observed into November, but detections did not occur at the furthest upstream monitoring location (RMT 2009). From December 2011 through early November 2012, YCWA Powerhouse staff had recorded incidental fish observations that included one jumping adult (species unknown) in January 2012 and then no observations until August 2012 when two fish were observed. A single fish was observed on October 23, 2012 holding in the Bypass Pool. Additionally, four observations were April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

66 made in November 2012 that included a holding behavior in the bypass pool. Observed behavior was generally jumping from the water surface. To document the potential interaction of the operations of the Narrows 2 Powerhouse with nearby salmonids, YCWA conducted Study Salmonids included in the study were fall and spring-run Chinook salmon and rainbow trout/steelhead. To assess the presence, potential for exposure, and resultant behavior of salmonids proximal to the Narrows 2 facilities, a series of different activities were implemented. These activities included: 1) operational monitoring and characterization; and 2) direct observation of fish. Figure shows areas of interest near the Narrows 2 Powerhouse. Englebright Dam Narrows 2 Powerhouse Dam Pool Bypass Pool Full Bypass (3,000 cfs capacity) Partial Bypass (650 cfs capacity) and Draft Tube Outlet (3,400 cfs capacity) Narrows 2 Pool Location of downstream water temperature logger Figure Looking upstream to the location of the study area in proximity to the Narrows 2 Powerhouse. Operational Monitoring Continuous monitoring provided information on water velocity in the Narrows 2 Powerhouse, as well as water surface elevations and water temperatures in the Bypass and Dam pools. The modeled results, from YCWA s Study 7-11, show that flow entering the penstock before the runner is accelerated and then slows as it approaches the draft tubes. Velocity also increases in all locations with greater discharge from the powerhouse. Velocity before the runner is greater than near the outlet. At low power generation flows (i.e. 900 cfs), velocity starts at ft/sec above the runner, accelerates to ft/sec below the runner, and then reduces to 6.79 ft/sec at Exh. E - Environmental Report Application for New License April 2014 Page E ,

67 the outlet. At maximum power generation (i.e. 3,400 cfs), the velocity starts at ft/sec, accelerates to ft/sec, and then reduces to ft/sec at the outlet. Water surface elevation monitoring occurred from August 9 through October 25, 2012 The Dam Pool and Bypass Pool elevations remained nearly identical throughout the entire recording period. Both pools were directly influenced by the discharges from the powerhouse and releases from the Full Bypass. Both pools were connected by surface water at discharges above 1,570 cfs. At 1,660 cfs, the surface water channel connecting the two pools measured approximately 0.5 ft wide. Although biologists surveyed a stage at zero flow for the Dam Pool at that channel, YCWA found that the two pools are connected through interstitial flow below the rocks and boulders which allows the Dam Pool to drain below the zero flow. During a 2-day period where Narrows 2 was generating approximately 880 cfs, both pools continued to drain by almost 1 foot. Continuous hourly temperature monitoring occurred at five locations from August 9 through October 25, Two temperature loggers were deployed in the Dam Pool near-surface and at the bottom of the pool. The upper logger was tethered to a buoy and remained near-surface as the water surface elevation fluctuated. The other three loggers were located in the Bypass Pool, the penstock entering Narrows 2 Powerhouse, and approximately 100 ft downstream of the Narrows 2 Powerhouse. Prior to August 22 the water temperature at the surface of the Dam Pool was approximately 10 C warmer than the bottom of the pool. A decrease in surface water temperature occurred on August 22 and August 31, coinciding with transfer of flow from Narrows 2 Powerhouse to the Full Bypass. By September 1, top and bottom water temperatures were nearly identical due to backwater mixing from the Full Bypass. Spikes in the Bypass Pool temperature occurred on August 22 and September 21. The temperature changes were due to rapid water mixing between the Dam Pool and Bypass Pool as water surface elevation in the Bypass Pool quickly changed, causing water inflow and outflow between the two pools. Prior to August 31, a temperature gradient occurred between the Bypass Pool and the surface water of the Dam Pool. On August 31, the Full Bypass began continuously operating, which allowed penstock flows to enter the Dam Pool. From August 31 through the October 25, water temperatures between the two pools remained relatively mixed. Direct Fish Observations Snorkeling efforts to identify species composition and behavior patterns were conducted over ten events between May through October Twice-monthly monitoring began in July and continued through December 15, Observed species included rainbow trout, Chinook salmon, black bass, Sacramento pikeminnow, and Sacramento sucker. Bass and pikeminnow, when found, were generally in the Dam Pool (Figure ), where water temperature was consistently greater than 20 C in August. Chinook salmon and rainbow trout were most prevalent in the pool downstream of Narrows 2 Powerhouse (Narrows 2 Pool), but were also found in the pool adjacent to the Narrows 2 Full Bypass Pool. No Chinook salmon or rainbow trout were observed in the Dam Pool. Snorkeling conditions were challenging making a reliable relative abundance estimate infeasible. The general behavior of salmonids was milling, with a April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

68 tendency to flee field biologists once observed. Fish were never observed entering the draft tubes or interacting directly with the Narrows 2 Powerhouse. All Narrows 2 Powerhouse operational changes involving shut-down, start-up, diversion of flow to the Full Bypass, or a change of more than 400 cfs were monitored. Five events occurred between July 15, 2012 and November 12, During the events, a DIDSON camera generally was deployed. The DIDSON camera recorded one day prior, day of, and at least one day following each event. Current results showed that the camera performed well when water was being released through the Full Bypass, but visibility was limited during releases from Narrows 2 Powerhouse. In 2013, YCWA began monitoring operational change events from July 15 to December 15. Monitoring included making visual observations from the shoreline as well as monitoring with the DIDSON camera four hours prior to, during, and four hours after the operational change. This monitoring approach differed from 2012, as snorkeling did not occur and DIDSON monitoring was reduced from full 24-hour periods before and after monitoring to 4 hours in Seven observation events and one outage monitoring event occurred. A summary of each of these events is included in Table Table Summary of planned and actual operational events from July through November Event Event 1 Announcement to Relicensing Participants Date July 31 and August 1, 2 and 7, 2013 Event Date(s) August 8, 2013 Summary OPERATIONAL EVENT Beginning on August 1, YCWA began working with PG&E to transfer flow (i.e. generation) from the Narrows 2 to the Narrows 1 Powerhouse following an outage period. Challenges with bringing Narrows 1 Powerhouse back online resulted in two unsuccessful attempts on August 1 and August 2. YCWA was informed PG&E was planning to work until August 9 on Narrows 1 Powerhouse to conduct the measures to remedy discovered issues. PG&E then alerted YCWA on August 7 that another attempt would be made on August 8 to bring Narrows 1 Powerhouse online. This attempt was successful at 6 pm, August 8. During this time, YCWA has left the DIDSON camera continuously collecting data from August 1 through the morning of August 9 (following the successful event). Staff was present during August 1, 2, and 8 to observe and document fish behavior in anticipation of the operational change. The event occurred on August 8 and DIDSON monitoring and fish observations occurred from the waters surface. Event 2 August 22, 2013 August 25, 2013 An operational event occurred and was successfully monitored on August 25, Shoreline fish observations were made and the DIDSON camera recorded pre-, during and post-event fish behavior. Bypass did not occur. The planned 9 am event occurred at 11 am when flow increased from 788 cfs to 1,217 cfs through the powerhouse as generation. The magnitude of flow change necessitated the monitoring event, but the powerhouse maintained power-generation status during the entire period. The 2-hour delay was a result of minor logistical issues. Fish were observed on the DIDSON camera. Exh. E - Environmental Report Application for New License April 2014 Page E ,

69 Table (continued) Event Event 3 Announcement to Relicensing Participants Date August 22, 2013 Event Date(s) August 31, 2013 Summary OPERATIONAL EVENT (continued) On Saturday August 31, YCWA conducted an operational change that reduced flow from the Narrows 2 Powerhouse from 709 cfs of generation to 41 cfs of bypass through the partial bypass. The YCWA monitoring team was onsite and conducted onshore visual observations and DIDSON camera monitoring. Prior to the changeover the DIDSON camera was positioned at a new location collaboratively agreed upon with NMFS (described above) and the gear housing was moved. During the operational change, the width of the water plume was wider than initially anticipated. The force of the water intruded into the gear housing and damaged the data logger. Unfortunately, DIDSON monitoring was not recorded during the August 31, changeover or following it due to the damaged data logger. Recordings were made prior to the changeover and visual observations were completed and will be documented. The DIDSON was repaired, and the new location with the reinforced housing was used in subsequent events. Observations from the surface and on the DIDSON camera were made prior to the changeover, but not during or following due to the water damage. Event 4 September 27, 2013 October 1, 2013 YCWA approached the conclusion of the outage at Narrows 2 Powerhouse and passed water through the powerhouse to test function. Some 74 cfs was put through the Partial Bypass. The discharge continued, but near 4pm an additional 300 cfs (approximately) was passed through the Narrows 2 Powerhouse for a brief period (estimated time less than 10 minutes). Flow then ceased through the Narrows 2 Powerhouse, but continued through the Partial Bypass. Behavioral observations from the shore occurred prior to, during and after the event and the DIDSON camera collected footage as well. Flow from the partial bypass did not change and therefore did not require a stranding survey. Fish were observed from the water surface and on the DIDSON camera. Event 5 October 7, 2013 October 7, 2013 An operational event occurred at 2:00 pm. Increased water demand required for flow to be transitioned from the Partial Bypass to the Full Bypass. The transition allowed for more response and flexibility by operators for releasing additional capacity from the Full Bypass to address rising water needs. YCWA monitoring staff conducted visual observations, DIDSON monitoring, and a Stranding Survey. Stranded fish were not observed, but fish were observed from the waters surface. Event 6 October 11, 2013 October 11, 2013 An operational event occurred before noon. Power necessitated that flow from the Full Bypass (near 200 cfs) be transferred to generation at 800 cfs. YCWA field teams conducted DIDSON monitoring and fish behavior observations for the shoreline. Fish observations were made and also collected on the DIDSON camera. Event 7 -- November 22, 2013 A seventh event occurred on November 22, 2013 when, in the morning, the 1,000 cfs of flow through the Narrows 2 Powerhouse was switched to 800 cfs through the Narrows Full Bypass. In the evening, the full flow was returned to the Narrows 2 Powerhouse. Prior to and during the morning switch-over, DIDSON and visual monitoring occurred. During the evening switch-over, only DIDSON monitoring occurred because it was too dark to perform visual observations. Outage August 14, 2013 September 8 30, 2013 PLANNED OUTAGES Operators shortly after 7 am transferred approximately 30 cfs running through the Partial Bypass to the Full Bypass and maintained flow between 200 to 300 cfs as of current during an outage period at Narrows 2 Powerhouse. This condition continued through September 30. The low flow resulted in minimal change in overall conditions and difference in water stage was negligible. The DIDSON camera operated successfully before, during and after the change and continued to operate through the outage. Behavioral observations were made pre-, during, and following the operational. Three staff also walked the shoreline from Narrows 2 to Narrows 1 powerhouse and thoroughly searched for stranding. Stranded fish were not observed. Following the event, a large school of adult Chinook salmon were observed moving upstream and milled within the vicinity of the Narrows 2 Powerhouse. The fish were observed clearly on the DIDSON camera. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

70 Table (continued) Event Announcement to Relicensing Participants Date Outage -- Event Date(s) October 13, 2013 Summary UNPLANNED OUTAGE An emergency event occurred that could not be monitored. Harmonic vibration at the Narrows 2 Powerhouse required for a temporary change from generation to Full Bypass and then a return to generation. The notice of the event from the operator was following the situation due to its urgency. These operational changes monitoring have documented salmonid presence in proximity to the Narrows 2 Powerhouse during operations. The abundance of fish present ranged from less than ten to over 100 fish identified from the DIDSON camera. In September and October 2013, a school of Chinook salmon ranging from 20 to 50 individuals at times, was frequently observed milling in front of the powerhouse. One to two adults infrequently were observed breaking the water s surface and leaping into the air. Behavioral observations have shown that fish appear to mill within the upper 60 percent of the water column (i.e. top 3.7 m of water) with no apparent association with flow direction. Individuals will periodically swim through deeper water where flow becomes more laminar in mid-depths of representing 30 percent of depth ( m of depth). At depth ( m), fish will hold near the substrate where velocity refuges are created from the structure of the base of the powerhouse and angular substrate. Fish can be observed milling in proximity of the powerhouse, but cannot be clearly identified to be moving within the draft tubes and no mortality as a result of the powerhouse or turbine has been observed to date Fish Stranding Downstream of New Colgate Powerhouse YCWA was unable to find any historical information on fish stranding or fish stranding surveys of the resident fish population in the Yuba River between New Colgate Powerhouse and Englebright Reservoir. In its 2012 Study 3.12, YCWA investigated ramping of New Colgate Powerhouse in the 1.79milong section of the Yuba River between the New Colgate Powerhouse and the NMWSE of Englebright Reservoir. The goal of the study was to determine the occurrence of and potential for fish stranding in the Yuba River downstream of New Colgate Powerhouse due to Project ramping operations. Study methods and analyses included field measurement and modeling of flow, depth, velocity, wetted perimeter, and areas of inundation at seven collaboratively selected transects and, visual observations for fish stranding at each cobble bar. Of the seven transects, four were located at Exh. E - Environmental Report Application for New License April 2014 Page E ,

71 Condemned Bar (RM 33.9) and three French Bar (RM 33.1). 18 The target species for analysis and observation was resident rainbow trout, though all observed species were documented. Six visual observation surveys were performed, one each on June 12 and 13; July 27 and 28; and August 25 and 30, Each survey began approximately one hour before a New Colgate Powerhouse down-ramp event was scheduled to begin, continued throughout the down-ramp event, and terminated no less than one hour after down-ramp event ended. Flow reductions ranged from 1,000 to 1,662 cfs, with starting flows ranging from 1,509 to 3,261 cfs. Visual observation surveys were conducted to document fish presence in the varial (i.e., fluctuating) littoral zone by walking or snorkeling before and after down-ramp events. The intent of these surveys was not to quantify the number of fish present, but rather to confirm fish presence, thereby implying a potential for stranding. All stranding observations were made in three specific locations that appeared to possess highstranding potential. Stranding Zone A was located at the head of Condemned Bar, near the confluence of Dobbins Creek. Stranding Zone B was located downstream on the opposite side of the river from Condemned Bar. Stranding Zone C was located at the end of French Bar on river left. Each zone was characterized by boulder and cobble substrate, though they also contained sand in the interstitial spaces between boulders. Study site reach maps showing the three Stranding Zones are presented in Figures and below. 18 Both Condemned Bar and French Bar were identified mining bar communities as early as the 1880 s (Figure 23-1 in the HPMP, Volume V of Application for New License). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

72 Page Left Blank Exh. E - Environmental Report Application for New License April 2014 Page E ,

73 Figure Location of Condemned Bar downstream of the New Colgate Powerhouse. Hydraulic transects, bar habitat mapping, fish stranding survey routes and fish stranding observations are shown. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

74 Figure Location of French Bar downstream of New Colgate Powerhouse Reach. Hydraulic transects, bar habitat mapping, fish stranding survey routes and fish stranding observations are shown. Exh. E - Environmental Report Application for New License April 2014 Page E ,

75 YCWA documented three fish species (i.e., rainbow trout, sculpin spp., and green sunfish) and one unidentified species in the survey area before and after down-ramping of flows occurred. Of the 1,628 fish observations from the six surveys, six percent (n=100) were rainbow trout ranging from 40 mm to 505 mm in length. The remaining 94 percent (n=1,528) of all observations consisted primarily of an unidentified species, with only two sculpin and three green sunfish observations. No rainbow trout were observed in the vicinity of French Bar. Sixteen stranded fish were observed during three of the six down ramp events in The stranded fish included one rainbow trout and fifteen unidentified juvenile fish. Stranded fish (n=15) were observed during two of the lower range ramp down events (1,541 cfs to 541 cfs) and one (n=1) of the higher range events (3,261 cfs to 1,599 cfs). The one rainbow trout was found at Condemned Bar and measured 40 mm FL. The unidentified species were found at both surveying locations (Condemned Bar and French Bar) and ranged in length from mm. The composition of the two species found stranded are consistent with the species composition recorded during prior surveys. In addition, stranding results totaled by month followed a similar seasonal trend in total monthly abundance of all species. June had the most stranded fish observed with 13 individuals, while July had one and August had two. There was a similar number of fish stranded at Condemned Bar (n=9) as compared to French Bar (n=7). Figure shows stranding counts by survey date for Condemned Bar and French Bar. Condemned Bar French Bar Count 3 Count Jun 12 Jun 13 Jul 27 Jul 28 Aug 25 Aug 30 0 Jun 12 Jun 13 Jul 27 Jul 28 Aug 25 Aug 30 Survey Event Survey Event Unknown Spp. Rainbow Trout Unknown Spp. Rainbow Trout Figure Condemned Bar and French Bar stranding survey counts by event. Surveyors were unable to identify the abundant unidentified species for a variety of reasons. However, surveyors were able to positively distinguish the unidentified species as nonsalmonids. First, all individuals were small and less than 30 mm in length with most individuals less than 20 mm in length. Second, because the surveys were visual, fish were not captured or handled making identification of fish this size particularly difficult. Third, the most predominant non-salmonid fish species potentially occurring in the study area (i.e., Sacramento sucker and pikeminnow) are difficult to differentiate when in the larval or young-of-year life stage. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

76 This study documented all species observed; however, the primary focus was on rainbow trout. Of the 16 stranding observations made during the study, only one observation made during the stranding surveys was of rainbow trout. An additional observation of a potentially stranded rainbow trout was made during Study 3.8 surveys. Fish species listed as threatened or endangered under the federal Endangered Species Act or the California Endangered Species Act, or otherwise considered special-status, were not found stranded. Results of the pre- and post-ramp down surveys showed that fish (e.g., rainbow trout, sculpin, green sunfish and unidentified spp.) were present in similar numbers and composition in the survey areas before and after down-ramp occurred. Of the total 1,628 fish observations from the six surveys, 6 percent (n=100) were rainbow trout ranging from 40to 505 mm in length. All rainbow trout were in the vicinity of Condemned Bar, primarily in the deep, swift pool where transects R7, R6 and R5 were placed. The observation of adult rainbow trout in pre- and postramp surveys as well as in fish surveys conducted in support of Study 3.8, indicate a persistent population that is not forced downstream by daily pulsed flows. This finding is consistent with recent research on the South Fork American River where radio-tagged rainbow trout remained in the study area with significant daily pulse flows ranging from 176 to 1,412 cfs (Cocherell et al. 2010). All stranded fish of any species observed were less than 50- mm-long, and 75 percent were less than 15-mm-long. The two rainbow trout were 40 and 50 mm, the latter from an incidental observation. Though very limited, these results are consistent with studies that have shown limited stranding of salmonid fry after they reach 40 to 50-mm-long (Pacificorp 2004; Hunter 1992; Olson 1990). All unidentified stranded fish were less than 15-mm-long. This indicates a strong relationship between the number of newly emerged larvae and young-of-year and the likelihood of stranding during the early summer rearing period. Fish of this size have a reduced swimming capacity as compared to juvenile or adult fish of the same species (Vogel 2007; Moyle 2002). Native larval and fry life stages are more likely to use shallow habitat along the river margin (Lorig et al. 2012; Bradford 1996), and have reduced swimming abilities (Moyle 2002). Fish in these early life stages are oftentimes adapted to utilize these shallow margin habitats because they have favorable velocity refuges, refuges from larger piscovores, warmer water temperature, and relatively abundant invertebrate prey items associated with adjacent vegetation and fine grained sediments (Moyle 2002; Gadomski et al. 2001; Harvey et al. 2002). Few studies have documented the influence of ramping on rainbow trout spawning behavior (Pacificorp 2004). In this study, no rainbow trout young-of-year or fry were observed during the pre- and post-ramping surveys. This suggests that the adult rainbow trout observed in the reach are not actively spawning or, newly emerged young-of-year are not using the varial zone. Since locations of suitable rainbow trout spawning gravel or evidence of spawning redds have not been identified in this reach, it is difficult to accurately predict the influence of daily flow changes in depth and velocity and the subsequent effect on spawning success. If rainbow trout are successfully spawning in this reach, the newly emerged rainbow trout were not documented in the nearshore habitats surveyed during this study. In a study on the effects of hydro-peaking on nearshore habitat use by young-of-the-year rainbow trout, Korman (2009) reported limited use of Exh. E - Environmental Report Application for New License April 2014 Page E ,

77 areas frequently subjected to dewatering and inundation and suggested that they were therefore holding further offshore. Another possible reason for limited rainbow trout stranding is that native fish that are commonly exposed to variable hydrographs, as they are in this reach, are less likely to be stranded when compared to non-native species (i.e., Centrarchids) and are more adapted to flow fluctuation (Sommer et al. 2005). Studies have shown that cold water temperatures of less than 7 C can increase the incidence of salmonid stranding (Bradford 1996; Saltveit 2001; Halleraker 2003). In the river directly downstream of New Colgate Powerhouse, an average monthly mean temperature 10 C was recorded during the period of study. As this temperature is within the tolerance of rainbow trout (Moyle 2002), it is unlikely that these temperatures would increase their stranding potential Similarly, water quality does not appear to be a factor in stranding potential in the study reach. Turbidity measurements reported in YCWA s relicensing Technical Memorandum 2-3, Water Quality, was 0.0 NTU. Numerous studies have documented that salmonid stranding due to rapid flow fluctuations is greatest when streambed gradients are less than five percent (Clarke et al. 2008; Hunter 1992; Olson 1990). Of the seven transect locations selected for intensive topographical survey, one transect - R3 - had a potential stranding zone gradient of 4.9 percent, though no stranding was documented at that location. All other transect locations were over five percent. In the reach downstream of New Colgate Powerhouse, isolated pools and potholes along the stream margins that are created during dewatering events appear to influence stranding potential more than low gradient gravel or cobble bars. These areas remain wetted with enough depth to keep young fish from swimming toward the main channel. Bradford (1996) reported considerable numbers of fry and juvenile salmonids in isolated water pockets as flows were reduced, even at low rates of change. The three stranding zones identified in this study were characterized by large boulder and cobble substrates, though Stranding Zone A contained a significant amount of sand in the interstitial zones between boulders. The substrate characteristics at each of these stranding locations are consistent with findings from studies that documented increased salmonid stranding in boulder and cobble substrate when compared to gravel substrate (Clarke et al. 2008; Pacificorp 2004). The survivability of young rainbow trout in residual backwater pools, potholes and depressions is highly variable and dependent on factors such as the duration of stranding, residual water volume, substrate permeability and the rate of water loss, water temperature changes exceeding lethal thresholds, oxygen depletion, and predation. Downstream of Narrows 2 Powerhouse Two fish stranding studies have occurred downstream of Narrows 2 Powerhouse, each of which is discussed below. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

78 YCWA s Fish Stranding Study In 2013, YCWA conducted an assessment of the relationship between shutdowns 19 of the Partial Bypass and fish stranding (Study 7.13). The relationship between shutdowns of the Partial Bypass and fish stranding was assessed by conducting fish stranding surveys to document the occurrence and condition of any fish found stranded after shutdowns of the Partial Bypass, visual observation events (or visual observations) of fish from the Narrows 2 Powerhouse deck before and after shutdowns of the Partial Bypass, 20 summarizing historical and current operations of the Partial Bypass, and summarizing incidental observations. 21 From October 1, 2006 (the Narrows 2 Full Bypass went into operation in January 2007) to December 15, 2013, the Partial Bypass was used 23 times, ranging from less than 1 day up to 37 days of continual use. The Partial Bypass was used most often in January, February, and September. Discharge from the Partial Bypass was normally less than 230 cfs, but was as high as 612 cfs. The existing FERC license, and other permits and licenses, do not include any restrictions, including ramping, regarding how YCWA operates the Partial Bypass, as long as instream flow and flow fluctuation requirements of the FERC license are met at the USGS streamflow gage at Smartsville and Marysville gages, downstream of PG&E s Narrows 1 Powerhouse. Over the course of the study period, operational changes that led to shutdowns of the Partial Bypass occurred twice, once on September 8, 2013 and again on October 7, Both involved transfers of flows from the Partial Bypass to the Full Bypass. During both events, the Narrows 1 Powerhouse operated at approximately 680 cfs. The operational conditions at the Partial Bypass varied from about 30 cfs during Event 1, to just over 200 cfs during Event 2. Fish stranding surveys were conducted immediately after operation of the Partial Bypass ceased. Surveys were conducted along the right bank as oriented downstream. No fish carcasses or stranded live fish were observed during the field surveys following operational changes. During the September 8, 2013 event, visual observations events from the powerhouse deck resulted in a total of 111 observations, of which 99 were of Chinook salmon and 12 were of fish that could not be identified. All of the fish observations occurred after the Partial Bypass was shut down. Observations of fish occurred as close as 15 ft and as far as 170 ft from the Narrows 2 Powerhouse, however, the majority of observations were made of fish circling between 50 and 150 ft downstream of the powerhouse. Observations during the October 7, 2013 event resulted in a total of 30 observations consisting of observations of 20 Chinook salmon and 10 fish that 19 A shutdown refers to a facility going from some level of operations to no operations. Shutdowns may be planned (i.e., scheduled with some advanced planning) or forced or unplanned (i.e., results from an emergency, such as equipment failure). 20 A visual observation event (also referred to as a visual observation) refers to YCWA s survey by one or more persons of the Yuba River surface in the vicinity of the Narrows 2 Powerhouse taken from the Narrows 2 Powerhouse deck at least 20 minutes prior to performing a fish stranding survey and at least 20 minutes after performing a fish stranding survey. No equipment is needed to perform a visual observation. Visual observation events are required by Study An incidental observation refers to a note by a person, normally during performance of a study. The observation is not the result of a survey, and taken only in passing. While Study 7.13 provided YCWA would report all incidental observations, the Study did not require YCWA to make any incidental observations. Exh. E - Environmental Report Application for New License April 2014 Page E ,

79 could not be identified. All but one of the observations occurred after an operational event. 22 The majority of fish observations occurred within 50 ft of the Narrows 2 Powerhouse, as fish swam into or out of the Full Bypass Pool, however, observations were made as far as 250 ft downstream of the Narrows 2 Powerhouse. Incidental Observations YCWA is aware of four salmon incidental observations that may be related to stranding in the Yuba River in the vicinity of the Narrows 2 Development facilities. Each of these is discussed below. YCWA staff and its relicensing consultants have not observed any other fish carcasses or live fish on stream banks in the vicinity of the Narrows 2 Powerhouse, nor has any Relicensing Participant provided to YCWA any other documented occurrences of fish carcasses or live fish on stream banks in the vicinity of the Narrows 2 Powerhouse. October 23, 2012 Incidental Observation YCWA staff observed a fish carcass on October 23, 2012 on the bank south of Narrows 2 Powerhouse (Figure ). No additional information about the species, time, condition of the fish, or its cause of death or exact location is available. Figure General location of the fish carcass observed by YCWA Operations staff on October 23, 2012 in relation to the Narrows 2 Powerhouse and Englebright Dam (yellow dot). 22 An operational event, is a change in flow of more than 400 cfs, as defined in Study 7.11, Fish Behavior and Hydraulics Near Narrows 2 Powerhouse and Radio Telemetry Study of Spring- and Fall-Run Chinook Migratory Behavior Downstream of Narrows 2 Powerhouse. An operational event includes shutdowns, and like shutdowns, an operational event may be planned (i.e., scheduled with some advanced planning) or forced or unplanned (i.e., results from an emergency, such as equipment failure). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

80 Operational changes did not occur within 24 hours of the observation (Figure ). The Full Bypass was operating before and after the observation at approximately 375 cfs and was the only point of discharge at Narrows 2 Powerhouse, while the Narrows 1 Powerhouse operated near 625 cfs. Discharge at the Smartsville Gage was approximately 1,000 cfs during this period. 1,200 1,000 Discharge (cfs) /22 12:00 Time of observation unknown 10/22 16:00 10/22 20:00 10/23 00:00 10/23 04:00 10/23 08:00 10/23 12:00 10/23 16:00 10/23 20:00 10/24 00:00 10/24 04:00 10/24 08:00 Narrows 1 Narrows 2 Partial Bypass Full Bypass Smartville Gage 10/24 12:00 Figure Fifteen-minute flows data at the Full Bypass, Narrows 1 Powerhouse, and Smartsville Gage from 12:00 p.m. on October 22, 2012 to 12:00 p.m. on October 24, The Narrows 2 Powerhouse and the Partial Bypass did not operate during this period, and spills over Englebright Dam did not occur. October 25, 2012 Incidental Observation During a Relicensing Participant field event on October 25, 2012, Cal Fish and Wildlife personnel found an adult Chinook salmon carcass head down in a crevice on the right bank about 70 ft downstream of the Narrows 2 Powerhouse (Figure ). When found, the fish was about 3 to 5 ft above the river water surface and 15 ft from the water s edge. The fish, identified as a female that was still gravid, measured 88.9 cm FL and weighed 7.39 kg and had a girth of 43.1 cm (S. Hoobler, pers. comm., 2014). The carcass was relatively fresh and had a silver/blue color. The adipose fin was not clipped (Figure ). The carcass was removed from the site by Cal Fish and Wildlife staff. 23 In this figure, Narrows 1 Powerhouse and Smartsville Gage data are from PG&E, and the Full Bypass data are based on flow data in the Narrows 2 Penstock AVM and YCWA operator s log books. Exh. E - Environmental Report Application for New License April 2014 Page E ,

81 Figure Sean Hoobler of Cal Fish and Wildlife holding an adult Chinook salmon carcass found in the crevice he is kneeling in on October 25, Photo taken by John Wooster of NMFS. The carcass was discovered around 12:30 p.m., about 30 minutes after an operational change from the Partial Bypass to the Full Bypass. Discharge from the Narrows 2 facilities remained similar before, during, and after the operational change (Figure ). The Smartsville Gage reported approximately 1,000 cfs during a 24-hour period before and after the operational change, with about 325 cfs from the Narrows 2 facility, and 675 cfs from the Narrows 1 Powerhouse. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

82 1,200 1,000 Discharge (cfs) /24 12:00 10/24 16:00 10/24 20:00 10/25 00:00 Approximate time of observation 10/25 04:00 10/25 08:00 10/25 12:00 Narrows 1 Narrows 2 Partial Bypass Full Bypass Smartville Gage 10/25 16:00 10/25 20:00 10/26 00:00 10/26 04:00 10/26 08:00 10/26 12:00 Figure Fifteen-minute discharge data at the Partial Bypass, Full Bypass, Narrows 1 Powerhouse, and Smartsville Gage from 12:00 p.m. on October 24, 2012 to 12:00 p.m. on October 26, The Narrows 2 Powerhouse did not operate during this period, and spills over Englebright Dam did not occur. The time the fish carcass was observed is shown. October 7, 2013 Incidental Observation YCWA issued an to Relicensing Participants advising them that increased downstream water demand would result in a flow transition at around 2:00 p.m. from the Narrows 2 Partial Bypass to the Narrows 2 Full Bypass, and that YCWA s consultant staff were mobilizing to conduct visual observations and dual frequency identification sonar (DIDSON ) imagery monitoring, as required by the FERC-approved Study 7.11 and to perform a fish stranding survey after the Partial Bypass was shut down for Study YCWA issued the notice within an hour of determining that the transition would occur. At approximately 12:15 p.m. on October 7, 2013, YCWA s consultant staff arrived at Narrows 2 Powerhouse in anticipation of performing the studies. The weather conditions were clear and sunny. 24 In this figure, Narrows 1 Powerhouse and Smartsville Gage data are from PG&E, and the Full Bypass data are based on flow data in the Narrows 2 Penstock AVM and YCWA operators log books. Exh. E - Environmental Report Application for New License April 2014 Page E ,

83 As staff prepared to perform the studies, they observed a fish carcass on the north bank of the Yuba River approximately 15 ft downstream from the face of the Narrows 2 Powerhouse (Figures A through D). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

84 A) General location of the fish carcass in relation to the Narrows 2 Powerhouse and Englebright Dam (yellow dot). B) Specific location of the fish carcass before it was handled by staff. C) Physical position of the fish carcass before it was handled by staff. D) Photograph of the fish carcass positioned by staff for the photo. Figure Series of photos cataloging the location and position of the fish carcass found on October 7, Exh. E - Environmental Report Application for New License April 2014 Page E ,

85 Staff found the carcass head first in a crevice under several angular rocks. Staff estimated that the carcass was approximately 2 ft from the water s edge and approximately 1.5 ft above the water surface. The dominant substrate at the location was bedrock and the subdominant substrate was angular cobble-sized rock. Water temperature in the river in the vicinity of the carcass was 12 C. YCWA operations staff said the discharge from the Partial Bypass was 200 cfs when staff first observed the carcass. Because the fish was dead, staff handled the carcass and determined it was a gravid female Chinook salmon, 68 cm FL, and showed no obvious signs of recent spawning activity (e.g., no signs of tail abrasion). Staff described the carcass as fresh, and reported it showed no rigor mortis, no bloating, no obvious smell of decay, and a clear eye. Staff removed the carcass and cut off the tail to be sure it would not be counted during the Study 7.13 survey. The carcass was placed in the flowing river. After the Narrows 2 Partial Bypass was shut down, staff performed the Study 7.13 survey. The Partial Bypass operated at approximately 205 cfs during the 4 hours preceding the operational change over to the Full Bypass (Figure ), which continued to operate at 231 cfs for the following 4 hours. From 24 hours before to 24 hours after the operational change, the Narrows 1 Powerhouse remained at a near-constant discharge of 675 cfs. The Smartsville Gage increased about 30 cfs after the operational change to about 940 cfs. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

86 1,200 1,000 Discharge (cfs) /06 14:00 10/06 18:00 10/06 22:00 10/07 02:00 10/07 06:00 10/07 10:00 10/07 14:00 10/07 18:00 Approximate start time of surface observations Narrows 1 Narrows 2 Partial Bypass Full Bypass Smartville Gage 10/07 22:00 10/08 02:00 10/08 06:00 10/08 10:00 10/08 14:00 Figure Fifteen-minute discharge data at the Partial Bypass, Full Bypass, Narrows 1 Powerhouse, and Smartsville Gage from 2:00 p.m. October 6, 2013 to 2:00 p.m. October 8, The Narrows 2 Powerhouse did not operate during this period, and spills over Englebright Dam did not occur. October 11, 2013 Incidental Observation YCWA issued an to Relicensing Participants advising them that changes in downstream water demand would necessitate a transition of flow around noon from the Full Bypass to Narrows 2 Powerhouse, and that YCWA s consultant staff were mobilizing to conduct visual observations and DIDSON monitoring, as required by the FERC-approved Study At approximately 11:30 a.m. on Friday, October 11, 2013, YCWA s consultant staff arrived at Narrows 2 Powerhouse in anticipation of performing visual observations and DIDSON monitoring. The weather conditions were clear and sunny. As part of the change, flow through the Narrows 2 Full Bypass was increased from 400 cfs to 990 cfs. The increased flow inundated a gravel bar on the southern edge of the river between the Full Bypass pool and the main channel of the river. Then, over the next 5 minutes, flow was changed from the Full Bypass to the Narrows 2 Powerhouse, at which point flow from the Full Bypass ceased completely. YCWA s consultant staff observed that the change-over had left a pool, approximately 30 ft by 10 ft wide, on the edge of the gravel bar (Figure A through D). 25 In this figure, Narrows 1 Powerhouse and Smartsville Gage data are from PG&E, and the Full and Partial bypasses data are based on flow data in the Narrows 2 Penstock AVM and YCWA operators log books. Exh. E - Environmental Report Application for New License April 2014 Page E ,

87 A) General location of the fish observed in the pool in relation to the Narrows 2 Powerhouse and Englebright Dam (yellow dot). B) Specific location of observed fish, flow in the river was approximately 990 cfs with all water being released from the Narrows 2 Powerhouse (generation). C) The blue arrows indicate four fish that can be seen in the pool. D) Photograph of the pool when the flow in the river was approximately 990 cfs, with all water being released from the Narrows 2 Full Bypass. The area of the pool shown in photos b and c is indicated by the blue arrow. Figure Series of photos that show the pool in which the fish were observed on October 11, The photos were taken from the Narrows 2 Powerhouse deck looking south across the Yuba River. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

88 On the morning of October 10, 2013, the Full Bypass was releasing approximately 230 cfs and PG&E s Narrows 1 Powerhouse was releasing approximately 680 cfs (Figure ). Starting shortly after 1:15 p.m., releases from the Full Bypass were increased to approximately 350 cfs by 1:45 p.m., PG&E s Narrows 1 Powerhouse releases remained at approximately 680 cfs and no flow was passing through the Partial Bypass. At approximately 7:00 a.m. on October 11, 2013 flows through the Full Bypass were increased first to 400 cfs, and at 10:15 a.m. flows were further increased until they reached approximately 1,050 cfs at 10:30 a.m. Between 10:30 and 10:45 a.m., the Narrows 2 Powerhouse began generating at flows of approximately 990 cfs, releases from the Full Bypass were stopped, and releases from the Narrows 1 Powerhouse were reduced to 130 cfs. YCWA s consultant staff observed fish in the pool at approximately 12:05 p.m. on October 11, This operations mode was maintained until just after 1:00 p.m. on October 13, 2013, at which time flows through the Narrows 2 Powerhouse began to be reduced to approximately 400 cfs by 2:00 p.m. and releases from PG&E s Narrows 1 Powerhouse were increased to approximately 670 cfs. By 2:15 p.m., releases through the Narrows 2 Powerhouse were stopped, and flow through the Full Bypass had been increased to approximately 400 cfs. These releases from the Full Bypass and PG&E s Narrows 1 Powerhouse continued beyond 5:00 p.m. on October 14, When YCWA consultant staff observed the river again on October 16, no fish were observed in or near the pool. Exh. E - Environmental Report Application for New License April 2014 Page E ,

89 1,200 1,000 Discharge (cfs) Approximate time of observation 0 10/10 12:00 10/10 16:00 10/10 20:00 10/11 00:00 10/11 04:00 10/11 08:00 10/11 12:00 10/11 16:00 10/11 20:00 10/12 00:00 10/12 04:00 10/12 08:00 10/12 12:00 10/12 16:00 10/12 20:00 10/13 00:00 10/13 04:00 10/13 08:00 10/13 12:00 10/13 16:00 10/13 20:00 10/14 00:00 10/14 04:00 10/14 08:00 10/14 12:00 10/14 16:00 Narrows 1 Narrows 2 Partial Bypass Full Bypass Smartville Gage Figure Fifteen-minute discharge data at the Narrows 2 Powerhouse, Full Bypass, Narrows 1 Powerhouse, and Smartsville Gage from 12:00 p.m. October 10, 2013 to 12:00 p.m. October 14, The Partial Bypass did not operate during this period, and Englebright Dam did not spill. The time the fish were observed in the pool is shown. Lower Yuba River Redd Dewatering and Fry Stranding Study The second fish stranding study was (ICF/JAS 2012), which was conducted in April 2007 to evaluate bar and off-channel stranding of juvenile salmonids associated with a flow reduction of 1, cfs at Smartsville at a ramping rate of 100 cfs per hour. Bar stranding was again evaluated in June with a temporary flow reduction of 1,600-1,300 cfs at a rate of 100 cfs per hour. Snorkel surveys were conducted between Rose Bar, located about 2.5 mi downstream of Englebright Dam, and the Highway 20 Bridge, located about 5.7 miles downstream of Englebright Dam. During the April 5, 2007 drawdown, field crews observed eight stranded salmon fry in the interstitial spaces of substrates on bar slopes (perpendicular to shoreline) ranging from 0.5 to 5.5 percent in slope. No stranded fish were observed during surveys conducted on June 18, The presence of both juvenile Chinook salmon and O. mykiss were confirmed in shallow, nearshore areas adjacent to the study sites, suggesting that the risk of bar stranding is greatly reduced by June. Following the April 5, 2007 flow reductions, juvenile salmon were found in 16 of the 24 disconnected off-channel sites (ICF/JSA 2012). Most of the fish that had become isolated in 26 In this figure, Narrows 1 Powerhouse and Smartsville Gage data are from PG&E, and the Full Bypass and Narrows 2 Powerhouse data are based on flow data in the Narrows 2 Penstock AVM, powerhouse generation records and YCWA operators log books. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

90 off-channel sites were mm fry. Out of the 16 sites where isolation of fry was observed, 70 percent of the fish were found in the four largest sites, which accounted for nearly 60 percent of the total wetted area that had become disconnected from the main river. According to ICF/JSA (2012), these four sites were unique in that they were all associated with man-made features within or adjacent to the main river channel (e.g., diversion channels, ponds and bridge piers). An updated Lower Yuba River Redd Dewatering and Fry Stranding Study was subsequently conducted from May 29, 2008 through June 4, 2008, with a scheduled flow reduction on June 1, A total of seven stranded trout fry ranging between mm were observed in the interstitial spaces of substrates on bar slopes ranging from 2.0 to 5.7 percent in slope. Juvenile salmon were found isolated in seven of the 12 off-channel sites that had become disconnected from the main river by the June 1, 2008 event. One site accounted for only about 7 percent of the total wetted area that had been disconnected from the main river, but nearly 80 percent of the total number of juvenile salmon that had been isolated by the June 1, 2008 event. A total of 13 steelhead fry were found isolated in two of the 12 off-channel sites that had become disconnected from the main river by the June 1, 2008 event. Nearly all of these fish were mm fry that had been isolated in a single backwater pool adjacent to the main river in the Timbuctoo Reach (ICF/JSA 2012) JSA (2008) suggested that the preliminary findings indicated that juvenile O. mykiss fry may be less vulnerable to off-channel stranding than juvenile Chinook salmon because of their more restricted distribution and inability to access off-channel areas under late spring flow conditions. Long-term monitoring of several isolated off-channel sites confirmed that some sites can support juvenile salmonids for long periods and even produce favorable summer rearing conditions. A 2010 study was conducted from June 21, 2010 through July 1, 2010, with a scheduled flow reduction between June 28 and 30 from approximately 4,000 cfs to 3,200 cfs as measured at the Smartsville Gage. As reported by ICF/JSA (2010), fish stranding surveys were conducted on June 21, 22, and 23 to identify potential stranding areas and document habitat conditions and fish presence before the flow reduction, and were repeated on June 29, June 30, and July 1 to document the incidence of fish stranding and habitat conditions after the flow reduction. After the June flow reduction, six juvenile salmon and 46 juvenile trout was observed in seven of the 26 off-channel sites that had become fully or nearly disconnected ( 0.1 foot deep) from the main river. Most of the stranded fish were juvenile trout mm in length that had become isolated in five off-channel sites above Daguerre Point Dam. Below Daguerre Point Dam, observations of stranded fish were limited to six juvenile salmon and two juvenile trout at two study sites (ICF/JSA 2010). Hydrologic and operating conditions in January and February 2011 provided the first opportunity to evaluate the effect of a winter flow reduction on the incidence of bar stranding. A series of three successive flow reductions were evaluated. Following a three week period of relatively stable flows, Englebright Dam releases were reduced from 3,000 to 2,600 cfs on January 31, from 2,600 to 2,200 cfs on February 7, and from 2,200 to 2,000 cfs on February 11. Exh. E - Environmental Report Application for New License April 2014 Page E ,

91 The first event was a 400 cfs flow reduction (3,000 2,600 cfs) conducted from 8:00 AM to 10:00 AM at a target rate of 200 cfs per hour on January 31, This event resulted in a 2.1- to 2.5- in. drop in water surface elevation and a rate of change of 0.6 to 0.8 in. per hour at the three study sites. Field crews searched 764 sq ft of dewatered shoreline and found 20 stranded salmon fry (30 to 40 mm long), and six stranded steelhead (50 to 90 mm long) (ICF/JSA 2012). During the second event on February 7, 2011, flows were again reduced by 400 cfs, from 2,600 to 2,200 cfs, from 8:00 AM to 10:00 AM, but at a target rate of 100 cfs per hour. This event resulted in a 1.8 to 2.1 inch drop in water surface elevation and a rate of change of 0.4 to 0.5 in. per hour at the three study sites. Field crews searched 560 sq ft of dewatered shoreline and found 10 stranded salmon fry (30 to 40 mm long) and no steelhead (ICF/JSA 2012). During the third event on February 11, 2011, flows were reduced by 200 cfs (2,200 to 2,000 cfs) from 2:00 AM to 4:00 AM at a target rate of 100 cfs per hour. This event resulted in a 0.8 to 1.3 in. drop in water surface elevation and a rate of change of 0.4 to 0.7 in. per hour at the three study sites. Field crews searched 248 sq ft of dewatered shoreline and found four stranded salmon fry (30 to 40-mm-long) and no steelhead (ICF/JSA 2012) Daguerre Fish Facilities In 2012, in accordance with the FERC-approved Study 7.12, YCWA performed an assessment of the potential effects of the Project on the functionality and performance of fish facilities on the Yuba River near Daguerre Point Dam. The results of the study are provided below. The Fish Facilities These facilities include: 1) the fish ladders associated with the USACE s Daguerre Point Dam; 2) the Hallwood-Cordua Diversion and fish screen; 3) the South Yuba-Brophy Diversion and rock gabion fish exclusion barrier; and 4) the Browns Valley Irrigation District (BVID) Diversion and fish screen. These four facilities are collectively referred to as the fish facilities, and are described below. Daguerre Point Dam and Associated Fish Ladders The California Debris Commission began construction of the original Daguerre Point Dam in 1904 as part of the Yuba River Debris Control Project (USACE 2001). Dam construction was completed in May 1906, but the Yuba River did not flow over the dam until 1910, when the location of river channel was changed (USACE 2007). Figures and provide aerial views of Daguerre Point Dam and associated fish ladders. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

92 Figure Daguerre Point Dam and associated north and south fish ladders. The South Yuba-Brophy District is seen in the upper left corner of the photograph. Figure The Daguerre Point Dam north (on left) and south (on right) fish ladders. The current configuration of Daguerre Point Dam is a reinforced, overflow concrete ogee ( sshaped ) spillway with concrete apron and concrete abutments. The ogee spillway section is 575 ft wide and 25 ft tall (USACE 1966, NMFS 2007 and 2012). Due to full sedimentation of the space behind the dam shortly after construction, the dam does not hold any storage and the dam has no low level outlets or spill gates. Therefore, there are no operations for storage or flow at the dam. Exh. E - Environmental Report Application for New License April 2014 Page E ,

93 Currently, the dam has two fish ladders that were constructed by USACE and Cal Fish and Wildlife. Each ladder has a control gate at the upstream exit of the ladder. The ladders are composed of a combination of 8 ft by 10 ft and 6 ft by 10 ft concrete bays on either side of the dam with 1 ft steps (USACE 1966). The ladders were designed for salmonid fish passage and are monitored with infrared VAKI Riverwatcher scanners year-round. The ladders have a hydraulic capacity that is estimated to be 6 cfs per ladder (USACE 2001). However, according to USACE operators of the fish ladders, the capacity of each ladder actually is closer to 15 cfs to 25 cfs per ladder, depending upon the forebay water surface elevation. USACE s Daguerre Point Dam Operations and Maintenance Manual requires that the fish ladders be physically closed when water elevations reach 130 ft at a local onsite staff gage, which corresponds to river flows of slightly less than 10,000 cfs (USACE 1966, SWRCB 2003). Once closed, the ladders are kept closed until the water elevation recedes to 127 ft, at which point USACE re-opens the ladders (USACE 1966, CALFED and YCWA 2005). However, USACE is collaborating with resource agencies to improve salmonid fish passage and current operational practices, and to keep the ladders open at water elevations near 130 ft. Management of the existing fish ladders is coordinated by several parties. Cal Fish and Wildlife has removed large woody material that may clog the ladders, and sometimes adjusts flashboards in the lowest bay to improve attraction flows. USACE operates the gates, and clears sediment at the tops of and exits from the fish ladders. Anadromous salmonid passage at Daguerre Point Dam can occur year-round because either adults are passing upstream or juveniles are passing downstream throughout the year. For example, adult spring-run Chinook salmon immigration and holding extends from April through September, adult fall-run Chinook salmon immigration occurs from July through December, and most juvenile Chinook salmon, including spring-run and fall-run Chinook salmon, emigration occurs from late-december through late-april. Adult fish passage is potentially impaired when rain or snowmelt runoff produces high flow conditions at the dam, which may be during the same time periods that spring-run Chinook salmon and steelhead are attempting to migrate upstream to spawning areas in the Yuba River. The 2007 NMFS Biological Opinion for Daguerre Point Dam (NMFS 2007) stated that when high flow conditions occur during winter and spring, adult spring-run Chinook salmon and steelhead can experience difficulty in finding the entrances to the ladders because of the relatively low amount of attraction flows exiting the fish ladders, compared to the magnitude of the sheet-flow spilling over the top of Daguerre Point Dam. In addition, NMFS s 2007 Biological Opinion (NMFS 2007) stated that the angles of the fish ladder entrance orifices and their proximities to the plunge pool increase the difficulty for fish to find the entrances to the ladders In addition to problems with adult salmonid passage, the ladders are not capable of passing the adult sturgeon (i.e., presumably green sturgeon) that occasionally migrate to the base of the dam (Cramer Fish Sciences 2011). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

94 In addition, flooding causes periodic obstruction of the ladders by LWM and sediment deposition around the ladder entrances, exits and ladder bays. The USACE has installed a log boom at the exit of the north ladder and implemented a sediment management program since 2003 to minimize obstructions to fish passage. Upstream passage at Daguerre Point Dam can potentially be adversely impacted when sediment builds up near the upstream exits of the fish ladders. When gravel builds up on the upstream side of the dam, it can impede flows into the ladders, thereby reducing the ability of fish to climb the ladders and reducing the attraction flows coming out at the base of the ladders. In addition, the gravel bars could potentially build up to the point where they could reduce access to the main channel for fish that have exited the ladders and are attempting to continue their upstream migration. Ongoing maintenance removes sediment from the forebay side of the fish ladders (USACE 2009). The USACE (2001) stated that juvenile fish passage is impeded at Daguerre Point Dam. It identified four potential issues: 1) unsuitable habitat due to pool habitat created by the dam; 2) injury or disorientation to fish passing over the dam face; 3) potential injury or entrainment to fish at diversion canals; and 4) impeded passage at low river flows. Specific studies identifying the success of migration pathways over the dam or through the fish ladders were not identified. The passage of juvenile fish over Daguerre Point Dam was identified by USACE, CALFED Bay-Delta Program (CALFED) and YCWA (CALFED; YCWA 2005) to potentially disorient or injure fish, but the USACE discussed the shape of the dam as the primary factor affecting that possible issue. Low river flow conditions at Daguerre Point Dam were mentioned by the USACE as a possible issue for juvenile emigration over the dam. The USACE did not define what range of river flows were considered to be low flow conditions or the potential issues created by such low flows. Issues associated with low river flows could include longer migration times, increased water temperatures, and increased exposure to predators; however, most of these issues relate directly to the physical arrangement of facilities and the resulting habitat created by Daguerre Point Dam. The magnitudes of releases from Narrows 2 Development facilities reaching Daguerre Point Dam are directly affected by available upstream storage and Yuba Accord minimum streamflow requirements, which are measured at the Smartsville Gage upstream and downstream of Daguerre Point Dam, and must be maintained regardless of agricultural diversion rates. In addition, these flows were designed to maintain optimum water temperatures in most years for key salmonid lifestages during the hotter seasons, so water temperatures due to Project operations would not be expected to affect the ability of salmonids to navigate the Daguerre Point Dam fish ladders. Exh. E - Environmental Report Application for New License April 2014 Page E ,

95 Overall, the findings from existing data indicate that Project operations (i.e., normal Discretionary Releases 28 ) do not affect the Daguerre Point Dam fish ladders operations within their design capability. Project Discretionary Releases have on very rare occasions exceeded 10,000 cfs (for New Bullards Bar flood pool control), and the USACE shuts down the ladders when river flows exceed this rate, but these instances were preceded or followed by river flows well in excess of 10,000 cfs, which are outside of the discretion of the Project and required the USACE to shut down the ladders anyway. Hallwood-Cordua Diversion and Fish Screen The Hallwood-Cordua Diversion, a gravity flow diversion facility located on the north bank of the Yuba River upstream of Daguerre Point Dam, has a diversion capacity of 625 cfs (SWRCB 2001). At the headworks of the diversion, gate valves allow water to flow into the intake channel. Water then flows a distance of approximately 1,500 ft to the fish screen facility. At the screen, water levels are manually controlled year round by board weirs. Minimum water levels are maintained to ensure conditions are adequate for any user to divert water when needed (SWRI et al. 2000). Although water elevations in these primary conveyances remain relatively constant, the flow rates through the conveyances may change with changes in agricultural demands. In 2001, the modified original fish screen was replaced with a flat-plate stainless steel fish screen designed in collaboration with Cal Fish and Wildlife and NMFS that more closely conformed to Cal Fish and Wildlife s and NMFS fish screening criteria (Figure ). The screen is at the same location as the original screen and has a fish collection system, appropriate-sized openings and sweeping and approach velocities to facilitate direct return of screened fish back to the river below Daguerre Point Dam (NMFS 2007). Exact dimensions and design were not available to YCWA, but Cal Fish and Wildlife has inspected the screen, and NMFS annually inspects it, and, to date, has approved operation of the screen (Barton 2011). The diversion channel was also inspected and approved by both agencies for operation. 28 Discretionary Releases are Project releases that are made for power generation, agricultural diversions at or near Daguerre Point Dam, supplemental instream flows for fisheries purposes and water transfers to other entities, and releases that are not specifically required by any regulatory requirements, but are made in anticipation of the need for an imminent Non- Discretionary release, such as releases made in anticipation of water storage in New Bullards Bar Reservoir entering the flood reservation space. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

96 Figure Hallwood-Cordua Diversion. Image on the left shows the control gate headworks on the north abutment of Daguerre Point Dam. Image on the right shows the current v-shaped screen. The fish screen is operated during the entire diversion season (NMFS 2002). High spill flow events over Daguerre Point Dam previously posed an issue for the diversion because there was overtopping into the diversion channel; however, now flow is controlled by both the headwork gates and flashboards that can be installed by CID during periods when overtopping may occur. Spills from Englebright Dam historically have led to river flows that overtopped the diversion gates and sent fish into the diversion channel resulting in fish entrainment and mortality. Now flashboards are installed near the headgates during Englebright Dam spill events to redirect very high river flows and prevent overtopping of the diversion gates. Also, the river flows during overtopping events were caused by spills at Englebright Dam that greatly exceeded the Discretionary Release capacity of the Project. The history of modifications associated with the Hallwood-Cordua Diversion is extensive. These updates were all found to be specifically associated with the design and operation of the diversion, unrelated to the operation of the Project. Revisions to the diversion and its operation over time have resulted in the facility appearing to be in a functional state throughout the Discretionary Release capacity of the Project based on existing information. Overall, the findings from existing data indicate that Project operations do not influence the efficiency or function of this diversion or fish screen. South Yuba-Brophy Diversion and Fish Exclusion Barrier The South Yuba-Brophy Irrigation Diversion is located approximately 1,000 ft upstream of Daguerre Point Dam on the south side of the river. The diversion headworks consist of an intake channel and bypass channel, a porous 450-ft long rock gabion fish screen fitted with a fine-mesh barrier within the gabion (USACE 2001), a diversion pond, which is approximately 1-ac in size, and an irrigation canal (Figure ). The 450 ft rock gabion is 30 ft wide at its base, narrowing to 10 ft wide at the top. Water flows from the river into the small side channel, where Exh. E - Environmental Report Application for New License April 2014 Page E ,

97 it either is diverted through the gabion or flows through the channel back into the river mainstem. Water entering the diversion pool percolates through the porous cobble-sized rock and flows through mesh. Water can be released from the diversion pond into the main irrigation canal through any of three 5-ft diameter pipes, which are located at the south end of the pond and are regulated by a gate at the head of each pipe. The pipes extend approximately 600 ft underground to the first pond in the Yuba Goldfields, part of the irrigation canal system. Figure The South Yuba-Brophy Diversion. The image on the left shows the general location of the diversion (center of picture) relative to Daguerre Point Dam. The image on the right shows an aerial view of the bypass channel, rock gabion, and diversion pool. Fisheries agencies have questioned the effectiveness of the rock gabion at excluding fish (CDFG 1988). High predation rates within the channel and forebay were also identified as an issue (USFWS 1989). On other occasions, fishery biologists have captured juvenile salmonids that were entrained behind the gabion, having passed either through the gabion or over the top of the gabion during high flows (USFWS 1990, Demko and Cramer 1993). River flows exceeding 20,000 cfs are expected to result in the overtopping of the gabion (USFWS 1990). The study findings indicate that the South Yuba-Brophy Diversion does exclude fish, but may have areas requiring improvement that are not related to Project operations. The irregular flows at the exclusion barrier and potentially low sweeping flows are caused by the gabion s rock composition and the bypass channel configuration. River flows that are sufficiently large to overtop the barrier are infrequent and are more than five times greater than the normal Discretionary Releases of the Project. Overall, the evidence does not suggest that the Project operations affect the performance of this barrier. Browns Valley Irrigation Diversion and Fish Screen BVID maintains a screened diversion upstream of the other Daguerre Point Dam diversion facilities (USACE 2001). The facility is located on a small channel that runs parallel to the main channel and rejoins it after approximately 4,000 ft. The facility is composed of a fish screen, a diversion lagoon, and a pumping station. The diversion lagoon is approximately 250 ft long by 70 ft wide (Figure ; BVID 2011, 2012). The facility is rated for diverting up to 65 cfs and BVID may divert up to 9,500 ac-ft per year of water during the months of April to August. The fish screen was installed and became operational in April April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

98 Figure Browns Valley Diversion. Image shows the screen and diversion forebay. The screen is composed of fish screen frames and panels, six vertical approach-velocity control flow baffles, and a screen cleaning system (sweeper arm; BVID 2011, 2012). The fish screen frames consist of a 1/8-in. thick stainless steel plate that occupies approximately the top section of the frame and a profile bar screen panel made of stainless steel wedge wire that measures about 81 in by 51 in and occupies approximately the bottom section of the frame. The fish screen panels have slotted openings approximately 1.75 mm wide. The openings in each screen panel comprise approximately 43 percent of each screen's surface. Ten fish screen frames slide into guide rails on the diversion-channel side of the fish screen structure and are held in place by gravity. The sweeper arm, consisting of two screen brushes, two brush trolleys mounted on a track system, and a motor to drive the trolleys, provides continuous cleaning. On July 29, 1999, a crew of engineers from NMFS, USDOI, Bureau of Reclamation, and SWRCB adjusted the fish screen baffles at the facility to achieve acceptable and relatively uniform approach velocities (BVID 2011). The team was able to set an acceptable and uniform approach velocity (approximately 0.33 feet per second [fps]) across the face of the entire set of fish screen panels. The fish screen also meets NMFS and Cal Fish and Wildlife s criteria for submerged screen area: the screen area must be at least equal to the quotient of the allowed maximum diversion rate associated with the screen (i.e., 65 cfs), divided by the allowed maximum approach velocity of the water entering the screen (i.e., 0.33 fps). The quotient in this case, 65 cfs divided by 0.33 fps, is sq ft. This is the minimum required submerged fish screen area. The ten fish screens, with the dimensions stated above, contain sq ft of area. The entirety of each fish screen panel is submerged when flow in the Yuba River is at or above 500 cfs, the minimum flow required for BVID to make its maximum diversion of 65 cfs. The barrier on top of the screen protects the screen from overtopping at higher river flows. Exh. E - Environmental Report Application for New License April 2014 Page E ,

99 In August of 1999, a NMFS dive team inspected the fish screen structure and reported to BVID that the structure was a fine structure that promises to provide fish protection for many years (BVID 2011). Given the modern screen design, Cal Fish and Wildlife and NMFS approval of the diversion, and the absence of reports identifying any known issues, it does not appear that Project operations affect the performance of this screen Narrows 2 Powerhouse Intake In 2012, in accordance with the FERC-approved Study 7.2, YCWA assessed whether the existing Narrows 2 Powerhouse intake was adequate to provide suitable water temperatures for anadromous fish downstream of the Narrows 2 Development facilities. YCWA concluded the existing intake was adequate based on the results of the RMT s November 2010 Lower Yuba River Water Temperature Objectives Technical Memorandum (RMT 2010), and the RMT's addendum to that memorandum (RMT 2013). The RMT s 2010 Tech Memo used available data and information to review the appropriateness of the water temperature regime in the Yuba River associated with implementation of the Yuba Accord, and addressed the issue regarding the potential that cold water conditions could affect adult spring-run Chinook salmon immigration and holding, and the issue of O. mykiss anadromy versus residency. The RMT concluded that implementation of the Yuba Accord provided a suitable thermal regime for these target species and life stages, and it did not recommend Project operational or infrastructure modifications. The RMT amended its 2010 Tech Memo in 2013 using updated lifestage periodicities, water temperature index values, water temperature monitoring data, and modeling. The 2013 addendum, like the 2010 Tech Memo, concluded that implementation of the Yuba Accord provides a suitable thermal regime for anadromous fish. The RMT did not recommend any Project operational or infrastructure modifications, including modifications to the Narrows 2 Powerhouse Intake Fish Habitat Versus Flow Relationships Upstream of Englebright Reservoir In 2011, 2012 and early 2013, YCWA conducted instream flow studies in six study reaches, which totaled 25.9 mi. One reach was divided into two sub-reaches. The reaches include all river segments downstream of Project facilities and upstream of Englebright Reservoir. Eleven study sites were identified in the six reaches, and between seven and 21 transects were placed in each site for a total of 132 transects. The study estimated the habitat index versus flow relationships (Weighted Useable Area, or WUA) using the Physical Habitat Simulation (PHABSIM) system and used WUA relationships and the hydrologic record to develop habitat duration, or time series, analyses of fish habitat over time under existing (With-Project Hydrology). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

100 Using PHABSIM, flow-habitat relationships were developed for four target fish species and seven life stages: spawning, juvenile and adult life stages of rainbow trout; and juvenile and adult life stages of hardhead, Sacramento pikeminnow and Sacramento sucker. Habitat suitability criteria (HSC) developed for rivers in NID s Yuba-Bear Hydroelectric Project and PG&E s Drum-Spaulding Project relicensings were used for the target species. Static WUA WUA was calculated for the seven PHABSIM reaches or sub-reaches. Resulting WUA tables and figures present the relationship between discharge and the availability of suitable habitat for target species in terms of square feet per 1,000 linear ft of stream. WUA values are not total area by sub-reach, nor do they account for the potential habitat limiting influence of other physical factors, such as water temperature on habitat suitability. Tabular WUA results from each of the seven study reaches are provided in Tables through with corresponding graphical WUA output, presented in Figures though Exh. E - Environmental Report Application for New License April 2014 Page E ,

101 Table WUA table for rainbow trout in the Our House Diversion Dam Reach. Rainbow Trout Discharge (cfs) Spawning Juvenile Adult 22 1,968 19,838 8, ,198 20,952 11, ,377 21,513 13, ,503 21,560 15, ,600 21,285 16, ,695 20,920 17, ,757 20,534 17, ,788 20,088 18, ,776 19,628 18, ,737 18,709 18, ,674 17,881 18, ,630 17,124 18, ,591 16,409 18, ,554 15,802 17, ,490 15,276 17, ,419 14,826 16, ,358 14,448 16, ,293 14,141 16, ,223 13,874 15, ,146 13,641 15, ,070 13,424 15, ,000 13,242 15, ,939 13,092 14, ,890 12,948 14, ,792 12,707 14, ,696 12,579 13, ,573 12,446 13, ,466 12,378 13, ,386 12,275 13, ,305 12,135 13,016 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Our House Diversion Dam Reach. Rainbow Trout % Discharge (cfs) Spawning Juvenile Adult 22 71% 92% 46% 30 79% 97% 59% 40 85% 100% 71% 50 90% 100% 81% 60 93% 99% 87% 70 97% 97% 92% 80 99% 95% 95% % 93% 97% % 91% 99% % 87% 100% % 83% 100% % 79% 99% % 76% 97% % 73% 94% % 71% 92% % 69% 90% % 67% 88% % 66% 86% % 64% 85% % 63% 83% % 62% 82% % 61% 81% % 61% 79% % 60% 78% % 59% 75% % 58% 74% % 58% 72% % 57% 71% % 57% 70% % 56% 69% WUA per 1000 linear feet 25,000 20,000 15,000 10,000 5,000 0 Middle Yuba River - Our House Diversion Dam Reach Rainbow Trout Discharge (cfs) Spawning Juvenile Adult Figure WUA for rainbow trout in the Our House Diversion Dam Reach of the Middle Yuba River. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

102 Table WUA table for Sacramento sucker in the Our House Diversion Dam Reach. Sacramento Sucker Discharge (cfs) Juvenile Adult 22 24,212 9, ,572 11, ,845 12, ,967 13, ,793 14, ,483 14, ,108 13, ,355 13, ,357 13, ,827 13, ,887 13, ,468 13, ,248 12, ,517 12, ,908 11, ,519 11, ,364 11, ,295 12, ,140 12, ,126 12, ,873 11, ,936 11, ,977 11, ,514 11, ,112 9, ,393 9, ,470 9, ,897 10, ,555 10, ,136 10,839 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Our House Diversion Dam Reach. Sacramento Sucker % Discharge (cfs) Juvenile Adult 22 97% 70% 30 98% 80% % 91% % 94% 60 95% 100% 70 90% 99% 80 89% 97% 90 86% 96% % 96% % 98% % 95% % 93% % 88% % 88% % 83% % 82% % 84% % 85% % 86% % 85% % 83% % 81% % 78% % 78% % 70% % 70% % 68% % 71% % 71% % 77% WUA per 1000 linear feet 25,000 20,000 15,000 10,000 5,000 0 Middle Yuba River - Our House Diversion Dam Reach Sacramento Sucker Discharge (cfs) Juvenile Figure WUA for Sacramento sucker in the Our House Diversion Dam Reach of the Middle Yuba River. Adult Exh. E - Environmental Report Application for New License April 2014 Page E ,

103 Table WUA table for rainbow trout in the Oregon Creek Reach of the Middle Yuba River. Rainbow Trout Discharge (cfs) Spawning Juvenile Adult ,700 4, ,432 8, ,856 10, ,584 14, ,485 16, ,890 17, ,129 18, ,168 20,364 19, ,333 19,792 19, ,475 19,359 19, ,622 18,907 19, ,767 18,465 19, ,922 18,061 19, ,105 17,516 18, ,253 17,012 18, ,369 16,529 17, ,474 16,119 17, ,591 15,756 17, ,702 15,440 16, ,776 15,199 16, ,800 14,986 15, ,776 14,532 15, ,636 14,163 14, ,477 13,920 13, ,368 13,716 13, ,232 13,562 13, ,150 13,456 12, ,135 13,367 12, ,151 13,295 12, ,181 13,201 12,503 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Oregon Creek Reach of the Middle Yuba River. Rainbow Trout % Discharge (cfs) Spawning Juvenile Adult 13 4% 78% 24% 22 9% 90% 41% 31 12% 97% 56% 46 18% 100% 73% 60 24% 100% 84% 74 29% 97% 92% 89 35% 94% 96% % 90% 98% % 88% 100% % 86% 100% % 84% 100% % 82% 99% % 80% 98% % 78% 96% % 75% 94% % 73% 92% % 71% 89% % 70% 87% % 68% 85% % 67% 83% % 66% 81% % 64% 77% % 63% 74% % 62% 71% % 61% 69% % 60% 67% % 60% 66% % 59% 65% % 59% 64% % 58% 64% WUA per 1000 linear feet 30,000 25,000 20,000 15,000 10,000 5,000 0 Middle Yuba River - Oregon Creek Reach Rainbow Trout Discharge (cfs) Spawning Juvenile Adult Figure WUA for rainbow trout in the Oregon Creek Reach of the Middle Yuba River. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

104 Table WUA table for Sacramento sucker in the Oregon Creek Reach of the Middle Yuba River. Sacramento Sucker Discharge (cfs) Juvenile Adult 13 22,336 12, ,727 13, ,871 15, ,533 17, ,318 19, ,073 20, ,446 20, ,069 21, ,316 19, ,106 19, ,837 18, ,094 18, ,640 17, ,559 16, ,592 16, ,939 14, ,687 13, ,479 14, ,206 14, ,964 13, ,943 13, ,345 13, ,266 12, ,335 12, ,183 12, ,876 12, ,470 12, ,495 12, ,743 12, ,544 12,045 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Oregon Creek Reach of the Middle Yuba River. Sacramento Sucker % Discharge (cfs) Juvenile Adult 13 83% 58% 22 96% 67% % 73% 46 99% 83% 60 94% 92% 74 90% 98% 89 87% 98% % 100% % 94% % 92% % 88% % 88% % 85% % 80% % 77% % 70% % 66% % 68% % 67% % 65% % 63% % 63% % 60% % 59% % 58% % 60% % 58% % 58% % 58% % 57% WUA per 1000 linear feet 30,000 25,000 20,000 15,000 10,000 5,000 0 Middle Yuba River - Oregon Creek Reach Sacramento Sucker Discharge (cfs) Juvenile Adult Figure WUA for Sacramento sucker in the Oregon Creek Reach of the Middle Yuba River. Exh. E - Environmental Report Application for New License April 2014 Page E ,

105 Table WUA table for rainbow trout in the Log Cabin Diversion Dam sub-reach of Oregon Creek. Rainbow Trout Discharge (cfs) Spawning Juvenile Adult 5 1,420 10,596 9, ,848 11,314 10, ,379 11,941 11, ,687 12,155 12, ,056 12,283 12, ,255 12,320 12, ,480 12,253 13, ,747 12,085 13, ,928 11,894 13, ,042 11,683 13, ,107 11,451 13, ,148 11,239 12, ,175 11,031 12, ,189 10,825 12, ,181 10,631 12, ,148 10,457 12, ,093 10,293 12, ,026 10,138 12, ,953 9,997 11, ,788 9,741 11, ,613 9,527 11, ,435 9,349 11, ,081 9,025 10, ,771 8,761 10, ,557 8,531 10, ,392 8,319 10, ,288 8,171 10, ,246 8,035 9, ,230 7,899 9, ,228 7,766 9,649 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Log Cabin Diversion Dam sub-reach of Oregon Creek. Rainbow Trout % Discharge (cfs) Spawning Juvenile Adult 5 34% 86% 75% 7 44% 92% 83% 10 57% 97% 91% 12 64% 99% 94% 15 73% 100% 97% 17 77% 100% 98% 20 83% 99% 99% 25 89% 98% 100% 30 93% 96% 100% 35 96% 95% 99% 40 98% 93% 99% 45 99% 91% 98% % 89% 97% % 88% 95% % 86% 94% 65 99% 85% 93% 70 98% 83% 92% 75 97% 82% 91% 80 95% 81% 90% 90 91% 79% 88% % 77% 86% % 76% 85% % 73% 82% % 71% 80% % 69% 79% % 68% 77% % 67% 76% % 65% 75% % 64% 74% % 63% 73% WUA per 1000 linear feet 18,000 16,000 14,000 12,000 10,000 8,000 6,000 4,000 2,000 0 Oregon Creek - Log Cabin Diversion Dam Reach Rainbow Trout Discharge (cfs) Spawning Juvenile Adult Figure WUA for rainbow trout in the Log Cabin Diversion Dam sub-reach of Oregon Creek. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

106 Table WUA table for Sacramento sucker in the Log Cabin Diversion Dam sub-reach of Oregon Creek. Sacramento Sucker Discharge (cfs) Juvenile Adult 5 13,185 5, ,106 5, ,985 5, ,456 6, ,781 6, ,900 6, ,277 7, ,558 7, ,500 7, ,415 7, ,097 8, ,983 8, ,067 8, ,120 8, ,315 8, ,509 9, ,284 9, ,145 9, ,796 9, ,624 9, ,656 9, ,301 9, ,110 9, ,407 9, ,483 8, ,801 8, ,219 8, ,926 8, ,652 8, ,710 9,023 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Log Cabin Diversion Dam sub-reach of Oregon Creek. Sacramento Sucker % Discharge (cfs) Juvenile Adult 5 81% 53% 7 87% 55% 10 92% 60% 12 95% 61% 15 97% 68% 17 98% 68% % 72% 25 96% 75% 30 95% 78% 35 95% 77% 40 93% 81% 45 92% 84% 50 93% 83% 55 93% 87% 60 88% 88% 65 89% 91% 70 88% 94% 75 86% 94% 80 85% 97% 90 84% 97% % 99% % 100% % 96% % 93% % 86% % 85% % 83% % 85% % 88% % 90% WUA per 1000 linear feet 18,000 16,000 14,000 12,000 10,000 8,000 6,000 4,000 2,000 0 Oregon Creek - Log Cabin Diversion Dam Reach Sacramento Sucker Discharge (cfs) Juvenile Figure WUA for Sacramento sucker in the Log Cabin Diversion Dam sub-reach of Oregon Creek. Adult Exh. E - Environmental Report Application for New License April 2014 Page E ,

107 Table WUA table for Rainbow trout in the Celestial Valley sub-reach of Oregon Creek. Rainbow Trout Discharge (cfs) Spawning Juvenile Adult 6 1,831 11,072 10, ,050 12,030 12, ,490 12,248 12, ,985 12,378 12, ,212 12,378 12, ,439 12,224 12, ,669 11,849 12, ,785 11,346 12, ,876 10,813 12, ,922 10,244 11, ,936 9,681 11, ,940 9,158 10, ,948 8,728 10, ,950 8,325 10, ,939 7,974 9, ,921 7,654 9, ,880 7,360 9, ,825 7,091 8, ,749 6,857 8, ,658 6,652 8, ,447 6,293 7, ,226 6,031 7, ,748 5,670 7, ,281 5,433 6, ,862 5,329 6, ,507 5,267 6, ,267 5,227 6, ,071 5,221 6, ,935 5,243 5, ,860 5,268 5,962 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Celestial Valley subreach of Oregon Creek. Rainbow Trout % Discharge (cfs) Spawning Juvenile Adult 6 31% 88% 78% 10 43% 93% 86% 12 61% 98% 94% 15 70% 99% 97% 17 80% 100% 99% 20 85% 100% 100% 25 90% 99% 100% 30 94% 96% 99% 35 97% 92% 97% 40 98% 87% 94% 45 99% 83% 91% % 78% 88% % 74% 85% % 71% 82% % 68% 79% % 65% 76% 75 99% 62% 74% 80 99% 60% 71% 85 98% 58% 69% 90 94% 55% 65% % 52% 62% % 50% 60% % 48% 56% % 46% 54% % 45% 52% % 44% 51% % 43% 50% % 43% 49% % 43% 48% % 43% 47% WUA per 1000 linear feet 20,000 18,000 16,000 14,000 12,000 10,000 8,000 6,000 4,000 2,000 0 Oregon Creek - Celestial Valley Reach Rainbow Trout Discharge (cfs) Spawning Juvenile Adult Figure WUA for rainbow trout in the Celestial Valley sub-reach of Oregon Creek. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

108 Table WUA table for Sacramento sucker in the Celestial Valley sub-reach of Oregon Creek. Sacramento Sucker Discharge (cfs) Juvenile Adult 6 13,736 3, ,379 4, ,052 4, ,727 5, ,887 5, ,278 5, ,739 5, ,095 5, ,545 5, ,249 5, ,799 6, ,702 6, ,398 6, ,390 7, ,851 7, ,496 8, ,076 8, ,830 8, ,402 8, ,350 7, ,621 7, ,038 6, ,710 6, ,880 6, ,626 5, ,084 6, ,956 5, ,327 5, ,239 5, ,233 4,790 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Celestial Valley sub-reach of Oregon Creek. Sacramento Sucker % Discharge (cfs) Juvenile Adult 6 75% 43% 10 79% 54% 12 88% 57% 15 97% 59% 17 98% 59% % 61% 25 97% 62% 30 99% 64% 35 91% 64% 40 83% 65% 45 75% 73% 50 69% 79% 55 68% 81% 60 62% 83% 65 59% 91% 70 57% 94% 75 55% 100% 80 48% 97% 85 46% 95% 90 46% 92% % 83% % 75% % 73% % 70% % 68% % 70% % 66% % 61% % 61% % 55% WUA per 1000 linear feet 20,000 18,000 16,000 14,000 12,000 10,000 8,000 6,000 4,000 2,000 0 Oregon Creek - Celestial Valley Sub-Reach Sacramento Sucker Discharge (cfs) Juvenile Adult Figure WUA for Sacramento sucker in the Celestial Valley sub-reach of Oregon Creek. Exh. E - Environmental Report Application for New License April 2014 Page E ,

109 Table WUA table for rainbow trout in the New Bullards Bar Dam Reach. Rainbow Trout Discharge (cfs) Spawning Juvenile Adult , ,154 2, ,129 15,015 4, ,259 16,636 6, ,305 17,545 7, ,330 18,591 10, ,313 18,964 12, ,420 19,090 14, ,548 19,287 15, ,631 19,274 16, ,699 19,090 17, ,744 18,965 17, ,774 18,881 17, ,816 18,737 18, ,816 18,618 18, ,760 18,558 18, ,676 18,533 19, ,607 18,420 19, ,509 18,236 19, ,408 18,298 19, ,379 18,514 20, ,377 18,757 20, ,395 19,001 21, ,338 17,490 22, ,801 16,491 21,773 1,000 1,822 16,288 21,592 1,400 1,172 14,609 21,492 1, ,453 20,625 2, ,008 19,543 2,800 1,040 8,898 16,992 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the New Bullards Bar Dam Reach. Rainbow Trout % Discharge (cfs) Spawning Juvenile Adult 2 23% 48% 3% 5 44% 63% 10% 10 62% 78% 19% 15 69% 86% 27% 20 72% 91% 35% 30 73% 96% 48% 40 72% 98% 58% 50 78% 99% 65% 60 85% 100% 71% 70 90% 100% 75% 80 93% 99% 78% 90 96% 98% 80% % 98% 81% % 97% 84% % 97% 85% % 96% 86% % 96% 87% % 96% 87% % 95% 88% % 95% 89% % 96% 91% % 97% 93% % 99% 97% % 91% 100% % 86% 99% 1, % 84% 98% 1,400 64% 76% 98% 1,800 27% 65% 94% 2,200 20% 57% 89% 2,800 57% 46% 77% WUA per 1000 linear feet 40,000 35,000 30,000 25,000 20,000 15,000 10,000 5,000 0 North Yuba River - New Bullards Bar Dam Reach Rainbow Trout ,000 1,500 2,000 2,500 Discharge (cfs) Spawning Juvenile Adult Figure WUA for rainbow trout in the New Bullards Bar Dam Reach of the North Yuba River. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

110 Table WUA table for Sacramento sucker in the New Bullards Bar Dam Reach. Sacramento Sucker Discharge (cfs) Juvenile Adult 2 15,834 11, ,359 12, ,104 14, ,055 14, ,320 14, ,434 16, ,592 17, ,420 17, ,451 18, ,262 17, ,876 17, ,987 17, ,479 16, ,697 17, ,738 16, ,984 16, ,493 16, ,763 15, ,520 13, ,363 14, ,307 13, ,243 13, ,416 16, ,112 16, ,179 15,686 1,000 14,847 16,196 1,400 12,928 14,000 1,800 11,055 13,483 2,200 8,445 13,111 2,800 6,446 10,515 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the New Bullards Bar Dam Reach. Sacramento Sucker % Discharge (cfs) Juvenile Adult 2 71% 64% 5 77% 69% 10 85% 79% 15 89% 82% 20 95% 82% % 90% 40 96% 96% 50 95% 97% 60 96% 100% 70 90% 99% 80 89% 99% 90 89% 98% % 94% % 96% % 93% % 92% % 89% % 87% % 77% % 78% % 76% % 77% % 89% % 89% % 87% 1,000 66% 90% 1,400 58% 77% 1,800 49% 75% 2,200 38% 73% 2,800 29% 58% WUA per 1000 linear feet 40,000 35,000 30,000 25,000 20,000 15,000 10,000 5,000 0 North Yuba River - New Bullards Bar Dam Reach Sacramento Sucker ,000 1,500 2,000 2,500 Discharge (cfs) Juvenile Figure WUA for Sacramento sucker in the New Bullards Bar Dam Reach of the North Yuba River. Adult Exh. E - Environmental Report Application for New License April 2014 Page E ,

111 Table WUA table for hardhead/pikeminnow in the New Bullards Bar Dam Reach. Hardhead and Pikeminnow Discharge (cfs) Juvenile Adult 2 25,735 15, ,110 17, ,562 20, ,436 22, ,215 23, ,338 26, ,937 28, ,070 29, ,374 30, ,276 31, ,239 32, ,066 33, ,833 33, ,284 34, ,186 34, ,997 34, ,676 35, ,080 35, ,511 35, ,554 35, ,819 36, ,638 36, ,536 37, ,269 38, ,391 38,932 1,000 27,279 39,143 1,400 25,106 39,098 1,800 22,720 38,499 2,200 20,526 37,485 2,800 18,055 35,299 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the New Bullards Bar Dam Reach. Hardhead and Pikeminnow % Discharge (cfs) Juvenile Adult 2 75% 39% 5 82% 45% 10 89% 52% 15 91% 57% 20 94% 61% 30 97% 68% 40 99% 73% 50 99% 76% % 79% % 81% % 83% 90 99% 85% % 86% % 87% % 88% % 89% % 90% % 91% % 91% % 92% % 93% % 94% % 96% % 99% % 99% 1,000 79% 100% 1,400 73% 100% 1,800 66% 98% 2,200 60% 96% 2,800 53% 90% WUA per 1000 linear feet 40,000 35,000 30,000 25,000 20,000 15,000 10,000 5,000 0 North Yuba River - New Bullards Bar Dam Reach Hardhead / Pikeminnow ,000 1,500 2,000 2,500 Discharge (cfs) Juvenile Figure WUA for hardhead and pikeminnow in the New Bullards Bar Dam Reach of the North Yuba River. Adult April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

112 Table WUA table for rainbow trout in the Middle/North Yuba River Reach. Rainbow Trout Discharge (cfs) Spawning Juvenile Adult 22 1,568 26,830 9, ,700 28,393 12, ,820 29,204 15, ,916 29,318 18, ,973 29,067 20, ,004 28,543 22, ,985 28,030 24, ,918 27,404 25, ,864 26,708 26, ,781 25,201 27, ,720 23,651 28, ,686 22,238 28, ,568 21,151 28, ,468 20,235 28, ,415 19,167 27, ,399 18,402 27, ,441 17,803 26, ,536 17,434 25, ,638 17,216 25, ,832 16,992 24, ,011 16,821 23, ,140 16,753 23, ,262 16,973 22, ,329 17,274 22, ,355 17,435 22, ,314 17,651 21,657 1,000 2,215 17,587 21,371 1,500 2,241 15,836 21,106 2,000 1,460 14,521 20,598 2, ,799 19,035 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Middle/North Yuba River Reach. Rainbow Trout % Discharge (cfs) Spawning Juvenile Adult 22 67% 92% 34% 30 72% 97% 45% 40 77% 100% 56% 50 81% 100% 66% 60 84% 99% 74% 70 85% 97% 81% 80 84% 96% 86% 90 81% 93% 90% % 91% 94% % 86% 98% % 81% 100% % 76% 100% % 72% 100% % 69% 99% % 65% 98% % 63% 96% % 61% 94% % 59% 92% % 59% 89% % 58% 87% % 57% 85% % 57% 83% % 58% 81% % 59% 80% % 59% 78% % 60% 77% 1,000 94% 60% 76% 1,500 95% 54% 75% 2,000 62% 50% 73% 2,880 7% 40% 67% WUA per 1000 linear feet 50,000 45,000 40,000 35,000 30,000 25,000 20,000 15,000 10,000 5,000 0 Mainstem Yuba River - Middle/North Yuba River Reach Rainbow Trout ,000 1,500 2,000 2,500 3,000 Discharge (cfs) Spawning Juvenile Adult Figure WUA for rainbow trout in the Middle/North Yuba River Reach of the Yuba River. Exh. E - Environmental Report Application for New License April 2014 Page E ,

113 Table WUA table for Sacramento sucker in the Upstream of New Colgate Powerhouse Reach. Sacramento Sucker Discharge (cfs) Juvenile Adult 22 35,934 19, ,129 21, ,208 24, ,964 26, ,522 26, ,538 29, ,615 30, ,656 32, ,451 33, ,330 34, ,150 35, ,661 35, ,703 34, ,707 33, ,245 32, ,508 29, ,601 27, ,065 25, ,122 23, ,445 22, ,197 21, ,502 20, ,696 19, ,925 17, ,764 15, ,065 14,392 1,000 17,493 14,511 1,500 15,840 15,824 2,000 12,992 17,146 2,880 10,279 13,499 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Upstream of New Colgate Powerhouse Reach. Sacramento Sucker % Discharge (cfs) Juvenile Adult 22 97% 54% 30 97% 61% % 70% 50 99% 74% 60 95% 76% 70 90% 82% 80 85% 86% 90 82% 90% % 94% % 98% % 100% % 99% % 98% % 95% % 90% % 84% % 78% % 71% % 67% % 62% % 59% % 57% % 54% % 49% % 45% % 40% 1,000 47% 41% 1,500 43% 45% 2,000 35% 48% 2,880 28% 38% WUA per 1000 linear feet 50,000 45,000 40,000 35,000 30,000 25,000 20,000 15,000 10,000 5,000 0 Mainstem Yuba River - Middle/North Yuba River Reach Sacramento Sucker ,000 1,500 2,000 2,500 3,000 Discharge (cfs) Juvenile Figure WUA for Sacramento sucker in the Middle/North Yuba River Reach of the Yuba River. Adult April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

114 Table WUA table for hardhead and pikeminnow in the Middle/North Yuba River Reach. Hardhead and Pikeminnow Discharge (cfs) Juvenile Adult 22 45,297 29, ,478 32, ,747 36, ,793 38, ,736 40, ,474 42, ,188 43, ,903 44, ,332 45, ,265 46, ,049 47, ,167 48, ,996 48, ,159 48, ,110 48, ,271 47, ,619 47, ,652 46, ,623 46, ,093 45, ,487 44, ,986 43, ,302 43, ,416 42, ,617 42, ,268 42,455 1,000 32,284 42,332 1,500 29,727 41,985 2,000 27,587 41,302 2,880 22,850 40,126 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the Middle/North Yuba River Reach. Hardhead and Pikeminnow % Discharge (cfs) Juvenile Adult 22 95% 61% 30 97% 68% % 74% % 80% % 84% 70 99% 87% 80 99% 90% 90 98% 92% % 94% % 97% % 98% % 99% % 100% % 100% % 99% % 98% % 97% % 96% % 95% % 93% % 92% % 91% % 89% % 88% % 88% % 88% 1,000 68% 87% 1,500 62% 87% 2,000 58% 85% 2,880 48% 83% WUA per 1000 linear feet 50,000 45,000 40,000 35,000 30,000 25,000 20,000 15,000 10,000 5,000 0 Mainstem Yuba River - Middle/North Yuba River Reach Hardhead / Pikeminnow ,000 1,500 2,000 2,500 3,000 Discharge (cfs) Juvenile Figure WUA for hardhead and pikeminnow in the Middle/North Yuba River Reach of the Yuba River. Adult Exh. E - Environmental Report Application for New License April 2014 Page E ,

115 Table WUA table for rainbow trout in the New Colgate Powerhouse Reach. Rainbow Trout Discharge (cfs) Spawning Juvenile Adult , , , , , , , , , , , , , , , , , , , , , Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the New Colgate Powerhouse Reach. Rainbow Trout % Discharge (cfs) Spawning Juvenile Adult % 97% 60% % 100% 78% % 97% 89% % 88% 98% % 80% 100% % 72% 99% % 65% 96% % 59% 92% % 55% 87% 1,056 36% 52% 83% 1,170 32% 49% 78% 1,285 29% 47% 74% 1,400 27% 45% 70% 1,635 26% 43% 63% 1,870 28% 41% 58% 2,105 30% 40% 54% 2,340 31% 40% 50% 2,575 32% 39% 48% 2,809 32% 38% 46% 3,044 32% 38% 45% 3,279 32% 37% 43% 3,514 31% 37% 42% 3,749 30% 37% 41% 4,333 30% 37% 39% 4,916 30% 39% 39% 5,500 26% 41% 39% 6,468 23% 43% 40% 7,436 21% 43% 41% 8,404 19% 41% 43% 9,373 16% 41% 43% WUA per 1000 linear feet 80,000 70,000 60,000 50,000 40,000 30,000 20,000 10,000 0 Mainstem Yuba River - New Colgate Powerhouse Reach Rainbow Trout 0 1,000 2,000 3,000 4,000 5,000 6,000 7,000 8,000 9,000 Discharge (cfs) Spawning Juvenile Adult Figure WUA for rainbow trout in the New Colgate Powerhouse Reach of the Yuba River. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

116 Table WUA table for Sacramento sucker in the New Colgate Powerhouse Reach. Sacramento Sucker Discharge (cfs) Juvenile Adult ,771 35, ,142 36, ,540 35, ,630 33, ,867 31, ,430 29, ,406 27, ,196 24, ,831 22,136 1,056 14,082 19,482 1,170 13,682 18,171 1,285 13,818 17,564 1,400 13,308 16,212 1,635 12,244 14,469 1,870 12,290 13,412 2,105 12,124 12,916 2,340 12,048 12,704 2,575 12,548 12,387 2,809 12,569 12,068 3,044 13,028 11,744 3,279 11,258 12,093 3,514 11,594 11,871 3,749 11,732 11,554 4,333 12,353 11,280 4,916 13,026 11,748 5,500 12,408 11,930 6,468 13,427 11,885 7,436 13,851 12,316 8,404 12,290 13,979 9,373 12,952 14,041 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the New Colgate Powerhouse Reach. Sacramento Sucker % Discharge (cfs) Juvenile Adult % 98% % 100% % 97% % 92% % 86% % 81% % 76% % 68% % 61% 1,056 38% 53% 1,170 37% 50% 1,285 38% 48% 1,400 36% 44% 1,635 33% 40% 1,870 33% 37% 2,105 33% 35% 2,340 33% 35% 2,575 34% 34% 2,809 34% 33% 3,044 35% 32% 3,279 31% 33% 3,514 32% 32% 3,749 32% 32% 4,333 34% 31% 4,916 35% 32% 5,500 34% 33% 6,468 37% 32% 7,436 38% 34% 8,404 33% 38% 9,373 35% 38% WUA per 1000 linear feet 80,000 70,000 60,000 50,000 40,000 30,000 20,000 10,000 0 Mainstem Yuba River - New Colgate Powerhouse Reach Sacramento Sucker 0 1,000 2,000 3,000 4,000 5,000 6,000 7,000 8,000 9,000 Discharge (cfs) Juvenile Figure WUA for Sacramento sucker in the New Colgate Powerhouse Reach of the Yuba River. Adult Exh. E - Environmental Report Application for New License April 2014 Page E ,

117 Table WUA table for hardhead and pikeminnow in the New Colgate Powerhouse Reach. Hardhead and Pikeminnow Discharge (cfs) Juvenile Adult ,449 70, ,001 75, ,649 77, ,411 78, ,212 78, ,253 76, ,282 74, ,436 71, ,068 68,089 1,056 36,588 64,924 1,170 34,896 61,938 1,285 33,612 59,132 1,400 32,160 56,546 1,635 29,561 51,910 1,870 28,316 48,155 2,105 27,211 45,191 2,340 25,910 42,876 2,575 25,209 40,958 2,809 24,639 39,380 3,044 23,966 38,045 3,279 23,612 36,961 3,514 23,536 36,080 3,749 23,551 35,044 4,333 24,255 34,276 4,916 24,639 33,791 5,500 24,525 33,792 6,468 25,081 34,444 7,436 25,035 35,303 8,404 25,261 36,094 9,373 25,900 36,949 Table Values with conditional formatting from 80 to 100 percent of the maximum WUA. Bimodal curves have the lower peak highlighted in yellow, and the upper peak highlighted in green for the New Colgate Powerhouse Reach. Hardhead and Pikeminnow % Discharge (cfs) Juvenile Adult % 89% % 96% % 98% % 100% % 99% % 97% % 94% % 90% % 86% 1,056 53% 82% 1,170 51% 78% 1,285 49% 75% 1,400 47% 72% 1,635 43% 66% 1,870 41% 61% 2,105 40% 57% 2,340 38% 54% 2,575 37% 52% 2,809 36% 50% 3,044 35% 48% 3,279 34% 47% 3,514 34% 46% 3,749 34% 44% 4,333 35% 43% 4,916 36% 43% 5,500 36% 43% 6,468 37% 44% 7,436 37% 45% 8,404 37% 46% 9,373 38% 47% WUA per 1000 linear feet 80,000 70,000 60,000 50,000 40,000 30,000 20,000 10,000 0 Mainstem Yuba River - New Colgate Powerhouse Reach Hardhead / Pikeminnow 0 1,000 2,000 3,000 4,000 5,000 6,000 7,000 8,000 9,000 Discharge (cfs) Juvenile Figure WUA for hardhead and pikeminnow in the New Colgate Powerhouse Reach of the Yuba River. Adult April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

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119 Rainbow trout spawning habitat was limited in most reaches due to patchy and limited distribution of suitable spawning substrate. Where suitable substrate was recorded, the preferred combination of depths and velocities were often not present. Spawning WUA was highest in Oregon Creek and downstream of New Colgate Powerhouse. Optimal spawning discharges varied significantly between streams and in some cases, between sub-reaches. For example on the Middle Yuba River, maximum spawning WUA downstream of Our House Diversion Dam was 90 cfs, whereas maximum spawning WUA downstream of the Oregon Creek confluence was 345 cfs. Upon further review, it was determined that much of the available spawning gravel downstream of the Oregon Creek confluence was perched (i.e., on the stream margin and/or out of the wetted channel at the high flow calibration measurements of 327 and 345 cfs) and are deposited during high flow events. Therefore, the perched gravels only become suitable when flows are high enough to inundate them. Rainbow trout juvenile and adult WUA functions were consistent in magnitude and discharge between study sub-reaches, increasing as channel size increased. The only exception was on the North Yuba River downstream of New Bullards Bar Dam. In this reach, maximum adult rainbow trout WUA occurred at 600 cfs. In comparison, the maximum WUA was 160 cfs upstream and 482 cfs downstream of New Colgate Powerhouse. A potential contributing factor is an artifact and limitation of the PHABSIM velocity model, in which low velocities along the stream margin or behind very large boulders are held unrealistically low as flows increase. This modeling limitation is typically a concern at simulated discharges which greatly exceed the velocity data set discharges, which were recorded with discharges up to 247 cfs. Table summarizes the range of discharges that produce maximum WUA in each reach or sub-reach for modeled life stages of rainbow trout. Table Summary table of discharge at maximum WUA for rainbow trout spawning, juvenile and adult life stages. Rainbow Trout Reach or Sub-reach Spawning (year-round) Juvenile (year-round) Adult (year-round) Corresponding Corresponding Corresponding Corresponding Corresponding WUA 1 Discharge (cfs) WUA Discharge (cfs) WUA Our House Diversion Dam 2, , , Oregon Creek Sub-reach 2, , , Log Cabin 4, , , Celestial Valley 4, , , New Bullards Bar Dam 1, , , Middle/North Yuba River 2, , , Corresponding Discharge (cfs) New Colgate Powerhouse 10, , , WUA, is defined as stream surface area (i.e., sq ft) weighted by habitat suitability variables, most often velocity, depth, and substrate or cover, normalized to 1,000 linear units. Sacramento sucker juvenile and adult WUA functions were also consistent in magnitude and discharge between study sub-reaches, increasing as channel size increased. The only exception was that adult WUA on Oregon Creek had a peak WUA associated with an average discharge of approximately 93 cfs. In comparison, maximum adult Sacramento sucker WUA on the Middle Yuba River was associated with an average discharge of 82 cfs. Given the difference in channel size between the Middle Yuba and Oregon Creek and the associated depths and velocities at each of these two discharges it would be expected that Oregon Creek would have a lower peak discharge. However, review of the Oregon Creek model suggests that sufficient areas of depth April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

120 and low velocity persists in pools and behind boulders, eddies and stream margins to allow for habitat suitability to increase up to approximately 100 cfs. Sacramento pikeminnow habitat was modeled in three of the seven sub-reaches in the North and mainstem Yuba rivers only. Again, the adult and juvenile WUA functions were generally consistent with the variability in channel shape and width except in the reach downstream of New Bullards Bar. Maximum adult WUA in this reach was 1,000 cfs which was 800 cfs and 633 cfs higher upstream and downstream of New Colgate Powerhouse respectively. Table summarizes the range of discharges that produce maximum WUA in each reach or sub-reach for modeled life stages of Sacramento sucker. Table Summary table of discharge at maximum WUA for Sacramento sucker juvenile and adult life stages. 1 Sacramento Sucker Juvenile (year-round) Adult (year-round) Reach or Sub-reach Corresponding WUA 1 Corresponding Discharge (cfs) Corresponding WUA Our House Diversion Dam 24, , Oregon Creek Sub-reach 26, , Log Cabin 16, , Celestial Valley 18, , New Bullards Bar Dam 22, , Middle/North Yuba River 37, , New Colgate Powerhouse 36, , Corresponding Discharge (cfs) WUA, is defined as stream surface area (i.e., sq ft) weighted by habitat suitability variables, most often velocity, depth, and substrate or cover, normalized to 1,000 linear units. Hardhead was included in YCWA s instream flow study as a species sharing the same habitat preferences as Sacramento pikeminnow. However, hardhead has not been documented in the Project-affected study reaches to date. Therefore, use of the PHABSIM results for hardhead in the development of flow recommendations is premature until such time as hardhead are documented. Table summarizes the range of discharges that produce maximum WUA in each reach or sub-reach for modeled life stages of Sacramento pikeminnow and hardhead. Table Summary table of discharge at maximum WUA for hardhead/pikeminnow juvenile and adult life stages. 1 2 Hardhead / Pikeminnow Juvenile (year-round) Adult (year-round) Stream reach or Sub-reach Corresponding WUA 1 Corresponding Discharge (cfs) Corresponding WUA Our House Diversion Dam Oregon Creek Sub-reach Log Cabin Celestial Valley New Bullards Bar Dam 34, ,143 1,000 Middle/North Yuba River 47, , New Colgate Powerhouse 68, , Corresponding Discharge (cfs) WUA, is defined as stream surface area (i.e., sq ft) weighted by habitat suitability variables, most often velocity, depth, and substrate or cover, normalized to 1,000 linear units. Dash indicates that the species was not found in the reach during sampling by YCWA in 2012 as part of Study 3.8. Exh. E - Environmental Report Application for New License April 2014 Page E ,

121 Habitat Time Series Habitat time series results can be used to evaluate habitat availability over time, and this is a crucial step in the examination of habitat availability that may influence long-term changes in fish populations (Waddle 2001). Each species and life stage has a distinctive time series due to the differences in the flow-habitat relationships derived from the WUA function. Evaluations of habitat time series results can be conducted through a variety of methods but are typically conducted in the form of a habitat exceedence (i.e., duration) analysis which is particularly useful for assessing the impacts of alternative flow regimes over the complete range of discharges considered for alternative flow scenarios (Waddle 2001). To summarize each habitat time series by reach, species and life stage or by month, a series of habitat exceedence curves and monthly Area under the Curve (AUC) charts were developed. The AUC metric is a full series metric calculated by summing the habitat value associated with each percentile along the habitat duration curve from one to 100 percent. From these charts, trends and patterns in habitat availability can be observed for a specific stream reach at various locations under different hydrologic conditions. For purposes of comparison, hydrologic nodes (i.e., Node 0, Node 1, Node 2, and Node 3) were used representing the cumulative effect of accretion on stream flow and thus habitat availability moving downstream from a Project facility. In general, trends in species and life stage habitat duration results followed seasonal flow patterns or powerhouse operations. Monthly AUC patterns in the Middle/North Yuba River confluence reach tracked Project releases and accretion closely. Downstream of New Bullards Bar Dam, habitat duration results were relatively constant between months due to the constant controlled year-round releases. Patterns in monthly habitat in the Yuba River downstream of New Colgate Powerhouse for all species closely tracked patterns in monthly median discharges from the New Colgate Powerhouse. Summer habitat was reduced due to high volumes releases while lower flow rates and/or reduced frequency of releases in the fall and winter correspond to the observed increase habitat availability. Upstream of New Colgate Powerhouse, juvenile life stages of all species displayed reduced habitat availability during the late winter and spring months (i.e., January-May) due to their preference for lower velocities and/or depths. Conversely, in the fall and early winter months (i.e., June-December) habitat availability increased due to lower flows. The adult life stages of all species displayed a positive relationship to increased flows in the winter and spring while habitat availability was reduced in the summer and early fall. Habitat availability did not necessarily increase downstream from Project facilities due to increases in accretion. For example, for all life stages of rainbow trout and Sacramento sucker, habitat availability decreased at the MY2 node (i.e., Oregon Creek Reach of the Middle Yuba River) as compared to the MY1 node (i.e., Our House Diversion Dam Reach. The comparatively lower habitat availability is associated to increased accretion as the WUA flow habitat relationships between these reaches were similar in terms of magnitude and optimal discharges. In contrast, in Oregon Creek habitat availability increased for all life stages of rainbow trout and Sacramento sucker moving downstream of Log Cabin Diversion Dam from OC1 node to OC3 node. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

122 In all, 70 habitat time series were developed for existing conditions (No Action Alternative) using the With-Project Hydrology dataset. Monthly habitat exceedences were generated for each of the 12 hydrologic nodes for the five to seven life stages analyzed in each reach. From habitat exceedence, the metric AUC was calculated. For reference, Figure shows the location and names of all hydrologic node locations used in the HDA analysis. Exh. E - Environmental Report Application for New License April 2014 Page E ,

123 Figure Map of hydrologic node locations for the habitat duration analysis (HDA). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

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125 Habitat exceedence tabular results are presented in Tables through , 29 while corresponding graphical results are presented in Figures through Each table and chart compare the monthly AUC metrics derived from the habitat exceedence curve for each species and life stage at a specific hydrologic node. Table Habitat duration analysis results for the Our House Diversion Dam Reach, Middle Yuba River for the No Action Alternative at Node 0. 1 Month Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/Hardhead Juvenile 1 Pikeminnow/Hardhead Adult 1 Oct -- 75,352,039 40,228,102 88,557,875 41,054, Nov -- 75,497,606 42,205,012 88,107,998 42,083, Dec -- 74,118,657 42,403,895 86,155,428 41,769, Jan -- 72,383,375 42,668,718 83,848,309 41,417, Feb -- 72,917,499 43,175,602 84,413,915 41,835, Mar -- 72,441,687 43,820,364 83,583,485 41,945, Apr 8,434,550 74,018,682 50,239,560 84,714,346 45,336, May 8,631,374 72,711,921 55,367,752 82,333,464 47,373, Jun 8,503,009 75,367,603 49,550,873 86,668,801 45,434, Jul -- 75,965,217 41,809,752 88,834,474 42,092, Aug -- 75,173,852 40,408,068 88,318,270 41,102, Sep -- 74,925,410 39,639,875 88,276,570 40,622, Pikeminnnow/Hardhead were not modeled as none have been documented in this reach. Figure Habitat duration analysis results for the Our House Diversion Dam Reach, Middle Yuba River for the No Action Alternative at Node Habitat exceedence charts were only developed for the months shown in the periodicity table (Section 2.2-1) for each species. For example, the analysis for rainbow trout spawning was only conducted from April through June and therefore, only charts for those months are shown. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

126 Table Habitat duration analysis results for the Our House Diversion Dam Reach, Middle Yuba River for the No Action Alternative at Node 1. 1 Months Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/Hardhead Juvenile 1 Pikeminnow/Hardhead Adult 1 Oct -- 75,714,700 41,447,854 88,746,069 41,843, Nov -- 75,838,492 45,544,701 87,806,031 43,860, Dec -- 74,189,288 48,925,880 84,763,488 44,800, Jan -- 71,917,112 52,432,630 80,808,564 45,546, Feb -- 71,942,077 55,946,527 79,859,371 46,967, Mar -- 70,892,434 58,469,798 77,528,949 47,585, Apr 9,179,497 71,932,457 59,794,104 78,347,798 48,242, May 8,943,653 70,830,049 59,277,739 77,259,323 48,275, Jun 8,728,133 75,222,402 52,434,696 85,398,099 46,875, Jul -- 76,360,339 43,371,868 89,035,047 43,087, Aug -- 75,417,556 41,174,976 88,464,117 41,608, Sep -- 75,187,133 40,364,168 88,437,965 41,103, Pikeminnnow/Hardhead were not modeled as none have been documented in this reach. Figure Habitat duration analysis results for the Our House Diversion Dam Reach, Middle Yuba River for the No Action Alternative at Node 1. Table Habitat duration analysis results for the Oregon Creek Reach, Middle Yuba River for the No Action Alternative at Node 2. Months Rainbow Rainbow Rainbow Sacramento Sacramento Pikeminnow/Hardhead Pikeminnow/Hardhead Trout Trout Trout Sucker Sucker Juvenile 1 Adult 1 Spawning Juvenile Adult Juvenile Adult Oct -- 54,780,657 32,250,791 65,147,714 41,498, Nov -- 53,831,995 36,683,749 62,573,765 43,621, Dec -- 50,986,041 39,393,706 58,200,849 44,287, Exh. E - Environmental Report Application for New License April 2014 Page E ,

127 Table (continued) 1 Months Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/Hardhead Juvenile 1 Pikeminnow/Hardhead Adult 1 Jan -- 47,405,577 41,005,316 53,420,105 43,521, Feb -- 45,651,266 42,810,490 50,775,949 43,327, Mar -- 43,681,937 43,489,019 48,352,296 42,176, Apr 4,059,351 45,460,823 44,731,866 50,011,022 44,008, May 3,570,327 46,822,309 44,391,348 51,681,776 45,612, Jun 2,259,171 52,512,741 41,538,950 59,133,268 46,676, Jul -- 55,372,467 34,868,273 64,932,110 43,087, Aug -- 54,888,950 31,648,030 65,545,999 41,030, Sep -- 54,607,274 30,538,483 65,562,276 40,402, Pikeminnnow/Hardhead were not modeled as none have been documented in this reach. Figure Habitat duration analysis results for the Oregon Creek Reach, Middle Yuba River for the No Action Alternative at Node 2. Table Habitat duration analysis results for the Log Cabin Diversion Dam Reach, Oregon Creek for the No Action Alternative at Node 0. Months Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/Hardhead Juvenile 1 Pikeminnow/Hardhead Adult 1 Oct -- 5,736,947 5,609,961 7,169,784 2,834, Nov -- 6,912,271 6,837,316 8,663,835 3,465, Dec -- 7,016,283 7,017,212 8,848,061 3,637, Jan -- 6,943,165 7,021,734 8,810,385 3,774, Feb -- 7,023,701 7,111,122 8,902,317 3,819, Mar -- 7,064,641 7,201,280 8,977,309 3,925, April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

128 Table (continued) 1 Months Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/Hardhead Juvenile 1 Pikeminnow/Hardhead Adult 1 Apr 1,613,554 7,407,168 7,571,905 9,424,925 3,923, May 1,785,919 7,641,205 7,888,336 9,775,844 4,015, Jun 1,550,220 7,499,111 7,558,786 9,474,109 3,774, Jul -- 6,718,739 6,633,849 8,408,002 3,313, Aug -- 5,709,895 5,592,574 7,137,242 2,818, Sep -- 5,151,429 5,018,328 6,434,575 2,546, Pikeminnnow/Hardhead were not modeled as none have been documented in this reach. Figure Habitat duration analysis results for the Log Cabin Diversion Dam Reach, Oregon Creek for the No Action Alternative at Node 0. Table Habitat duration analysis results for the Log Cabin Diversion Dam Reach, Oregon Creek for the No Action Alternative at Node 1. 1 Months Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/Hardhead Juvenile 1 Pikeminnow/Hardhead Adult 1 Oct -- 5,782,036 5,662,028 7,228,145 2,860, Nov -- 6,972,930 6,935,141 8,761,533 3,513, Dec -- 7,117,401 7,197,595 9,015,846 3,734, Jan -- 7,081,016 7,281,638 9,055,508 3,919, Feb -- 7,197,500 7,448,652 9,221,204 4,008, Mar -- 7,257,833 7,588,818 9,342,995 4,151, Apr 1,822,213 7,521,556 7,841,444 9,666,763 4,142, May 1,905,456 7,670,432 8,013,430 9,872,423 4,186, Jun 1,604,296 7,538,338 7,637,523 9,541,868 3,840, Jul -- 6,752,125 6,679,154 8,452,909 3,335, Aug -- 5,740,892 5,627,644 7,177,152 2,835, Sep -- 5,190,038 5,059,443 6,483,671 2,567, Pikeminnnow/Hardhead were not modeled as none have been documented in this reach. Exh. E - Environmental Report Application for New License April 2014 Page E ,

129 Figure Habitat duration analysis results for Log Cabin Diversion Dam Reach, Oregon Creek for the No Action Alternative at Node 1. Table Habitat duration results for the Log Cabin Diversion Dam Reach, Oregon Creek for the No Action Alternative at Node 2 (Celestial Valley). 1 Months Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/Hardhead Juvenile 1 Pikeminnow/Hardhead Adult 1 Oct -- 5,285,129 5,176,384 6,444,646 1,955, Nov -- 6,410,691 6,401,083 8,009,664 2,491, Dec -- 6,519,905 6,636,543 8,484,441 2,661, Jan -- 6,372,376 6,601,090 8,670,629 2,751, Feb -- 6,396,781 6,715,634 9,048,443 2,893, Mar -- 6,322,500 6,732,055 9,175,169 3,009, Apr 2,451,516 6,675,909 7,064,610 9,755,284 3,037, May 2,456,633 6,903,150 7,244,927 10,074,411 3,025, Jun 2,037,387 6,991,482 7,106,635 9,291,096 2,804, Jul -- 6,246,060 6,187,925 7,548,002 2,372, Aug -- 5,247,331 5,133,058 6,360,803 1,937, Sep -- 4,712,551 4,583,859 5,736,196 1,717, Pikeminnnow/Hardhead were not modeled as none have been documented in this reach. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

130 Figure Habitat duration results for the Log Cabin Diversion Dam Reach, Oregon Creek for the No Action Alternative at Node 2 (Celestial Valley). Table Habitat duration results for the Log Cabin Diversion Dam Reach, Oregon Creek for the No Action Alternative at Node 3. 1 Months Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/Hardhead Juvenile 1 Pikeminnow/Hardhead Adult 1 Oct -- 10,006,163 9,867,364 12,543,116 4,981, Nov -- 11,875,726 12,042,610 15,043,619 6,208, Dec -- 11,967,440 12,532,333 15,408,146 6,796, Jan -- 11,719,396 12,658,458 15,327,899 7,335, Feb -- 11,773,060 12,967,108 15,504,448 7,736, Mar -- 11,687,273 13,118,203 15,483,140 8,117, Apr 3,834,976 12,180,375 13,483,023 16,010,615 7,918, May 3,721,960 12,541,576 13,641,298 16,414,787 7,674, Jun 3,039,891 12,700,521 13,155,777 16,243,437 6,780, Jul -- 11,516,910 11,498,891 14,470,832 5,727, Aug -- 9,847,079 9,695,628 12,322,338 4,879, Sep -- 8,995,294 8,800,739 11,248,860 4,460, Pikeminnnow/Hardhead were not modeled as none have been documented in this reach. Exh. E - Environmental Report Application for New License April 2014 Page E ,

131 Figure Habitat duration results for Log Cabin Diversion Dam Reach, Oregon Creek for the No Action Alternative at Node 3. Table Habitat duration results for the New Bullards Bar Dam Reach, North Yuba River for the No Action Alternative at Node 0. Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/ Hardhead Juvenile Pikeminnow/ Hardhead Adult Months Oct -- 16,851,657 3,702,277 22,881,400 16,728,485 36,863,982 23,697,044 Nov -- 16,851,657 3,702,277 22,881,400 16,728,485 36,863,982 23,697,044 Dec -- 16,526,326 3,819,195 22,337,033 16,516,233 36,119,636 23,726,849 Jan -- 16,325,034 4,789,409 21,728,486 16,441,542 35,432,988 24,755,053 Feb -- 16,520,136 4,826,901 21,974,662 16,549,555 35,810,190 24,804,965 Mar -- 16,461,772 6,463,465 21,285,043 16,625,804 35,183,080 26,719,754 Apr 1,180,274 16,699,808 4,908,225 22,200,942 16,678,299 36,123,873 25,019,576 May 1,147,360 16,477,465 5,749,267 21,596,453 16,621,237 35,510,031 25,946,486 Jun 1,178,519 16,794,258 6,198,613 21,803,966 16,833,533 35,933,570 26,437,622 Jul -- 16,851,657 3,702,277 22,834,030 16,728,485 36,833,441 23,697,044 Aug -- 16,851,657 3,702,277 22,881,400 16,728,485 36,863,982 23,697,044 Sep -- 16,851,657 3,702,277 22,881,400 16,728,485 36,863,982 23,697,044 April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

132 Figure Habitat duration results for the New Bullards Bar Dam Reach, North Yuba River for the No Action Alternative at Node 0. Table Habitat duration results for the New Bullards Bar Dam Reach, North Yuba River for the No Action Alternative at Node 1. Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/ Hardhead Juvenile Pikeminnow/ Hardhead Adult Months Oct -- 16,953,990 3,776,446 22,943,839 16,789,089 36,951,688 23,793,441 Nov -- 17,315,057 4,082,833 23,172,585 16,983,034 37,240,604 24,165,602 Dec -- 17,519,670 4,740,809 22,949,565 17,061,560 36,904,038 24,841,460 Jan -- 17,873,820 6,278,100 22,709,462 17,286,874 36,662,761 26,472,387 Feb -- 18,485,116 6,638,229 23,209,276 17,607,386 37,369,623 26,941,206 Mar -- 18,531,552 8,285,477 22,569,688 17,750,685 36,814,713 28,898,916 Apr 1,368,249 18,466,370 6,322,770 23,273,936 17,667,847 37,555,042 26,768,081 May 1,256,014 17,488,059 6,531,666 22,197,604 17,199,851 36,348,478 26,935,298 Jun 1,213,646 17,107,795 6,426,917 21,994,850 17,020,164 36,204,150 26,734,398 Jul -- 16,986,878 3,800,282 22,912,716 16,808,566 36,946,189 23,824,421 Aug -- 16,915,851 3,748,803 22,920,568 16,766,502 36,919,000 23,757,514 Sep -- 16,911,392 3,745,571 22,917,848 16,763,861 36,915,178 23,753,313 Exh. E - Environmental Report Application for New License April 2014 Page E ,

133 Figure Habitat duration results for the New Bullards Bar Dam Reach, North Yuba River for the No Action Alternative at Node 1. Table Habitat duration results for the Middle/North Yuba River Reach, Yuba River for the No Action Alternative at Node 1. Months Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/ Hardhead Juvenile Pikeminnow/ Hardhead Adult Oct -- 88,466,508 56,532, ,113,028 79,646, ,273, ,469,552 Nov -- 84,423,941 64,668, ,620,949 83,804, ,565, ,337,824 Dec -- 76,913,789 70,101,206 88,318,689 85,648, ,753, ,461,147 Jan -- 68,013,925 73,153,202 74,231,067 84,089, ,620, ,652,701 Feb -- 63,752,086 76,774,242 67,293,218 86,429, ,818, ,877,916 Mar -- 58,015,045 77,012,841 59,252,781 83,020, ,184, ,092,683 Apr 4,835,809 62,766,066 80,079,523 65,311,447 91,026, ,058, ,598,040 May 4,995,621 66,973,331 78,845,400 71,134,527 91,356, ,556, ,399,309 Jun 5,611,081 78,676,485 71,622,216 89,650,600 86,726, ,198, ,769,732 Jul -- 88,399,240 60,684, ,727,140 81,526, ,346, ,322,354 Aug -- 88,968,132 55,155, ,652,837 78,514, ,583, ,167,516 Sep -- 88,857,024 53,539, ,696,916 77,731, ,538, ,697,594 April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

134 Figure Habitat duration results for the Middle/North Yuba River Reach, Yuba River for the No Action Alternative at Node 1. Table Habitat duration results for the New Colgate Powerhouse Reach, Yuba River for the No Action Alternative at Node 0. Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/ Hardhead Juvenile Pikeminnow/ Hardhead Adult Months Oct -- 18,240,970 31,561,392 15,454,413 23,174,795 38,402,142 64,553,606 Nov -- 18,312,222 30,633,756 15,631,609 22,959,253 38,174,396 63,017,199 Dec -- 18,761,926 28,924,340 16,582,302 22,578,523 37,878,395 60,148,608 Jan -- 16,249,335 24,204,793 14,795,000 18,342,932 32,655,360 51,423,829 Feb -- 15,417,363 22,320,158 14,183,011 17,049,246 30,812,619 47,923,600 Mar -- 15,799,537 22,362,483 14,615,225 17,371,123 31,389,201 48,110,642 Apr 4,000,954 15,075,632 23,435,575 13,650,843 16,712,471 30,742,119 49,868,663 May 2,966,713 12,366,833 18,826,127 11,460,239 12,621,532 25,009,995 41,030,640 Jun 2,962,077 12,402,730 19,218,509 11,430,223 12,804,304 25,325,977 41,736,399 Jul -- 12,605,547 20,594,578 11,507,002 13,208,833 26,251,385 44,538,262 Aug -- 13,628,324 23,395,756 12,072,061 14,882,958 28,844,039 49,710,229 Sep -- 17,891,595 31,024,909 15,212,813 22,429,308 37,671,287 63,527,372 Exh. E - Environmental Report Application for New License April 2014 Page E ,

135 Figure Habitat duration results for the New Colgate Powerhouse Reach, Yuba River for the No Action Alternative at Node 0. Table Habitat duration results for the New Colgate Powerhouse Reach, Yuba River for the No Action Alternative at Node 1. Months Rainbow Trout Spawning Rainbow Trout Juvenile Rainbow Trout Adult Sacramento Sucker Juvenile Sacramento Sucker Adult Pikeminnow/ Hardhead Juvenile Pikeminnow/ Hardhead Adult Oct -- 18,228,396 31,555,003 15,443,534 23,158,759 38,382,044 64,534,912 Nov -- 18,272,602 30,632,050 15,588,150 22,915,514 38,100,487 62,973,980 Dec -- 18,689,089 28,921,827 16,500,294 22,504,682 37,749,081 60,070,071 Jan -- 16,178,058 24,190,387 14,713,093 18,270,845 32,512,557 51,328,197 Feb -- 15,344,350 22,297,742 14,107,731 16,969,216 30,672,784 47,813,339 Mar -- 15,691,785 22,337,681 14,491,626 17,258,844 31,185,854 47,974,383 Apr 3,969,901 14,997,002 23,361,265 13,580,231 16,608,681 30,585,843 49,688,685 May 2,961,480 12,351,635 18,788,749 11,451,169 12,597,243 24,977,171 40,958,111 Jun 2,960,443 12,399,075 19,205,804 11,429,000 12,796,476 25,316,045 41,713,366 Jul -- 12,603,514 20,588,143 11,505,643 13,204,909 26,245,940 44,526,621 Aug -- 13,626,561 23,391,375 12,071,125 14,879,867 28,839,857 49,702,208 Sep -- 17,885,564 31,019,904 15,207,556 22,420,130 37,661,125 63,517,194 April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

136 Figure Habitat duration results for the New Colgate Powerhouse Reach, Yuba River for the No Action Alternative at Node 1. Downstream of Narows 2 Powerhouse YCWA performed Study 7.10, an instream flow study in the Yuba River downstream of the Narrows 2 Powerhouse. The objectives of the study were to: 1) estimate fish habitat versus flow relationships; 2) use weighted usable area (WUA) versus flow relationships and the hydrologic record to develop a habitat duration analysis of fish habitat over time under the existing operational scenario; and 3) model the relationship between river flow and the inundation of potential juvenile salmonid floodplain rearing habitat. The study targeted the following five fish species and lifestages: 1) spawning, fry and juvenile Central Valley steelhead; 2) adult rainbow trout; 3) spawning, fry and juvenile Chinook salmon (i.e., both spring-run and fall-run); 4) spawning North American green sturgeon; and 5) adult and ammocoete lamprey (i.e., Pacific lamprey and river lamprey). YCWA and Relicensing Participants collaboratively agreed to use the existing Sedimentation and River Hydraulics two-dimensional Model, Version 2.1 (SRH2D v2.1) for Project modeling in the Yuba River below Englebright. The model was developed by the RMT to simulate flow velocities, depths and directions in the river, excluding a 1.16-mi long inaccessible, narrow, bedrock canyon known as the Narrows Reach. The RMT collected field data to develop the model from June 2006 through June The hydraulic model was developed from October 2010 through June Habitat modeling results presented below, were developed using the YCWA and Relicensing Participants collaboratively developed HSC for target species and life stages. The HSC are Exh. E - Environmental Report Application for New License April 2014 Page E ,

137 presented, in detail, in Technical memorandum 7-10, Instream Flow Downstream of Englebright Reservoir. For spring-run and fall-run Chinook salmon and steelhead spawning WUA analyses conducted in the Applicant-Prepared BA (and the Chinook salmon spawning WUA analyses in the Applicant- Prepared Draft EFH Assessment), simulated spawning WUA was evaluated for two sets of Chinook salmon and steelhead spawning HSCs. Simulated spawning habitat availability for Chinook salmon was calculated using the best bioverified Chinook salmon spawning HSCs (i.e., the Beak/RMT CHSI S5c model), and the Relicensing Participants Chinook salmon spawning HSCs. Simulated spawning habitat availability for steelhead also was calculated using the best bioverified steelhead spawning HSCs (i.e., the RMT HSCs), as well as for the Relicensing Participants steelhead spawning HSCs. For habitat modeling purposes, the study area was divided into four Hydrologic Zones (HZs): Englebright Dam (EDHZ); Deer Creek (DeerHZ); Dry Creek (DryHZ); and Daguerre Point Dam (DPHZ) (Table ). WUA was calculated for all target species and lifestages for each HZ. Table Hydrologic zone boundaries established for habitat modeling in the Yuba River downstream from Englebright Dam. 1 Habitat/Hydrologic Zone Reach Name Daguerre Point Dam Hydrologic Zone Dry Creek Hydrologic Zone Deer Creek Hydrologic Zone 1 Englebright Dam Hydrologic Zone Zone Abbreviation DPHZ DryHZ DeerHZ EDHZ Zone Description Zone extends from the Feather River confluence upstream to Daguerre Point Dam. Zone extends from Daguerre Point Dam upstream to the confluence of Dry Creek. Zone extends from the confluence of Dry Creek upstream to the confluence of Deer Creek. Zone extends upstream from the confluence with Deer Creek to approximately 500 ft below Englebright Dam. Lower Boundary (RM) Upper Boundary (RM) Length (miles) [Length not modeled] [0.2] [1.1 1 ] [0.1] Total [1.4] The Narrows Reach, which is within the Deer Creek HZ, is very confined, with Class III-V rapids that prevent topographic and bathymetric surveys due to safety and accessibility issues. Slope and thalweg location cannot be accurately determined. Therefore, habitat was not modeled in this 1.1 mile section of the Deer Creek reach. Figure is a map of the Yuba River showing the four Hydrologic Zones. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

138 Figure Map of hydrologic zone boundaries used in Study Exh. E - Environmental Report Application for New License April 2014 Page E ,

139 For approximately half of the species and lifestages, WUA results showed a bimodal habitat function. Bimodal WUA functions are common in streams where the active channel and floodplain are highly connected; in the Yuba River downstream of Englebright Dam, floods regularly spill onto the floodplain (YCWA 2012). One peak of the WUA curves usually occurred within the active channel and one peak occurred outside the active channel in the floodplain. Bimodal functions are most common in DryHZ DPHZ. Based on hydrology records from 1970 to 2010, there is a higher statistical likelihood (frequency) of flows annually exceeding bankfull in the two downstream HZs (i.e., DryHZ and DPHZ) than in the two upstream HZs (i.e., EDHZ and DeerHZ) (YCWA 2012). Based on YCWA s relicensing Technical Memorandum 1-2, Channel Morphology Downstream of Englebright Dam, bankfull discharge is approximately 5,000 cfs in the Yuba River downstream of Englebright Dam. According to flood frequency analysis, 5,000 cfs has a return interval of about once every 1.25 years. That means that there is an 82 percent chance the river will spill out onto the floodplain in any given year. The next higher inundation threshold is approximately 21,100 cfs, which is considered to be the floodplain-filling flow. This discharge has a 2.5 year return interval and a 40 percent chance of occurring in any given year. In several cases, WUAs peaked at flows above the floodplain-filling threshold of 21,100 cfs. The product of the SRH2D v2.1 model velocity and depth results and the species/lifestage specific HSC is an index of habitat suitability known as WUA, which is a relationship between flow and habitat for each target species/lifestage. Total WUA (sq ft of habitat versus flow) was calculated as described in Section 2.10 of Technical Memorandum The study area was then partitioned into HZs (Figure ) and total WUA was calculated for each HZ. The WUA Tables through and Figures through below show the relationship between discharge and the availability of suitable habitat for life stages of target species within each HZ. WUA figures and tables are for the modeled range only. Extrapolated WUA tables are presented in Attachment 7-10 C of Technical Memorandum 7-10 in Appendix E6. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

140 Page Left Blank Exh. E - Environmental Report Application for New License April 2014 Page E ,

141 Table Summary table of discharge at peak WUA for Chinook salmon spawning, fry and juvenile life stages Hydrologic Zone Upper and Lower Peak of Bimodal WUA Curve 1 Fry with Cover Juvenile with Cover Fry No Cover Juvenile No Cover Spawning (Spring-run Nov 15 Feb 15) (Spring-run all year) (Spring-run Nov 15 Feb 15) (Spring-run all year) (Spring-run Sep 1 Oct 15) (Fall run Dec 15 Apr 30) (Fall-run Jan 15 Jun 30) (Fall run Dec 15 Apr 30) (Fall-run Jan 15 Jun 30) (Fall-run Oct 1 Dec 30) Corresponding WUA 2 Corresponding Discharge (cfs) 3 Corresponding WUA 2 Corresponding Discharge (cfs) 3 Corresponding WUA 2 Corresponding Discharge (cfs) 3 Corresponding WUA 2 Corresponding Discharge (cfs) 3 Corresponding WUA 2 Corresponding Discharge (cfs) 3 Englebright Dam Lower Upper 133, , , , ,641 15,000 Deer Creek Lower 4,329, ,974, ,825, ,862, ,060, Upper 5,238,000 21,100 3,200,000 21,100 Dry Creek Lower 1,091, ,375, ,611, ,083,000 1,500-1,700 Upper 1,126,000 5,000 1,674,000 5,000 1,806,000 15,000 2,926,000 21,100 1,540,000 15,000 Daguerre Lower 3,521, ,048, ,939, ,996, ,684, Upper 3,803,000 5,000 5,456,000 5,000 6,352,000 21,100 11,260,000 21,100 4,631,000 21,100 Because of the significant bimodal WUA functions observed for some life stages, both the lower maximum and the upper maximum are provided. WUA is the total stream surface area (i.e., sq ft) weighted by habitat suitability variables of velocity, depth, and substrate or cover. Normal maximum controllable releases at YCWA s New Colgate and Narrows 2 powerhouses are 3,430 cfs and 3,400 cfs, respectively. Maximum controllable flow below Englebright Dam is the combined capacity (4,130 cfs) of YCWA s Narrows 2 Powerhouse of 3,400 cfs and the PG&E Narrows 1 Powerhouse capacity of 730 cfs). Table Summary table of discharge at peak WUA for steelhead spawning, fry, juvenile, and adult life stages. Hydrologic Zone Upper and Lower Peak of Bimodal WUA Curve 1 Corresponding WUA 2 Fry with Cover Juvenile with Cover Fry No Cover Juvenile No Cover Spawning (Apr 1 Jul 31) (all year) (Apr 1 Jul 31) (all year) (Jan 1 Apr 30) Corresponding Corresponding Corresponding Corresponding Corresponding Corresponding Corresponding Corresponding Discharge (cfs) 3 WUA 2 Discharge (cfs) 3 WUA 2 Discharge (cfs) 3 WUA 2 Discharge (cfs) 3 WUA 2 Corresponding Discharge (cfs) 3 Englebright Dam Lower Upper 134, , , , ,527 21,100 Deer Creek Lower 3,634, ,294, ,455,000 2,500 3,000 3,272, ,805, Upper 3,913,000 21,100 5,254,000 21,100 5,754,000 42,200 Dry Creek Lower 1,393, ,617,000 1,000 1,314,000 5,000 1,656,000 5,000 Upper 2,097,000 15,000 3,100,000 21,100 2,509,000 15,000 Daguerre Lower 5,087, ,745, ,096, ,959,000 1,700 4,143,000 5,000 Upper 5,446,000 5,000 7,265,000 21,100 11,773,000 21,100 9,702,000 30,000 1 Because of the significant bimodal WUA functions observed for some life stages, both the lower maximum and the upper maximum are provided. 2 WUA is the total stream surface area (i.e., sq ft) weighted by habitat suitability variables of velocity, depth, and substrate or cover. 3 Normal maximum controllable releases at YCWA s New Colgate and Narrows 2 powerhouses are 3,430 cfs and 3,400 cfs, respectively. Maximum controllable flow below Englebright Dam is the combined capacity (4,130 cfs) of YCWA s Narrows 2 Powerhouse of 3,400 cfs and the PG&E Narrows 1 Powerhouse capacity of 730 cfs). Table Summary table of discharge at peak WUA for rainbow trout adult and lamprey ammocoete and adult life stages Upper and Lower Peak of Bimodal WUA Curve 1 Rainbow Trout Adult (all year) Lamprey Adult (Mar 1 Jun 30) Lamprey Ammocoetes Hydrologic Zone Corresponding Corresponding Corresponding Corresponding Corresponding Corresponding WUA 2 Discharge (cfs) 3 WUA 2 Discharge (cfs) 3 WUA 2 Discharge (cfs) 3 Englebright Dam Lower 152,133 21,100 N/A N/A 79 21,100 Upper 216, N/A N/A Deer Creek Lower 3,521, N/A N/A 64, Upper 3,999,134 42,200 N/A N/A Dry Creek Lower 1,285, N/A N/A 47,457 1,700 Upper 2,156,000 21,100 N/A N/A Daguerre Lower 5,103, ,240 5,000 72,699 2,500 Upper 10,625,000 30, , ,780 10,000 Because of the significant bimodal WUA functions observed for some life stages, both the lower maximum and the upper maximum are provided. WUA is the total stream surface area (i.e., sq ft) weighted by habitat suitability variables of velocity, depth, and substrate or cover. Normal maximum controllable releases at YCWA s New Colgate and Narrows 2 powerhouses are 3,430 cfs and 3,400 cfs, respectively. Maximum controllable flow below Englebright Dam is the combined capacity (4,130 cfs) of YCWA s Narrows 2 Powerhouse of 3,400 cfs and the PG&E Narrows 1 Powerhouse capacity of 730 cfs). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

142 Table Englebright Dam Hydrologic Zone Chinook salmon WUA results. Discharge (cfs) Percent Exceedance Spawning 1 Chinook WUA (sq ft) Fry No Cover 1 Juvenile No Cover 1 Fry Cover 1 Juvenile Cover 1 Spawning Fry No Cover Percent of Maximum WUA Juvenile No Cover Fry Cover Juvenile Cover % 100.0% 100.0% 100.0% 100.0% % 95.9% 97.6% 97.0% 98.5% % 93.3% 95.7% 94.8% 97.3% % 91.6% 94.5% 93.5% 96.4% 1, % 89.6% 92.8% 91.9% 95.2% 1, % 82.7% 86.5% 86.1% 90.2% 1, % 79.1% 83.0% 83.0% 87.0% 1, % 76.5% 79.8% 80.5% 84.1% 2, % 72.7% 75.8% 77.0% 80.1% 2, % 68.2% 70.2% 72.6% 74.2% 3, % 64.7% 66.0% 69.0% 69.7% 4, % 61.0% 60.3% 64.4% 63.3% 5, % 59.8% 57.3% 61.2% 59.8% 7, % 61.7% 54.8% , % 70.1% 59.7% , % 64.6% 57.9% , % 57.1% 55.7% , % 41.8% 40.8% , % 46.1% 41.4% , % 44.3% 36.3% , % 41.3% 36.5% Values shown are in thousands. Lower Peak -- Higher Peak Greater than 80% of Max Figure Englebright Dam Hydrologic Zone Chinook salmon WUA results. Exh. E - Environmental Report Application for New License April 2014 Page E ,

143 Table Englebright Dam Hydrologic Zone steelhead WUA results. Discharge (cfs) Spawning 1 Steelhead WUA (sq ft) Fry No Cover 1 Juvenile No Cover 1 Fry Cover 1 Juvenile Cover 1 Spawning Fry No Cover Percent of Maximum WUA Juvenile No Cover Fry Cover Juvenile Cover % 100.0% 100.0% 100.0% 100.0% % 95.6% 97.0% 96.0% 98.1% % 92.8% 94.8% 93.2% 96.7% % 91.1% 93.4% 91.6% 95.7% 1, % 89.1% 91.6% 89.6% 94.4% 1, % 82.2% 84.7% 82.3% 88.9% 1, % 78.4% 81.2% 78.3% 85.9% 1, % 75.5% 78.0% 75.2% 83.1% 2, % 72.0% 74.1% 71.4% 79.3% 2, % 67.4% 69.3% 66.9% 74.5% 3, % 64.3% 65.4% 63.8% 70.5% 4, % 60.7% 60.0% 59.7% 64.9% 5, % 59.6% 56.8% 57.0% 61.2% 7, % 60.4% 54.3% , % 67.0% 60.2% , % 66.0% 58.2% , % 55.2% 56.6% , % 40.4% 40.6% , % 41.4% 41.9% , % 39.5% 37.1% , % 39.0% 37.1% Values shown are in thousands. Lower Peak -- Higher Peak Greater than 80% of Max Figure Englebright Dam Hydrologic Zone steelhead WUA results. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

144 Table Englebright Dam Hydrologic Zone rainbow trout adult, lamprey adult, and lamprey ammocoete WUA results. Discharge (cfs) Rainbow Trout and Lamprey WUA (sq ft) Rainbow Lamprey Trout Adult Adult Lamprey Ammocoetes Rainbow Trout Adult Percent of Maximum WUA Lamprey Adult Lamprey Ammocoetes , % 0.0% , % 0.0% , % 0.0% , % 0.0% -- 1, , % 0.0% -- 1, , % 0.0% -- 1, , % 0.0% -- 1, , % 0.0% -- 2, , % 0.0% -- 2, , % 0.0% -- 3, , % 0.0% -- 4, , % 0.0% -- 5, , % 0.0% -- 7, , % 18.0% -- 10, , % 34.5% -- 15, , % 62.6% -- 21, , % 100.0% -- 30, , % 28.1% -- 42, , % 16.3% -- 84, , % 0.0% , , % 1.8% -- Lower Peak -- Higher Peak Greater than 80% of Max Figure Englebright Dam Hydrologic Zone rainbow trout adult, and lamprey guild WUA results. Exh. E - Environmental Report Application for New License April 2014 Page E ,

145 Table Deer Creek Hydrologic Zone Chinook salmon WUA results. Discharge (cfs) Spawning 1 Chinook WUA (sq ft) Fry No Cover 1 Juvenile No Cover 1 Fry Cover 1 Juvenile Cover 1 Spawning Fry No Cover Percent of Maximum WUA Juvenile No Cover Fry Cover Juvenile Cover % 91.1% 82.4% 100.0% 98.3% % 88.2% 82.7% 98.2% 99.2% % 85.5% 82.6% 96.3% 99.6% % 83.0% 82.4% 94.6% 99.8% % 80.0% 81.9% 92.5% 100.0% % 77.5% 81.2% 90.7% 99.9% % 76.8% 80.9% 90.2% 99.7% % 74.1% 79.8% 88.0% 99.1% % 71.0% 78.2% 85.4% 98.1% % 68.7% 76.9% 83.5% 97.3% % 67.4% 76.1% 82.3% 96.7% 1, % 66.1% 75.1% 81.3% 95.9% 1, % 62.7% 71.2% 78.0% 92.9% 1, % 61.3% 69.2% 76.7% 91.3% 1, % 59.6% 67.0% 75.0% 89.4% 2, % 56.5% 63.7% 71.7% 86.0% 2, % 56.5% 61.3% 72.2% 83.8% 3, % 55.4% 59.0% 71.3% 81.3% 4, % 53.2% 55.7% 68.9% 77.7% 5, % 52.6% 53.7% 65.6% 74.8% 7, % 56.6% 55.8% , % 67.9% 64.5% , % 88.0% 82.4% , % 100.0% 100.0% , % 77.2% 87.5% , % 73.1% 85.6% , % 59.8% 62.9% , % 47.6% 50.1% Values shown are in millions. Lower Peak -- Higher Peak Greater than 80% of Max Figure Deer Creek Hydrologic Zone Chinook salmon WUA results. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

146 Table Deer Creek Hydrologic Zone steelhead WUA results. Discharge (cfs) Spawning 1 Steelhead WUA Fry No Cover 1 Juvenile No Cover 1 Fry Cover 1 Juvenile Cover 1 Spawning Fry No Cover Percent of Maximum WUA Juvenile No Cover Fry Cover Juvenile Cover % 92.9% 80.7% 100.0% 96.7% % 90.6% 81.4% 98.7% 97.9% % 88.3% 81.7% 97.2% 98.7% % 86.0% 81.7% 95.6% 99.2% % 82.9% 81.6% 93.5% 99.8% % 80.3% 81.3% 91.6% 100.0% % 79.5% 81.1% 91.0% 100.0% % 76.8% 80.3% 88.8% 99.7% % 73.5% 79.2% 86.1% 99.1% % 71.2% 78.3% 84.2% 98.6% % 69.8% 77.6% 83.0% 98.2% 1, % 68.2% 76.8% 81.6% 97.7% 1, % 64.4% 73.3% 77.9% 95.1% 1, % 63.1% 71.2% 76.5% 93.4% 1, % 61.3% 69.2% 74.6% 91.7% 2, % 58.3% 65.7% 71.4% 88.3% 2, % 58.1% 62.5% 71.2% 85.1% 3, % 56.7% 59.4% 69.9% 81.9% 4, % 54.7% 55.4% 67.9% 77.6% 5, % 53.7% 53.3% 65.4% 74.8% 7, % 58.5% 55.8% , % 70.1% 63.9% , % 87.9% 82.0% , % 100.0% 100.0% , % 77.2% 87.4% , % 69.8% 88.2% , % 50.2% 67.0% , % 38.2% 54.1% Values shown are in millions. Lower Peak -- Higher Peak Greater than 80% of Max Figure Deer Creek Hydrologic Zone steelhead WUA results. Exh. E - Environmental Report Application for New License April 2014 Page E ,

147 Table Deer Creek Hydrologic Zone rainbow trout adult, lamprey adult, and lamprey ammocoete WUA results. Discharge (cfs) Rainbow Trout and Lamprey WUA (sq ft) Rainbow Trout Adult Lamprey Adult Lamprey Ammocoetes Rainbow Trout Adult Percent of Maximum WUA Lamprey Adult Lamprey Ammocoetes 300 3,188,593 49, % 77.4% ,307,623 54, % 84.7% ,393,784 57, % 90.2% ,453,380 59, % 93.2% ,505,784 63, % 98.5% ,521,062 64, % 100.0% ,521,158 63, % 99.1% ,507,561 64, % 99.9% ,471,549 62, % 97.2% ,439,012 60, % 94.8% ,410,357 59, % 92.7% -- 1,000 3,374,219 57, % 90.1% -- 1,300 3,175,146 49, % 77.6% -- 1,500 3,045,111 45, % 71.3% -- 1,700 2,919,394 43, % 67.1% -- 2,000 2,726,870 41, % 64.2% -- 2,500 2,529,699 42, % 66.3% -- 3,000 2,385,364 46, % 72.2% -- 4,000 2,202,602 46, % 72.9% -- 5,000 2,107,623 41, % 65.2% -- 7,500 2,205,675 24, % 37.7% -- 10,000 2,411,230 13, % 21.2% -- 15,000 2,900,847 6, % 10.8% -- 21,100 3,760,411 7, % 12.4% -- 30,000 3,546,851 5, % 8.5% -- 42,200 3,999,134 4, % 6.9% -- 84,400 3,657,218 1, % 1.6% ,400 3,408,918 2, % 3.4% -- Lower Peak -- Higher Peak Greater than 80% of Max Figure Deer Creek Hydrologic Zone rainbow trout adult and lamprey adult WUA results. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

148 Table Dry Creek Hydrologic Zone Chinook salmon WUA results. Discharge (cfs) Spawning 1 Chinook WUA (sq ft) Fry No Cover 1 Juvenile No Cover 1 Fry Cover 1 Juvenile Cover 1 Spawning Fry No Cover Percent of Maximum WUA Juvenile No Cover Fry Cover Juvenile Cover % 67.5% 54.1% 96.9% 82.1% % 66.1% 54.6% 96.0% 83.3% % 64.6% 54.9% 94.9% 84.2% % 63.2% 55.0% 93.9% 84.9% % 61.2% 55.0% 92.4% 85.6% % 59.6% 54.9% 91.2% 86.0% % 59.1% 54.9% 90.8% 86.1% % 57.6% 54.7% 89.6% 86.5% % 55.7% 54.2% 87.9% 86.5% % 54.3% 53.8% 86.7% 86.4% % 53.5% 53.5% 85.9% 86.4% 1, % 52.9% 53.5% 85.7% 86.8% 1, % 49.4% 51.9% 82.3% 86.0% 1, % 48.3% 51.2% 81.9% 86.1% 1, % 47.2% 50.3% 81.0% 85.6% 2, % 47.2% 49.5% 81.8% 85.5% 2, % 46.9% 48.6% 82.2% 85.8% 3, % 51.6% 49.6% 88.8% 88.5% 4, % 58.4% 53.6% 98.1% 95.0% 5, % 61.9% 57.5% 100.0% 100.0% 7, % 71.4% 66.8% , % 86.9% 77.9% , % 100.0% 99.4% , % 89.3% 100.0% , % 61.1% 74.4% , % 49.8% 65.3% , % 33.6% 30.6% , % 40.1% 33.3% Values shown are in millions. Lower Peak -- Higher Peak Greater than 80% of Max Figure Dry Creek Hydrologic Zone Chinook salmon WUA results. Exh. E - Environmental Report Application for New License April 2014 Page E ,

149 Table Dry Creek Hydrologic Zone steelhead WUA results. Discharge (cfs) Spawning 1 Steelhead WUA (sq ft) Fry No Cover 1 Juvenile No Cover 1 Fry Cover 1 Juvenile Cover 1 Spawning Fry No Cover Percent of Maximum WUA Juvenile No Cover Fry Cover Juvenile Cover % 66.4% 50.3% 94.7% 80.7% % 65.5% 51.0% 94.3% 82.2% % 64.6% 51.6% 93.8% 83.4% % 63.7% 52.0% 93.2% 84.5% % 62.3% 52.4% 92.2% 85.6% % 61.3% 52.5% 91.6% 86.4% % 61.0% 52.6% 91.4% 86.6% % 59.8% 52.7% 90.4% 87.3% % 58.3% 52.5% 89.1% 87.7% % 57.2% 52.2% 88.1% 87.8% % 56.5% 52.0% 87.4% 87.8% 1, % 56.0% 52.2% 87.1% 88.5% 1, % 52.3% 51.1% 83.5% 88.4% 1, % 50.9% 50.4% 82.6% 88.5% 1, % 49.4% 49.3% 81.3% 87.7% 2, % 48.7% 48.1% 81.2% 87.0% 2, % 48.1% 47.1% 81.0% 87.0% 3, % 52.4% 47.5% 87.0% 88.7% 4, % 59.6% 50.4% 96.7% 94.4% 5, % 63.2% 54.1% 100.0% 100.0% 7, % 72.2% 64.3% , % 87.6% 74.1% , % 100.0% 95.6% , % 87.1% 100.0% , % 54.8% 72.7% , % 40.7% 64.1% , % 20.4% 33.5% , % 27.3% 34.7% Values shown are in millions. Lower Peak -- Higher Peak Greater than 80% of Max Figure Dry Creek Hydrologic Zone steelhead WUA results. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

150 Table Dry Creek Hydrologic Zone rainbow trout adult and lamprey adult and ammocoete WUA results. Discharge (cfs) Rainbow Trout and Lamprey WUA (sq ft) Rainbow Trout Adult 1 Lamprey Adult Lamprey Ammocoetes Rainbow Trout Adult Percent of Maximum WUA Lamprey Adult Lamprey Ammocoetes , % 56.3% , % 61.1% , % 65.1% , % 69.2% , % 73.4% , % 77.6% , % 79.7% , % 81.7% , % 87.2% , % 90.3% , % 91.3% -- 1, , % 93.6% -- 1, , % 97.4% -- 1, , % 99.1% -- 1, , % 100.0% -- 2, , % 99.2% -- 2, , % 95.8% -- 3, , % 92.7% -- 4, , % 91.2% -- 5, , % 97.4% -- 7, , % 85.5% -- 10, , % 45.9% -- 15, , % 14.6% -- 21, , % 9.8% -- 30, , % 4.1% -- 42, , % 2.8% -- 84, % 0.8% , , % 2.9% -- 1 Values shown are in millions. Lower -- Peak Higher Peak Greater than 80% of Max Figure Dry Creek Hydrologic Zone rainbow trout adult and lamprey adult WUA results. Exh. E - Environmental Report Application for New License April 2014 Page E ,

151 Table Daguerre Point Dam Hydrologic Zone Chinook salmon WUA results. Chinook WUA (sq ft) Percent of Maximum WUA Discharge (cfs) Spawning 1 Fry No Cover 1 Juvenile No Cover 1 Fry Cover 1 Juvenile Cover 1 Spawning Fry No Cover Juvenile No Cover Fry Cover Juvenile Cover % 62.0% 52.1% 92.6% 88.7% % 61.0% 53.1% 92.3% 90.9% % 59.1% 53.2% 91.0% 91.7% % 57.5% 53.2% 89.7% 92.2% % 55.1% 52.8% 87.6% 92.5% % 53.1% 52.3% 85.8% 92.5% % 52.5% 52.2% 85.3% 92.4% % 50.6% 51.5% 83.5% 92.2% % 48.5% 50.6% 81.6% 91.7% % 47.1% 49.8% 80.2% 91.2% % 46.3% 49.4% 79.5% 90.9% 1, % 45.8% 49.0% 79.4% 91.0% 1, % 43.3% 47.3% 77.8% 90.7% 1, % 44.8% 46.1% 80.5% 90.9% 1, % 44.0% 44.9% 79.9% 90.0% 2, % 43.5% 43.6% 79.7% 89.3% 2, % 43.8% 42.2% 80.8% 88.4% 3, % 45.6% 41.8% 84.0% 88.7% 4, % 52.7% 44.2% 96.0% 94.3% 5, % 57.5% 47.7% 100.0% 100.0% 7, % 65.2% 57.1% , % 76.9% 66.0% , % 97.5% 92.7% , % 100.0% 100.0% , % 75.0% 87.0% , % 71.9% 79.8% Values shown are in millions. Lower Peak -- Higher Peak Greater than 80% of Max Figure Daguerre Point Dam Hydrologic Zone Chinook salmon WUA results. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

152 Table Daguerre Point Dam Hydrologic Zone steelhead WUA results. Discharge (cfs) Spawning 1 Steelhead WUA (sq ft) Fry No Cover 1 Juvenile No Cover 1 Fry Cover 1 Juvenile Cover 1 Spawning Fry No Cover Percent of Maximum WUA Juvenile No Cover Fry Cover Juvenile Cover % 65.3% 50.0% 95.8% 87.5% % 64.4% 51.2% 95.7% 90.0% % 62.6% 51.6% 94.4% 91.3% % 60.9% 51.8% 93.0% 92.1% % 58.2% 51.7% 90.6% 92.9% % 55.9% 51.5% 88.4% 93.3% % 55.2% 51.4% 87.7% 93.4% % 52.9% 51.0% 85.5% 93.4% % 50.3% 50.3% 82.9% 93.2% % 48.5% 49.8% 81.1% 93.0% % 47.6% 49.4% 80.1% 92.9% 1, % 46.7% 49.2% 79.4% 93.2% 1, % 43.8% 47.9% 77.1% 93.5% 1, % 44.5% 46.4% 78.7% 93.3% 1, % 43.6% 45.2% 77.9% 92.3% 2, % 43.3% 43.7% 77.9% 91.4% 2, % 43.7% 41.9% 78.9% 89.9% 3, % 45.6% 40.9% 82.0% 89.3% 4, % 52.6% 42.4% 93.2% 93.5% 5, % 58.0% 45.7% 100.0% 100.0% 7, % 66.2% 55.7% , % 76.6% 65.1% , % 99.2% 92.0% , % 100.0% 100.0% , % 69.8% 88.0% , % 62.8% 79.4% Values shown are in millions. Lower Peak -- Higher Peak Greater than 80% of Max Figure Daguerre Point Dam Hydrologic Zone steelhead WUA results. Exh. E - Environmental Report Application for New License April 2014 Page E ,

153 Table Daguerre Point Dam Hydrologic Zone rainbow trout adult, and lamprey adult and ammocoete WUA results. Rainbow Trout and Lamprey WUA Discharge (cfs) Rainbow Trout Adult 1 (sq ft) Lamprey Adult 1 Lamprey Ammocoete 2 Rainbow Trout Adult Percent of Maximum WUA Lamprey Adult Lamprey Ammocoete % 78.1% 16.4% % 84.9% 16.0% % 90.2% 15.6% % 94.7% 15.4% % 97.8% 15.1% % 99.3% 15.0% % 100.0% 15.0% % 99.3% 15.0% % 98.5% 15.1% % 96.2% 15.1% % 94.6% 15.1% 1, % 91.6% 15.5% 1, % 78.7% 16.7% 1, % 70.6% 47.4% 1, % 63.4% 47.8% 2, % 54.7% 47.0% 2, % 45.1% 63.3% 3, % 40.3% 60.3% 4, % 39.6% 61.7% 5, % 46.9% 68.3% 7, % 35.8% 77.3% 10, % 15.1% 100.0% 15, % 9.3% 54.1% 21, % 7.7% 37.6% 30, % 5.9% 13.4% 42, % 4.1% 11.9% 1 Values shown are in millions. Lower Peak -- Higher Peak 2 Values shown are in thousands. Greater than 80% of Max Figure Daguerre Point Dam Hydrologic Zone rainbow trout adult, lamprey adult, and lamprey ammocoete WUA results. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

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155 Provided below is a brief description of WUA results by species and life stage. For Chinook salmon spawning, the WUA function was bimodal in all but the EDHZ. All higherpeak WUA occurred outside the active channel at 15,000, 21,100, 15,000, and 21,100 cfs for EDHZ, DeerHZ, DryHZ, and DPHZ, respectively. Lower-peak WUA within the active channel occurred at 800, 1,500-1,700; and 800 cfs in DeerHZ, DryHZ, and DPHZ, respectively. For Chinook salmon fry and juvenile with cover, the WUA function was unimodal in the EDHZ and the DeerHZ and bimodal in the DryHZ and DPHZ. For fry and juvenile with no cover, the WUA function was bimodal in all but the EDHZ. WUA peaked for fry and juvenile with cover in the active channel between 300 and 700 cfs. Outside of the active channel fry and juvenile with cover WUA peaked at 5,000 cfs. For Chinook salmon fry and juvenile with no cover, WUA peaked outside of the active channel between 15,000 and 21,100 cfs in the DeerHZ, DryHZ, and EDHZ. For steelhead spawning, the WUA function was bimodal for DeerHZ and DPHZ. The highest peaks were outside the active channel at 21,000, 42,200, 15,000, and 30,000 cfs, for EDHZ, DeerHZ, DryHZ, and DPHZ, respectively. Peaks in the active channel were at 2,500 and 1,700 for DeerHZ and DPHZ, respectively. For steelhead fry and juvenile with cover, the WUA function was unimodal in all but the DPHZ. For fry and juvenile with no cover, the WUA function was bimodal in all but the EDHZ. WUA peaked for fry and juvenile with cover in the active channel between 300 and 700 cfs. Outside of the active channel fry and juvenile with cover WUA peaked at 5,000 cfs. For steelhead fry and juvenile with no cover, WUA peaked outside of the active channel between 15,000 and 21,100 cfs in all but the EDHZ, which peaked within the active channel at 700 cfs. For rainbow trout adult, the WUA function was bimodal in all HZs. Active channel WUA peaks were at 700, 622, 700, and 622 cfs for EDHZ, DeerHZ, DryHZ, and DPHZ, respectively. In the EDHZ, the active channel peak was the main peak. A lower peak WUA outside the active channel occurred at 21,100 cfs at EDHZ. Main WUA peaks occurred outside the active channel at 42,200; 21,100; and 30,000 cfs for the DeerHZ, DryHZ, and DPHZ, respectively. Lower peaks of WUA within the active channel occurred at ; 700; and 622 cfs for the DeerHZ, DryHZ, and DPHZ, respectively. For Lamprey Guild adult, the WUA function was unimodal in all hydrologic zones except DPHZ. WUA peaked inside of the active channel at DPHZ, DeerHZ, and DryHZ at 622, 600, and 1,700 cfs respectively, with a secondary DPHZ peak at 5,000 cfs. WUA peaked outside the active channel for EDHZ at 21,100 cfs. For Lamprey Guild ammocoetes, habitat in the EDHZ, DeerHZ, and DryHZ does not exist due to the lack of suitable substrates (less than 2 mm). The only HZ where suitable combinations of sand and hydraulics exist is in DPHZ, where WUA for Lamprey Guild ammocoetes peaked at 10,000 cfs, with a secondary peak at 2,500 cfs, and a tertiary peak at 300 cfs. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

156 Because there had not been any previous instream flow studies for green sturgeon in the lower Yuba River, Study 7-10 and Study 7-9, Green Sturgeon Downstream of Englebright Dam, were the first studies to model (i.e., Study 7-10) and report (i.e., Study 7-9) green sturgeon spawning WUA in the lower Yuba River. Examination of relationships between streamflow at Marysville and green sturgeon spawning WUA (in pool morphological units) in the Yuba River downstream of Daguerre Point Dam demonstrates a steeply increasing positive linear relationship with flows up to about 5,000 cfs, a positive, yet lower rate of increase in WUA between about 5,000 and 10,000 cfs, and relatively little increase in spawning WUA at flows above 10,000 cfs. Examination of the relationship between Marysville flow and green sturgeon spawning WUA (in all morphological units) in the lower Yuba River downstream of Daguerre Point Dam demonstrates a steeply increasing positive linear relationship for flows up to 42,200 cfs. As previously discussed, the green sturgeon spawning WUA-discharge relationship within all morphological units (without restriction to the pool morphological units) likely represents the best available estimate of green sturgeon spawning WUA in the lower Yuba River downstream of Daguerre Point Dam. Spawning habitat duration analyses for the months corresponding to the potential spawning period (March through July) demonstrates the highest amounts of spawning WUA during the spring months (March through May). Tables and displays the amounts of green sturgeon spawning WUA (within pool morphological units, and within all morphological units, respectively) in the Yuba River downstream of Daguerre Point Dam. Estimated green sturgeon spawning WUA based on extrapolation for flows ranging from 50 cfs to 250 cfs, and from 84,400 cfs to 150,000 cfs are shaded. Table Flows at the Marysville Gage and North American green sturgeon spawning WUA relationships (in pool morphological units) in the Yuba River downstream of Daguerre Point Dam. Flow (cfs) WUA (sq. ft.) Flow (cfs) WUA (sq. ft.) Flow (cfs) WUA (sq. ft.) Flow (cfs) WUA (sq. ft.) ,319 2, ,726 42,200 1,814, ,676 2, ,530 84,400 1,864, ,896 3, , ,400 1,891, ,736 4,000 1,227, ,000 1,902, ,193 5,000 1,413, ,000 1,912, ,770 7,500 1,644, ,000 1,923, , ,246 10,000 1,696, ,000 1,934, , ,666 15,000 1,759, ,258 1, ,400 21,100 1,790, ,030 1, ,946 30,000 1,825, Table Flows at the Marysville Gage and North American green sturgeon spawning WUA relationships (in all morphological units) in the Yuba River downstream of Daguerre Point Dam. Flow (cfs) WUA (sq. ft.) Flow (cfs) WUA (sq. ft.) Flow (cfs) WUA (sq. ft.) Flow (cfs) WUA (sq. ft.) ,349 2,000 1,287,697 42,200 25,348, ,922 2,500 2,014,520 84,400 25,348, ,655 3,000 2,789, ,400 25,348, , ,026 4,000 4,268, ,000 25,348, , ,530 5,000 5,611, ,000 25,348, , ,004 7,500 7,973, ,000 25,348, ,310 1, ,850 10,000 9,441, ,000 25,348, ,658 1, ,132 15,000 12,192, Exh. E - Environmental Report Application for New License April 2014 Page E ,

157 Table (continued) Flow (cfs) WUA (sq. ft.) Flow (cfs) WUA (sq. ft.) Flow (cfs) WUA (sq. ft.) Flow (cfs) WUA (sq. ft.) ,193 1, ,604 21,100 15,068, ,222 1, ,088 30,000 19,926, Figures and display green sturgeon spawning WUA-discharge relationships (within pool morphological units, and within all morphological units, respectively) based on the green sturgeon spawning habitat suitability criteria, including the extrapolated WUA-discharge relationships (green line). Green Sturgeon Spawning WUA in Pool MUs (sq. ft.) 2,000,000 1,750,000 1,500,000 1,250,000 1,000, , , , ,000 40,000 60,000 80, , , , ,000 Marysville Flow (cfs) Calculated WUA-Discharge Relationship Extrapolated WUA-Discharge Relationship Figure Relationship between flows at the Marysville Gage and North American green sturgeon spawning WUA (in pool morphological units) in the Yuba River downstream of Daguerre Point Dam. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

158 30,000,000 Green Sturgeon Spawning WUA in All MUs (sq. ft.) 25,000,000 20,000,000 15,000,000 10,000,000 5,000, ,000 40,000 60,000 80, , , , ,000 Marysville Flow (cfs) Calculated WUA-Discharge Relationship Extrapolated WUA-Discharge Relationship Figure Relationship between flows at the Marysville Gage and green sturgeon spawning WUA (in all morphological units) in the Yuba River downstream of Daguerre Point Dam Amphibians This section provides an overview of all of the amphibian species that may occur in the Project Area, followed by specific information on ESA-listed and special-status amphibians. 30,31 Amphibians in stream reaches downstream of Project facilities are addressed first, then upstream of the Project on the Middle Yuba River, North Yuba River, and Oregon Creek. Distribution Overview Eight species of amphibians are known to occur or occurred historically in the Project Area (Table ). Six of the eight species are aquatic during at least some portion of their life cycle, associated with still or slow-flowing water, including parts of streams, ponds, and other lentic habitats. New Bullards Bar Reservoir and the two diversion impoundments are generally unsuitable for native amphibians because of deep water, steep shorelines and presence of predatory fishes. Two of the amphibian species are terrestrial salamanders without a free-living larval stage. Sierra Nevada ensatina (Ensatina eschscholtzii platensis) and California slender salamander (Batrachoseps attenuatus) are widespread and common species associated with forests, oak woodlands, and chaparral, where they are usually only encountered by active searching under rocks, logs, bark slabs, leaf litter, or other ground-cover objects. 30 For the purpose of this document, a special-status amphibian species is considered one that is: found on NFS land and listed by the Forest Service as Sensitive; listed by NMFS or USFWS as Species of Concern; listed by Cal Fish and Wildlife as a Species of Special Concern; or a combination of the above but not listed as threatened or endangered on the ESA. Species listed as endangered or threatened under the ESA are discussed separately in this document in Section No amphibians in the Project Vicinity are Proposed or a Candidate for listing under the ESA. Exh. E - Environmental Report Application for New License April 2014 Page E ,

159 Table Amphibian species reported from the Project vicinity. Common Name/ (1) General Distribution and Status Scientific Name (2) Observations (1) Widespread and common species, breeding in ponds, lakes, reservoirs, and streams mostly at low to middle elevations in forest and woodland areas. (2) Observed (often in large numbers) in and near Middle Yuba River below Our Sierra newt None House Diversion Dam; North Yuba below New Bullards Bar Dam and above New Taricha sierrae Bullards Bar Reservoir; Yuba River above New Colgate Powerhouse; Oregon Creek below and above Log Cabin Diversion Dam; and in five tributaries of New Bullards Bar Reservoir. (1) Widespread and common species that is terrestrial in all life stages; occurring mostly in forested habitats over a broad range of elevations (known from 1,300-5,300 Sierra Nevada ensatina None ft). Ensatina eschscholtzii platensis (2) No observations, but reported by Barry (2002) west of New Bullards Bar Reservoir. (1) Widespread and common species that is terrestrial in all life stages; occurring California slender salamander mostly in forested foothills and chaparral, occasionally to 3,000 ft El. None Batrachoseps attenuatus (2) No observations, but reported by Barry (2002) west of New Bullards Bar Reservoir. (1) Widespread and common species that occurs over a wide range of elevations; and breeds in ponds, lake and reservoir edges, ditches, and slow-moving or still sections of streams. Sierran treefrog (chorus frog) (2) Larvae were observed in connected or isolated side pools and backwaters areas; Pseudacris sierra 1 None and adults occasionally seen or heard on Middle Yuba River; North Yuba below New Bullards Bar Dam; Yuba River above New Colgate Powerhouse; Oregon Creek downstream and upstream of Log Cabin Diversion Dam; and wetlands near Dry Creek and Little Oregon Creek, both tributaries of New Bullards Bar Reservoir. (1) Widespread species that is terrestrial after metamorphosis and breeds in ponds, Western toad lake and reservoir edges, and slow-moving or still sections of streams across a wide Anaxyrus boreas 2 None range of elevations. (2) No observations, but reported by Barry (2002) west of New Bullards Bar Reservoir. (1) Nearly extirpated in the Sierra Nevada, this species formerly occurred on at least 30 drainages in the foothills (mostly below 3,500 ft elevation). Breeds in slowmoving or still sections of streams and ponds, usually where there is emergent and California red-legged frog FT, Rana draytonii 3 CSC aquatic vegetation. (2) No observations, but reported west of New Bullards Bar Reservoir (CDFG 2012). See Section for more information. (1) Occurs on small to large streams and rivers with pools, low-gradient riffles, and runs (smallest streams are usually only non-breeding habitat). Breeding sites usually in shallow, slow-flowing areas near the shore with coarse substrates (cobbles and Foothill yellow-legged frog FS-S, boulders). Most known occurrences are between 600 and 5,000 ft El. Rana boylii CSC (2) Observed and with evidence of breeding (eggs or larvae found) on Middle Yuba River below Our House Diversion Dam; North Yuba above New Bullards Bar Reservoir; and Oregon Creek below and above Log Cabin Diversion Dam. (1) Introduced and well established in slow-moving streams, stock ponds, lakes, and reservoirs. The presence of bullfrogs may be associated with declines of other native frogs. American bullfrog (2) Observed and with evidence of breeding (larvae often numerous) on Middle Yuba Lithobates catesbeianus 4 None River below Our House Diversion Dam; North Yuba below New Bullards Bar Dam, and Yuba River upstream of New Colgate Powerhouse. Also heard calling at Moran Cove on New Bullards Bar Reservoir and two juveniles found on Oregon Creek downstream of Log Cabin Diversion Dam. Sources: Jennings and Hayes 1994, Jennings 1996, Lannoo 2005, NatureServe 2012 FS-S = Forest Service Sensitive, CSC = California Species of Special Concern, FT = Federal Threatened, ST = State Threatened 1 Previously classified as Hyla regilla (Pacific treefrog) (see Recuero et al. 2006a, 2006b). Retention of the common name treefrog reflects longstanding, popular usage. 2 Previously classified as Bufo boreas (see Frost et al. 2006). 3 Previously classified as Rana aurora draytonii (see Frost et al. 2006). 4 Previously classified as Rana catesbeiana (see Frost et al. 2006). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

160 ESA-Listed Amphibians One ESA-listed amphibian species occurs in the Yuba River basin: the California red-legged frog (CRLF) (Rana draytonii), which is listed as threatened under the ESA. CRLF and Project effects on CRLF are discussed in Section Special-Status Amphibians Foothill yellow-legged frog (FYLF) (Rana boylii) is classified as a Species of Special Concern by Cal Fish and Wildlife and Sensitive by Forest Service. This is the only special-status amphibian species that may occur in the Project Area. Foothill Yellow-legged Frog (USFS-S & CSC) FYLF is a stream-adapted species usually associated with streams with backwater habitats and coarse substrates (Jennings and Hayes 1994). Currently known populations occur from about 91 to 1,525 m (600 to 5,000 ft) in elevation (Moyle 1973, Seltenrich and Pool 2002, ECORP Consulting, Inc. 2005). Populations of FYLF persist on at least some portions of most drainages with known historical occurrences, except in parts of southern California (NatureServe 2012). FYLF populations may require both mainstem and tributary habitats for long-term persistence. Streams too small to provide breeding habitat for this species may be critical as seasonal habitats, such as in winter, when flows are too high in mainstem streams; and during the hottest part of the summer, when small, heavily shaded streams may be cooler (Van Wagner 1996). Evidence suggests that habitat use by young-of-the-year, sub-adult, and adult frogs differs by age-class and can change seasonally (Randall 1997, Haggarty 2006). Breeding tends to occur in spring or early summer (Ashton et al. 1997). At one site in northwestern California studied for six years, the period of breeding activity varied in length from three to 7.5 weeks (Wheeler and Welsh 2008). Eggs are typically laid in areas of shallow, slow moving waters near the shore (Ashton et al. 1997). FYLF are infrequent in habitats where introduced fish and bullfrogs are present (Jennings and Hayes 1994). The native fish, Sacramento pikeminnow is also a predator of FYLF life stages other than eggs, particularly mid-stage tadpoles (Corum 2003). However, FYLF tadpoles may be most vulnerable to predation by introduced fish, such as smallmouth bass (Paoletti et al. 2011). Moyle (1973) suggested that American bullfrog (Lithobates catesbeianus) predation and competition was a proximate cause of FYLF range contraction in California. Kupferberg (1996, 1997) found that FYLF tadpoles were significantly less abundant in stream reaches where American bullfrogs occurred and showed experimentally that competition for food (algae) with large, second-year American bullfrog tadpoles (affecting growth and survival) and recently hatched first-year tadpoles (affecting survival) was likely responsible. Invasive American bullfrogs benefit from the presence of sunfish and bass, which prey upon dragonfly nymphs and other predators of American bullfrog tadpoles (Smith et al. 1999, Adams et al. 2003). In the Sierra Nevada, natural predators of FYLF include three species of garter snakes (Thamnophis Exh. E - Environmental Report Application for New License April 2014 Page E ,

161 spp.) and probably Sierra newt (Taricha sierrae). Predation by another newt species, roughskinned newt (Taricha granulosa), on FYLF eggs has been documented (Evenden 1948), and newts (T. granulosa or T. torosa [California newt]) are known to prey on eggs of California redlegged frog (Rathbun 1998). Predation by exotic signal crayfish (Pacifastacus leniusculus) on FYLF eggs and tadpoles has been documented (Wiseman 2004), although population-level significance of predation by crayfish is not known. The growth and development of FYLF tadpoles is closely related to water temperature. In experimental enclosures, FYLF tadpoles selected temperatures between 16.5 C and 22.2 C (mean=19.6 C ± 0.6 C) (Catenazzi and Kupferberg 2013). Kupferberg et al. (2013) found that tadpoles experienced highest survival to metamorphosis when the maximum average water temperature was 19.9 C, compared to tadpoles reared at C, 16.9 C, or 21.8 C. At the warmest temperature, tadpoles grew larger and metamorphosed earlier, but experienced higher rates of mortality, which may have been associated with heat stress. Parasitism by the copepod Lernaea cyprinacea (i.e., anchor worm ) is also most prevalent under warm water conditions (Kupferberg et al. 2009, Kupferberg et al. 2013). Potentially suitable habitats for FYLF occur in: 1) Middle Yuba River downstream of Our House Diversion Dam; 2) North Yuba River downstream of New Bullards Bar Dam; 3) Yuba River downstream of the confluence of the Middle and North Yuba rivers to New Colgate Powerhouse; 32 and 4) Oregon Creek downstream of Log Cabin Diversion Dam. Known existing information on the distribution of FYLF in these stream reaches is limited and does include any comprehensive surveys for amphibians. There are historical records of FYLF on the Middle Yuba River at about RM 12.4 (i.e., just downstream of Our House Diversion Dam) and near the confluence with Oregon Creek, and on two tributaries, Grizzly and Moonshine creeks. There are also records of FYLF along Oregon Creek, Log Cabin Diversion Dam Reach, and the Oregon Creek tributary, Mosquito Creek. None of the historical records provides evidence of FYLF breeding locations and there are no records for North Yuba River, New Bullards Bar Dam Reach, Yuba River, or tributaries of these stream reaches. New Bullards Bar Reservoir is not suitable habitat for FYLF, but FYLF occurs on some of the tributaries to the reservoir, including Little Oregon, Bridger, and Willow creeks (Barry 2002, USFS 2011). To supplement existing information, YCWA performed habitat assessments and surveys under Study 3.4 and 3.13, and habitat modeling for FYLF under Study 3.5, which are described below. Foothill Yellow-legged Frog Surveys In accordance with Study 3.4, YCWA assessed habitats and performed standard visual encounter survey (VES) for FYLF at ten sites on stream reaches that may be affected by Project flows and two sites where flows are not affected: on the North Yuba River upstream of New Bullards Bar Reservoir and on Oregon Creek upstream of Log Cabin Diversion Dam Impoundment. Surveys were performed in 2011 at Oregon Creek sites, but because of unusually prolonged high spring 32 The Yuba River below New Colgate Powerhouse is below 600 feet (ft) in elevation and thus outside of the known or expected distribution of FYLF. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

162 flows on other stream reaches in 2011, surveys of all other sites occurred in The survey sites (Figure ) were determined collaboratively, with agreement on site locations between YCWA and Relicensing Participants. YCWA also performed FYLF surveys at two sites in 2013 under Study 3.13 the results of which are also described below. Exh. E - Environmental Report Application for New License April 2014 Page E ,

163 Figure Foothill yellow-legged frog survey site locations. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

164 Middle Yuba River Downstream of Our House Diversion Dam Two FYLF survey sites representing a total distance of 1.2 mi were located between Our House Diversion Dam and the confluence of Oregon Creek, MYR-4 just below Our House Diversion Dam and MYR-3B extending nearly one mile upstream from Oregon Creek. Three sites representing a distance of 1.15 mi were located between Oregon Creek and the confluence of the North Yuba River. MYR-3A extended about 0.3-mi downstream from the confluence of Oregon Creek, MYR-2 was situated at the confluence of Yellowjacket Creek, and MYR-1 extended 0.25-mi upstream of the North Yuba River. The survey results at the sites in Our House Diversion Dam Reach included no FYLF egg masses; however, there were detections of all other FYLF life stages during surveys, indicating that breeding had occurred (Table ). Downstream of the confluence of Oregon Creek, FYLF breeding was documented only at the confluence site. There were no FYLF survey detections at the other two sites and only one incidental observation from another YCWA study of FYLF at one of the sites (MYR-2). In response to this detection, YCWA surveyed the adjacent tributary, Yellowjacket Creek, in 2013; however, no FYLF were found. Yellowjacket Creek is a small stream lacking suitable FYLF breeding habitat. Table Summary of FYLF surveys and other information regarding the distribution of FYLF in the Middle Yuba River downstream of Our House Diversion Dam. Survey Summary and Incidental Observations MIDDLE YUBA RIVER, OUR HOUSE DIVERSION DAM REACH: SITES MYR-3B AND MYR-4 FYLF, including tadpoles, found at both survey sites and observed incidentally elsewhere on the reach. A total of 23 metamorphosed young-of-year FYLF were documented at Site MYR-3B, but only one was found at Site MYR-4. Large numbers of Sierra newts were observed during surveys and incidentally, especially at Site MYR-3B, along with moderate numbers of American bullfrogs at Site MYR-3B and one observation at Site MYR-4. Potential FYLF Breeding and Rearing Habitat at Survey Sites Potential habitat was abundant in Site MYR-3B, associated with slow moving water in pool tail-outs, and shallow edgewater throughout the reach. In Site MYR-4, potential habitat occurred in areas of lowvelocity edgewater along run and glide sections. MIDDLE YUBA RIVER, OREGON CREEK REACH: SITES MYR-1, MYR-2, AND MYR-3A; AND YELLOWJACKET CREEK FYLF found during surveys only at Site MYR-3A, where there were two detections, a juvenile and egg mass. At Site MYR-2, one adult FYLF was observed incidentally. No young-of-year FYLF were documented at survey sites, but six juveniles, likely including metamorphosed young-of-year, were observed in another part of the reach near Moonshine Creek in August Detections of Sierra newts were numerous during surveys at Site MYR-2 and there were large numbers of American bullfrogs at each site. Crayfish were found at Site MYR-3A. Juvenile American bullfrogs were found in Yellowjacket Creek during Study Potential habitat was most common in Sites MYR-2 and MYR-3A, which both had slow-moving water in pool tail-outs, and areas of shallow edgewater throughout. In Site MYR-1 potential habitat is limited to parts of the right bank and included low gradient riffles, runs and glides, backwater pools, with edgewater mostly concentrated at the downstream end of the site. Other amphibians detected during surveys were Sierra newt, Sierran treefrog (Pseudacris sierra), and American bullfrog. Adult Sierra newts were particularly abundant at Site MYR-3B and MYR-2. American bullfrog tadpoles were found in pool habitat at Site MYR-3B and were the most commonly detected amphibians at sites downstream of Oregon Creek and particularly abundant at Site MYR-2 and MYR-3A. Sierran treefrog tadpoles were found at each of the Middle Yuba River sites except MYR-1. Based on the developmental stages of FYLF tadpoles found during surveys in 2012, water temperature data, and observations from other streams, FYLF breeding in the Middle Yuba River Exh. E - Environmental Report Application for New License April 2014 Page E ,

165 downstream of Our House Diversion Dam may have begun on about May 1 and concluded by mid-may. An earlier brief warm period, which peaked on April 21 with a water temperature of about 15 C before dropping again, could also have triggered limited breeding, although this was not confirmed by the survey results. North Yuba River Downstream of New Bullards Bar Dam One FYLF survey site, 0.55-mi-long, was situated in the North Yuba River extending up from the confluence with the Middle Yuba River. The only amphibians found during surveys at the site or reported from the reach as incidental observations from other studies were Sierra newt, American bullfrog, and Sierran treefrog (Table ). Potential habitat for FYLF is scarce. Table Summary of FYLF surveys and other information regarding the distribution of FYLF in the North Yuba River downstream of New Bullards Bar Dam at Site NYR-1. Survey Summary and Incidental Observations Potential FYLF Breeding and Rearing Habitat at Survey Site No FYLF found during surveys or observed incidentally. Moderate Potential habitat is scarce and limited to pool tail-outs and some numbers of detections of American bullfrog and Sierra newt occurred shallow edgewater associated with mid-channel pools. Substrate is during surveys. Sierran treefrog tadpoles and juveniles also found. mostly bedrock and massive boulders. Yuba River Downstream of the Middle Yuba/North Yuba Confluence Two FYLF survey sites, representing a distance of 0.7 mi were located in the Middle/North Yuba River Reach of the Yuba River under Study 3.4, Site YR-1 situated about 0.37 mi upstream of New Colgate Powerhouse and YR-2 just downstream of the confluence of the North Yuba River. American bullfrog tadpoles were numerous at the survey sites and bass occurred throughout YR-2 (Table ). There were no survey detections of FYLF at the survey sites and no reported incidental observations from other studies of FYLF in the reach. Surveys for FYLF were performed again in 2013 under Study 3.13 at Site YR-2A, which included Site YR-2, but expanded to about 0.12mi-long. The surveys were performed in summer when flows were low to allow for increased survey accessibility. Once again, there were no detections of FYLF. Established FYLF populations likely do not occur in this reach. Because there are no apparent barriers to dispersal at lower flows, individual FYLF may nonetheless occur infrequently. Table Summary of FYLF surveys and other information regarding the distribution of FYLF in the Yuba River downstream of Middle Yuba/North Yuba Confluence at Sites YR-1, YR-2, and YR-2A. Survey Summary and Incidental Observations Potential FYLF Breeding and Rearing Habitat at Survey Sites No FYLF found during surveys or observed incidentally. American bullfrog detections were numerous at the survey sites, with larvae more abundant at Site YR-1. The only observations of Sierra newt were two adults observed incidentally on the stream bank in January 2012 at Site YR-1. One Sierran treefrog tadpole was found at YR-1. Crayfish were also found at the sites. Potential habitat is limited in extent at the survey sites. In Site YR-2 potential habitat was associated with a single main-channel pool and tail-out. Within the expanded Site YR-2A, the only additional potential habitat for FYLF was associated with edgewater in the higher gradient section downstream of the pool. Potential habitat in Site YR-1 was associated with a low-gradient riffle and mid-channel pool at the downstream end of the site. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

166 Oregon Creek Downstream of Log Cabin Diversion Dam Two FYLF survey sites were located in Oregon Creek downstream of Log Cabin Diversion Dam, Site OC-1 situated at the confluence of the Middle Yuba River (0.6-mi-long) and OC-2 in Celestial Valley (0.65-mi-long). The survey results did not include egg mass detections; however, a small number of tadpoles were found at Site OC-2, indicating that breeding had occurred (Table ). There were FYLF detections at both survey sites and incidental observations were reported from other studies throughout the reach. Breeding locations may be scattered, particularly in low gradient sections, such as in Celestial Valley. Incidental observations suggest that more young-of-year FYLF occurred in 2009 and 2012 than in Table Summary of FYLF surveys and other information regarding the distribution of FYLF in Oregon Creek downstream of Log Cabin Diversion Dam at Sites OC-1 and OC-2. Survey Summary and Incidental Observations Potential FYLF Breeding and Rearing Habitat at Survey Sites FYLF found at both survey sites and observed incidentally elsewhere on the reach. Small numbers of tadpoles were found at Site OC-2. No metamorphosed young-of-year were observed during the surveys; Potential habitat present throughout both sites associated with lowvelocity edgewater areas along mid-channel pools and low-gradient however, young-of-year were noted incidentally at scattered locations during other studies in 2009 and There were numerous riffles. detections of Sierra newts during the surveys at both sites. Two postmetamorphic Sierran treefrogs were detected at OC-2. Crayfish were found at Site OC-1. FYLF breeding in Oregon Creek downstream of Log Cabin Diversion Dam in 2011 probably occurred in June. Water temperatures in the Log Cabin Diversion Dam Reach held favorable for breeding by the first week of June. Upstream of the diversion dam, FYLF egg masses, some less than one week old, were found during the June 15 survey. Upstream of the Project Existing information regarding FYLF in the Middle Yuba River upstream of Our House Diversion Dam Impoundment is derived from surveys performed in 2008 as a relicensing study for the Yuba-Bear Hydroelectric Project (PG&E and NID 2011) (Table ). Site MY-2 in that study was located approximately 305 m upstream of Our House Diversion Dam Impoundment. Study 3.4 survey sites were located on the North Yuba River upstream of New Bullards Bar Reservoir (one site, 0.65-mi-long, surveyed in 2012) and Oregon Creek upstream of Log Cabin Diversion Dam Impoundment (one site, 0.55-mi-long, surveyed in 2011). In addition, Study 3.14 incidentally documented adult and juvenile FYLF in the Middle Yuba River upstream of Our House Diversion Dam Impoundment to about 305 m upstream of the FERC Project Boundary on August 6, On October 18, 2013 during a site visit to Log Cabin Diversion Dam with Cal Fish and Wildlife and Forest Service staff, YCWA observed young-of-year FYLF in Oregon Creek as close as 100 m from the dam, and up the reach to the Lohman Ridge Tunnel. Under low flow conditions on that date, numerous FYLF occurred, mostly along the edges of the stream and in the surrounding sediments. Exh. E - Environmental Report Application for New License April 2014 Page E ,

167 Table Summary of FYLF surveys and other information regarding the distribution of FYLF upstream of Project facilities on the Middle Yuba River, North Yuba River, and Oregon Creek. Survey Summary and Incidental Observations Potential FYLF Breeding and Rearing Habitat at Survey Sites MIDDLE YUBA RIVER, UPSTREAM OF OUR HOUSE DIVERSION DAM IMPOUNDMENT: SITE MY-2 (NID AND PG&E 2011) Site MY-2 was surveyed in Relatively large numbers of adult and Potential breeding and rearing habitat is abundant throughout site, juvenile FYLF were detected during surveys, along with 18 egg masses generally associated with shallow edgewater bordering low relief and large numbers of early-stage (n=777) and late-stage tadpoles cobble bars. Low gradient with numerous low-relief lateral and point (n=438). Large number of metamorphosed young-of-year found bars in lower half of site, which is largely a depositional area. (n=397). Cobble/gravel bars are derived from colluviums and mining activities. NORTH YUBA RIVER, UPSTREAM OF NEW BULLARDS BAR RESERVOIR: SITE NPNYR-1 Few adult or juvenile FYLF (n=4) were detected during surveys; however, 21 egg masses were found, associated with low-gradient riffles, a run, and main-channel pool. A decreasing number of tadpoles were found on each survey, and a total of eight metamorphosed youngof-year on the last survey. No other amphibians were found. Incidental observations included crayfish. Potential breeding and rearing habitat is present throughout site, including low gradient riffles and pools in the main channel and side channels, boulder and sedge pools, and pool tail-outs in the margin and edgewater areas. OREGON CREEK, UPSTREAM OF LOG CABIN DIVERSION IMPOUNDMENT: NPOC-1 Relatively small numbers of adult and juvenile FYLF and at least 21 egg masses were found at the site associated with two macrohabitats, a main channel pool and a run. Few late stage tadpoles were found and only one metamorphosed young-of-year. Adult Sierra newts and egg masses were also detected. Sierran treefrog tadpoles were detected in isolated pools. Potential breeding and rearing habitat is concentrated in lower 0.2 mi of the site, concentrated in pool tail-outs and low-gradient riffles, although boulder and bedrock pools also provide potential breeding and rearing habitat. Trout are common, with all size classes observed in edgewater areas. Foothill Yellow-Legged Frog Habitat Modeling 33 In accordance with Study 3.5, YCWA performed River 2D (i.e., 2 dimensional) habitat modeling to simulate the relationship of stream flows to FYLF habitat suitability defined by water depth and velocity, and substrate for a site on each of two stream reaches where FYLF breeding is known to occur: Middle Yuba River, Our House Diversion Dam Reach at RM 12.4, 0.2 mi downstream of Our House Diversion Dam; and Oregon Creek, Log Cabin Diversion Dam Reach RM 3.4, 0.9 mi downstream of Log Cabin Diversion Dam. Two sites were selected in collaboration with Relicensing Participants. One site was in Oregon Creek and extended from RM 3.3 to RM 3.4, and included approximately 813 sq m. The second site was located in the Middle Yuba River and extended from approximately RM 12.4 to RM 12.5, and included approximately 3,251 sq m. In the spring of 2013, YCWA collected all field data, including topographic and hydraulic measurements, at each site at three calibration flows. In total, 12,964 and 23,256 topographic data points were collected on Oregon Creek and the Middle Yuba River, resulting in data point densities of 0.65 m and 0.52 m for Oregon Creek and Middle Yuba River, respectively. Data were verified in Microsoft Excel to ensure that there were no obvious elevation errors in the 33 Since the River 2D Model uses meters instead of feet, all data in this section are presented in meters. When possible, the equivalent in feet is provided. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

168 survey data. Once initial quality control measures were completed, topographic data were entered into ArcGIS for the development of a Triangulated Irregular Network (TIN). The TIN was then imported to ArcScene for a visual verification of the topographic data. Data were modeled using River2D, a 2D, depth averaged finite-element model (Stefflar and Blackburn 2002). The final Oregon Creek mesh had 5,769 computational nodes and 11,236 mesh elements yielding 2.16 computation nodes per square meter while the final Middle Yuba River mesh had 23,080 computational nodes and 45,547 mesh elements yielding 6.25 computation nodes per square meter. The final mesh for Oregon Creek had a minimum triangle quality (QI) of The final mesh for the Middle Yuba River had a minimum triangle quality (QI) of Hydraulic models were calibrated using bed roughness (Ks) and groundwater transmissivity (TR) adjustments. Calibration results were then compared to validation data including water surface elevation (WSE) data, downstream boundary discharge, velocity, and depth measurements. Validation tolerance thresholds of twice the average error for each model parameter were applied to each of the three calibration flows. On Oregon Creek, 841 WSE, velocity and depth validation measurements were taken during the calibration flow data collection periods. Of those, the calibrated Oregon Creek hydraulic model simulated each parameter within greater than 88 percent of the established threshold criteria. On the Middle Yuba River, 676 WSE, velocity and depth validation measurements were taken during the calibration flow data collection periods. Of those, the calibrated Middle Yuba River hydraulic model simulated each parameter within greater than 90 percent of the established threshold criteria. Rating curves for each study site were developed using field measurements collected during each of the three calibration surveys. These measurements were further validated through the careful evaluation of stage data from numerous deployed Onset Hobo U-20 pressure transducers and compared rating curves developed at co-located PHABSIM transects for Study HSC recently used by NID in the relicensing of its Yuba-Bear Hydroelectric Project was used for both the Oregon Creek and Middle Yuba River study sites. FYLF egg mass and tadpole habitat data collected on Oregon Creek during surveys conducted in the spring of 2011 and 2012 for Study 3.4 were examined to determine if unique habitat suitability curves were warranted or changes should be made to the proposed FYLF HSCs. After a thorough examination, it was determined that the development of unique FYLF HSC for Oregon Creek was not warranted. Simulation flows to be modeled in each study site were selected in collaboration with the Relicensing Participants based on review of the hydrologic records downstream of Log Cabin Diversion Dam and Our House Diversion Dam. Simulation flows in Oregon ranged from 0.14) to cubic meters per second (cms)( cfs) while simulation flows ranged from 0.59 cms to cms ( cfs). Exh. E - Environmental Report Application for New License April 2014 Page E ,

169 In collaboration, Relicensing Participants identified areas of interest (AOI) regions from which simulation analyses would be conducted. The average change in water surface elevation for each simulation discharge for the AOI regions and the site averages for Middle Yuba River and Oregon Creek are presented below in Table and , respectively. Table Change in water surface elevations (ft) summarized by AOI region for the Middle Yuba River model domain. Discharge Area of Interest Region Site cfs cms A B C D E F G H I Average , , , Table Change in water surface elevations (ft) summarized by AOI region for the Oregon Creek model domain. Discharge Area of Interest Region Site cfs cms A B C D E Average April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

170 The distribution of suitable habitat in the Middle Yuba River model domain for both life stages of FYLF tended to be on the near-shore margins, where shallow, slow water conditions exist or behind large boulders which create suitable velocity conditions. The majority of the main channel in this section of the Middle Yuba River surveyed for this study was generally deeper than the suitable depth range (i.e., m) for the FYLF egg mass life stage. Similarly, main channel depths generally exceeded the FYLF tadpole depth range (i.e., m). However, as was observed during surveys conducted in support of Study 3.4, the incidental observations recorded during Study 3.10 and the conduct of this study, the boulder dominated and heavily vegetated margin on the northern river margin (i.e., river right looking downstream) provides sufficient habitat for adult and tadpole FYLF. Along the vegetated stream margin on river right, habitat is recruited incrementally at each increasing simulation flow due to the inundation of shallow, slow water. Despite the inundation of the shallow right bank, the rate of recruitment, and therefore the overall amount of available habitat, diminishes at each successive simulation flow. This trend is due to a shift of suitable velocity and depths over boulder and cobble substrate to areas dominated by sand which occupies much of the vegetated right bank. Incremental decreases in discharge at the Middle Yuba River study site produced a general trend of increasing areas of egg mass and tadpole suitability. The locations of suitable habitat also follow the decreasing flow as it recedes. For example, at high flows (i.e., above 17 cms [600 cfs]) there are still a small areas of suitable habitat on the left bank ascending in the vegetated riparian zone and on right bank ascending in some areas behind large boulders. Areas of tadpole suitability track similarly to egg mass suitability except the tadpole areas of suitability are even less extensive. Figures and below present the combined suitability for FYLF egg mass and tadpole life stages, respectively. Exh. E - Environmental Report Application for New License April 2014 Page E ,

171 Figure Egg mass combined suitability output from the Middle Yuba 2D model for three simulation flows. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

172 Figure Tadpole combined suitability output from the Middle Yuba 2D model for three simulation flows. Exh. E - Environmental Report Application for New License April 2014 Page E ,

173 The distribution of suitable habitat in the Oregon Creek site for both life stages of FYLF tended to be near shore margins, where shallow, slow water conditions exist or behind large boulders which create suitable velocity conditions. A significant amount of habitat for both the egg mass and tadpole life stages exists in both pool tail habitats at the lower flows. Habitat exists in the main channel at lower flows; however, most suitable locations are on the margins and in sheltered areas around boulders. While there is a general decrease in suitable area with increases in flow, there is a short reversal of this trend between 5.66 cms (200.0 cfs) and 7.08 cms (250.0 cfs). The reason for this trend is recruitment of new habitat due to the inundation of the lateral boulder/cobble bar on the right bank ascending near the bottom of the site. Figures and show FYLF egg mass and tadpole habitat suitability at three flows, from 0.4 cms (14.1 cfs) to 2.76 cms (97.6 cfs). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

174 Page Left Blank Exh. E - Environmental Report Application for New License April 2014 Page E ,

175 Figure Egg mass combined suitability output from the Oregon Creek 2D model for three simulation flows. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

176 Figure Tadpole combined suitability output from the Oregon Creek 2D model for three simulation flows. Exh. E - Environmental Report Application for New License April 2014 Page E ,

177 Incremental decreases in discharge at the Oregon Creek site produces a general trend of increasing areas of egg mass and tadpole suitability as the flow drops. The locations of suitable habitat also follow the decreasing flow as it recedes. For example, at high flows (i.e., above 5.66 cms) there are still a small areas of suitable habitat on the left bank ascending of the pool, while the most suitable habitat is found on the boulder/cobble floodplain on the right bank ascending of the bottom of the site. As the flow drops, the boulder/cobble bar dewaters, eliminating the habitat while the pool habitat and right bank ascending of the run near the bottom of the site increase in suitability. The left channel ascending of the split becomes increasingly suitable as flow decreases until they reach between 0.28 cms and 0.14 cms where the side channel becomes dewatered. Areas of tadpole suitability track similarly to egg mass areas of suitability except that at higher flows, suitable habitat on the right bank ascending boulder/cobble floodplain is more limited. WUA for each site was calculated at all simulation flows for the egg mass and tadpole life stages. On Oregon Creek and the Middle Yuba River, WUA generally shows a decreasing trend as flows increase as shown in Figure However, the rate of change in the amount of suitable habitat slows after reaching flows of 3.54 cms (125.0 cfs) on Oregon Creek and 7.08 cms (250.0 cfs) on the Middle Yuba River WUA (m 2 ) Discharge (cfs) Middle Yuba Egg Mass Middle Yuba Tadpole Oregon Creek Egg Mass Oregon Creek Tadpole Figure WUA for FYLF egg mass and tadpole life stages in the Oregon Creek and Middle Yuba River study sites. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

178 Aquatic Turtles Only one freshwater turtle species, western pond turtle (WPT) (Actinemys marmorata) is native to California. This section provides general information regarding this species, which is considered a sensitive species by the Forest Service, followed by information on the distribution of WPT in the Project Vicinity. The Project impoundments are addressed first, followed by stream reaches downstream of Project facilities, and then upstream of the Project on the Middle Yuba River, North Yuba River, and Oregon Creek. Introduced species of turtles in California include painted turtle (Chrysemys picta) and red-eared slider (Trachemys scripta elegans), although there are no known reports of these species in the Project Vicinity. WPT occurs in a wide variety of aquatic habitats, including low-velocity regions of permanent streams, ponds, and lakes. Adults may also use seasonal streams or ponds when available. To attain suitable body temperature ( thermoregulate ), individuals engage in basking behavior upon emergent large woody debris, overhanging vegetation, rock outcrops, or mats of submerged vegetation. Oviposition (egg-laying) sites or nests are shallow, soil-covered excavations and have been found in locations that are relatively sunny, well-drained, and proximate to aquatic habitat. Factors limiting population distribution and abundance may be the availability of terrestrial areas suitable for nesting, aquatic habitats suitable for hatchlings (i.e., warm, shallow water with ample hiding cover in the form of dense submerged or short emergent vegetation), and basking sites for juveniles and adults (Jennings and Hayes 1994, Buskirk 2002). Population recruitment may be low in some areas because of low hatching success and survivorship of juveniles. According to Holland (1991) viable populations of WPT do not occur in reservoirs larger than 2-3 hectares, where predation by introduced centrarchid fishes (especially largemouth bass) and American bullfrog upon hatchlings can be high (Holland 1991). Within large, deep reservoirs, WPT may seek protected, south-facing coves with shallower water (Rosenberg et al. 2009). Western Pond Turtle Surveys To supplement existing information, YCWA s Study 3.6 included habitat assessments, mapping, and surveys for WPT, which are described below. YCWA reviewed existing and readily available sources to identify areas of potentially suitable aquatic habitat and nesting habitat for WPT based on the description of habitat elements in the scientific literature. Potential WPT nesting habitat was identified and mapped remotely using GIS, based on certain attributes associated with known WPT nest sites, including distance from aquatic habitats, percent slope, aspect, and soil type (Holland 1991, PG&E and NID 2008). This was a coarse-scaled approach that demonstrated that potential nesting habitat occurred to varying extents on the stream reaches, but was scarce on Oregon Creek, and occurred abundantly around New Bullards Bar Reservoir, but was scarce on Our House and Log Cabin diversion dam Exh. E - Environmental Report Application for New License April 2014 Page E ,

179 impoundments. Further analyses or conclusions are not warranted. No WPT nests were found incidentally. In the field, YCWA conducted field reconnaissance in 2011 to assess habitat conditions and identify locations for WPT surveys at New Bullards Bar Reservoir, Our House Diversion Dam Impoundment, Log Cabin Diversion Dam Impoundment, and selected stream reaches. YCWA performed surveys in 2012 using binoculars and spotting scopes to detect basking WPT from fixed locations. Sites on New Bullards Bar Reservoir and stream reaches were each surveyed twice and sites at Our House Diversion Dam Impoundment and Log Cabin Diversion Dam Impoundment were each surveyed on three dates, with two of the survey visits occurring when water was being diverted into the respective diversion tunnels. The field reconnaissance and survey locations, locations of incidental sightings, and historical data are shown in Figure April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

180 Page Left Blank Exh. E - Environmental Report Application for New License April 2014 Page E ,

181 Figure Locations of WPT field reconnaissance and survey detections, incidental observations, and existing records. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

182 Figure (continued) Exh. E - Environmental Report Application for New License April 2014 Page E ,

183 New Bullards Bar Reservoir At New Bullards Bar Reservoir, existing information from review of Forest Service records and other sources included observations of WPT at Moran Cove, Garden Point, Tractor Cove (i.e., east of Garden Point), and the mouth of Indian Creek. YCWA surveyed six sites at New Bullards Bar Reservoir and detected WPT at Moran Cove, Tractor Cove, and Willow Cove (i.e., near mouth of Willow Creek) (Table ). All of the survey detections were adults or subadults larger than 15 cm carapace length. The greatest number of detections was at Willow Cove, where there were detections during basking platform deployment (n=3), the first survey (n=3), and the second survey (n=1). There were also incidental observations from other studies of WPT at Willow Cove and Tractor Cove. There were no WPT detections at the survey site in the north arm of the reservoir, where there are also no historical records of WPT. The study results indicated that New Bullards Bar Reservoir contained relatively few areas with habitat features potentially attractive to WPT and persistent with seasonal changes in water surface elevation. Downed wood, shoreline vegetation, and banks suitably oriented for basking when exposed and underwater hiding cover when submerged, were primarily associated with tributary inlets. At these locations, patches of willows (Salix spp.) below the NMWSE occurred, potentially providing both basking substrates and underwater hiding cover, depending on water surface elevation. Other features of some suitable sites included areas of shoreline erosion and resulting partially submerged large woody material, and moderate or gentle slopes where relatively shallow water would occur. Vegetated, shallow water areas necessary for hatchling WPT occurred infrequently at New Bullards Bar Reservoir and were limited to the mouths of some tributaries. Table Summary of WPT basking surveys results. Location/UTM coordinates Willow Cove UTM E N ) Tractor Cove UTM E N South of Tractor Cove UTM E N East of Garden Point UTM E N Garden Point UTM E N Near Alabama Bar UTM E N Moran Cove UTM E N Moran Cove UTM E N WPT: Basking Survey Comments Number/Lifestage/Date NEW BULLARDS BAR RESERVOIR 3 adult (5/29/12) 1 adult (7/11/12) No detections (5/29/12) 1 adult (7/11/12) No detections (5/31/12) No detections (6/6/12) No detections (5/31/12) No detections (6/6/12) No detections (5/31/12) No detections (6/6/12) No detections (6/1/12) No detections (6/8/12) No detections (6/1/12) 1 adult (6/8/12) No detections (6/1/12) 2 adults (6/8/12) Site was in cove near mouth of Willow Creek and another small stream. WPT were basking on downed wood, including an inclined, partially submerged log. On 7/11/12 WPT had evidently just emerged from the water and returned to the water after basking. Recreational anglers and boaters were briefly present during surveys. Site was near mouth of two small perennial tributaries. WPT was observed swimming in clump of submerged willows. No disturbances during either survey. Site on east-facing shore of peninsula. Small pontoon boat crossed in front of survey area just before end of first survey. Site is between two small south-facing coves. Wakes from motor boats caused site disturbance which delayed the start of first survey, and re-occurred during survey. Site is at south-facing cove east of campgrounds. Motor boats were passing nearby for the majority of the first survey. Site is near mouth of a perennial tributary. Motor boat passed near survey site during last quarter of second survey. Site is near the mouth of Little Oregon Creek. WPT was observed on floating log in southwest corner of cove. Recreationists in area briefly at start of first survey. Site is near the mouth of Little Oregon Creek. One WPT was observed on floating log and the other was in the water. No disturbances during either survey. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

184 Table (continued) Location/UTM coordinates UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N UTM E N WPT: Basking Survey Comments Number/Lifestage/Date OUR HOUSE DIVERSION DAM IMPOUNDMENT No detections (5/22/12) No detections (6/7/12) No detections (7/13/12) No detections (5/22/12) No detections (6/7/12) No detections (7/13/12) No detections (5/22/12) N.A. (6/7/12) No detections (7/13/12) No detections (5/22/12) No detections (6/7/12) No detections (7/13/12) Site included the downstream half of the impoundment. No disturbances during the surveys. Site included the downstream half of the impoundment. No disturbances during the surveys. Site included the upstream half of the impoundment. Recreationists approached cobble bar at upstream end of impoundment during last half hour of first survey and stayed for duration of survey. Second survey abandoned because of full shade. Site included the upstream half of the impoundment. Recreationists were at upstream end of site during last half hour of first survey. LOG CABIN DIVERSION DAM IMPOUNDMENT No detections (5/24/12) Site provided views of the upstream portion of the impoundment at the Camptonville No detections (6/7/12) Tunnel outlet. No disturbances during the surveys. Site provided views of the steep left bank where there is exposed bedrock and overhanging vegetation is generally absent. The same individual WPT was observed on 1 adult (5/24/12) 1 adult (6/7/12) both dates and was the same animal observed from two other sites. No disturbances No detections (7/12/12) during the surveys. 1 adult (5/24/12) 1 adult (6/7/12) 1 adult (7/12/12) 1 adult (5/24/12) No detections (6/7/12) 1 adult (7/12/12) Site provided views of the steep left bank where there is exposed bedrock and overhanging vegetation is generally absent. The same individual WPT was observed on each date and was the same animal observed from two other sites. No disturbances during the surveys. Site provided views of both the left and right banks and the boom near the dam. The same individual WPT was observed on both dates and was the same animal observed from two other sites. No disturbances during the surveys. MIDDLE YUBA RIVER, OREGON CREEK DAM REACH 2 adults (5/30/12) Site was at deep mid-channel pool near mouth of Yellowjacket Creek. WPT were 1 adult (7/12/12) observed basking on boulders and downed log. No disturbances during the surveys. No detections (5/30/12) Site was at deep mid-channel pool near mouth of Yellowjacket Creek. No No detections (7/12/12) disturbances during the surveys. Site was at deep mid-channel pool near mouth of Moonshine Creek. WPT were 1 adult (6/6/12) observed basking on floating platform and boulders. On 6/6/12, a Forest Service 2 adults (7/12/12) crew surveying for FYLF was in survey area for part of survey. Site was at deep mid-channel pool near mouth of Moonshine Creek. WPT basking on downed willow branches and on rock, and one in water. One of the WPT was the same observed at adjacent survey site above on the same date. MIDDLE YUBA RIVER, OUR HOUSE DVERSION DAM REACH 1 adult (6/6/12) 1 adult, 1 sub-adult (7/10/12) No detections (5/30/12) No detections (7/9/12) No detections (5/30/12) No detections (7/9/12) Site was at deep mid-channel pool near mouth of Oregon Creek. No disturbances during the surveys. Site was at deep mid-channel pool near mouth of Oregon Creek. No disturbances during the surveys. YUBA RIVER, MIDDLE/NORTH YUBA REACH No detections (6/5/12) Mid-channel pool upstream of New Colgate Powerhouse. Intermittent construction No detections (7/10/12) noises at powerhouse during survey on 6/5/12. No detections (6/5/12) Mid-channel pool upstream of New Colgate Powerhouse. Intermittent construction No detections (7/10/12) noises at powerhouse during survey on 6/5/12, Our House Diversion Dam Impoundment There are no known sightings of WPT at Our House Diversion Dam Impoundment. YCWA s Study 3.6 included surveys of the impoundment, but there were no detections of WPT (Table ). The absence of WPT was consistent with the results of two previous surveys at the impoundment in 2010 (PG&E and NID 2011). Aquatic habitat potentially suitable for WPT is limited to the right bank of Our House Diversion Dam Impoundment, where dense riparian vegetation may provide both basking habitat and underwater refuges. Exh. E - Environmental Report Application for New License April 2014 Page E ,

185 YCWA also assessed the potential for WPT to occasionally occur at Our House Diversion Dam Impoundment by surveying pools in the Middle Yuba River upstream of the impoundment. The upstream end of the impoundment and 10 pools upstream of the impoundment were surveyed by snorkeling under Study 3.14 on May 16 and August 6, The study area extended from about RM to RM There were no detections of WPT during the study. Habitat information collected during the study indicated that potential underwater hiding areas for WPT were absent in the study area at the observed water level, except for one pool where part of a bank was undercut. Log Cabin Diversion Dam Impoundment One adult WPT, photographed to verify it was the same individual, was repeatedly detected at Log Cabin Diversion Dam Impoundment over three survey visits under Study 3-6 (Table ) and additional observation periods for YCWA s Study This WPT basked at different locations ranging from 24 to 110 m from the diversion tunnel intake during the periods when the tunnel was diverting, and 20 to 24 m from the tunnel when the tunnel was not diverting. As part of efforts for YCWA s Entrainment Study, two other adult WPT were captured in a hoop net in Oregon Creek approximately 0.3 mi upstream of Log Cabin Diversion Dam Impoundment. In addition, a juvenile WPT was observed incidentally in a puddle on the road next to Log Cabin Diversion Dam Impoundment 0.1 mi upstream of the dam on June 15, Log Cabin Diversion Dam Impoundment is located within a portion of Oregon Creek characterized by mid-channel pools and low-gradient riffles interspersed amongst steeper sections with high-gradient riffles and cascades further upstream. Aquatic habitat potentially suitable for WPT is mainly located on the right bank of the impoundment, where dense willows and cottonwoods (Populus spp.) may provide both basking habitat and underwater refuges. Patches of waterweed (Elodea spp.) in the downstream portion of the impoundment may provide suitable habitat for juvenile WPT, particularly as water depths become shallower over the summer. Middle Yuba River Downstream of Our House Diversion Dam In the Middle Yuba River, downstream of Our House Diversion Dam, there are numerous midchannel and scour pools with adequate basking substrate, riparian vegetation, and sun exposure located throughout the reach. Downstream of Oregon Creek, suitable habitat occurred in the vicinity of Yellowjacket and Moonshine creeks, and at several other segments upstream of RM 0.3. During basking surveys at three sites, a total of nine WPT detections were recorded, including one that was likely a repeat observation of the same individual (Table ). There were also seven incidental observations. North Yuba River Downstream of New Bullards Bar Dam Conditions along the North Yuba River downstream of New Bullards Bar Dam are generally unsuitable for WPT. Although there are a few large, deep mid-channel pools with boulder and bedrock basking substrate, little or no potential nesting habitat or potential habitat for juvenile WPT was identified. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

186 Yuba River Along the Yuba River, habitats potentially suitable for WPT include numerous mid-channel, scour pools located upstream of Englebright Reservoir and downstream of Timbuctoo Bend. YCWA performed basking surveys just upstream of New Colgate Powerhouse at RM within a portion of the river reach characterized by low gradient, long mid-channel pools interspersed with low-gradient riffles/runs. There were no WPT observations during surveys (Table ) and no incidental observations were reported from the Yuba River during other studies. Oregon Creek Downstream of Log Cabin Diversion Dam There are no known observations of WPT in Oregon Creek downstream of Log Cabin Diversion Dam. Habitat is limited to a few deeper mid-channel pools and suitable basking areas under the dense riparian canopy are also scarce. Upstream of the Project There are few known records of WPT upstream of the Project. On the Middle Yuba River, one adult WPT was found about 3.5 miles upstream of Our House Diversion Dam during surveys in 2010 for relicensing of NID s Yuba-Bear Hydroelectric Project; no WPT were observed during surveys of five other sites on the Middle Yuba River further upstream. During similar surveys at 10 sites on the South Yuba River in 2010 for relicensing of PG&E s Drum-Spaulding Project, a total of 5 WPT were detected at two of the sites, both located just upstream of the U.S. Army Corps of Engineers Englebright Reservoir. In Oregon Creek, as indicated above, YCWA captured two adult WPT in a hoop net approximately 0.3 mi upstream of Log Cabin Diversion Dam Impoundment as part of Study YCWA is unaware of any other records of WPT upstream of the Project Mollusks The discussion of mollusks first describes special-status mollusks. Then, the results of mollusk surveys conducted within the Project area are addressed followed by a discussion of invasive mollusks. Special-Status Mollusks According to the Forest Service, seven aquatic mollusk species are considered FSS and have a potential to occur in Project-affected reaches on NFS lands. These FSS mollusk species include one freshwater mussel (California floater [Anodonta californiensis]), one sphaeriid (montane peaclam [Pisidium ultramontanum]), and five gastropods (Great Basin rams-horn [Hellisoma newberryi newberryi], topaz juga [Juga acutifilosa], scalloped juga [J. occata], Owen s Valley springsnail [Pyrgulopsis owensensis], and Wong s springsnail [P. wongi]). The associated habitat requirements and known distributions of the target species are described in Table Exh. E - Environmental Report Application for New License April 2014 Page E ,

187 Table Target Forest Service Sensitive mollusk species. Common Name Scientific Name Habitat Requirements California floater Anodonta californiensis Shallow muddy or sandy habitats in large rivers, reservoirs, and lakes. Great Basin rams-horn Hellisoma newberryi Large lakes, slow rivers, and spring-fed creeks; burrows in soft mud. Topaz juga Juga acutifilosa Sand and gravel substrates in spring-influenced streams and lakes and occasionally in large spring pools. Scalloped juga Juga occata Cold, moving waters of large rivers, often spring-influenced, with stable boulder and cobble substrates. Montane peaclam Pisidium ultramontanum Sand and gravel substrates in spring-influenced streams and lakes and occasionally in large spring pools. Owen s Valley springsnail Pyrgulopsis owensensis Small springs and spring runs, typically in watercress. Wong s springsnail Pyrgulopsis wongi Perennial seeps and small- to moderate-sized springs and spring runs, only in flowing waters. Cal Fish and Wildlife does not list any special-status aquatic mollusks in the vicinity of the Project. A review of Cal Fish and Widlife s California Natural Diversity Database (CNDDB) also showed no record of special-status mollusks in the Project Vicinity. Mollusk Surveys YCWA is unaware of any prior study of mollusks in the Project area. In July of 2012, YCWA conducted surveys for Study 3.3. Surveys were conducted at three sites within New Bullards Bar Reservoir, one site on Oregon Creek downstream of Log Cabin Diversion Dam, and one site in the Middle Yuba River downstream of Our House Diversion Dam. Surveys were performed by qualified biologists using qualitative timed-search methods and snorkel gear. No special-status mollusks were found during the surveys. No mollusks of any species were found at New Bullards Bar Reservoir. Several different species of aquatic mollusks were observed at both stream sites. The western pearlshell mussel (Margaritifera falcata) was typically found grouped in pockets near boulders, especially near the stream edges, where there is protection from high velocity water. Live specimens of two gastropod families, Pleuroceridae and Physidae, were found scattered over rocks of different sizes, but were most common on boulders and bedrock outcrops located outside of the highest velocity areas. The specimens of Pleuroceridae were identified as Juga spp. based on Burch (1989), but were not either of the two special-status Juga species described by Frest and Johannes (1999). The specimens found in Oregon Creek were typically large (up to 29 mm), with a smooth dark shell lacking any sculpturing, and no obvious banding. Other gastropods observed at the Oregon Creek site included three live specimens of the family Physidae and a single shell of the family Lymnaeidae. YCWA did not find any invasive mollusks species during relicensing studies Benthic Macroinvertebrates The discussion of benthic macroinvertebrates (BMI) first describes special-status BMI. BMI assemblages upstream of Englebright Dam are then discussed, followed by BMI assemblages downstream of Englebright Reservoir. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

188 Special-Status Benthic Macroinvertebrate Species The Forest Service considers benthic macroinvertebrates, as an assemblage, to be a Management Indicator Species. 34 Aquatic Macroinvertebrates Surveys Upstream of Englebright Reservoir Information on aquatic macroinvertebrates upstream of Englebright Reservoir is summarized from benthic macroinvertebrate (BMI) studies conducted as a component of YCWA s Sediment Pass-Through Program (Stillwater 2009), the South Yuba River Citizen's League (SYRCL) (G. Reedy, pers. comm., 2012), and YCWA s Study 3.1. In 2012, YCWA conducted surveys for Study 3.1. Surveys conformed to the Surface Water Ambient Monitoring Program (SWAMP) reach-wide benthos (RWB) data collection method, which is a multi-habitat protocol for documenting and describing BMI assemblages and physical habitat (Ode 2007). Surveys were conducted at eight sites in stream reaches upstream of Englebright Reservoir. Sites were located in: the North Yuba River below New Bullards Bar (1 site); Oregon Creek below Log Cabin Diversion Dam (2 sites); the Middle Yuba River below Our House Diversion Dam (3 sites); and the Yuba River above Englebright Reservoir (2 sites). YCWA identified 3,481 organisms representing 96 distinct taxa (i.e., 89 insect and seven noninsect taxa) from sub-samples of the BMI collected from the eight BMI sites. This equated to an estimated collection of 4,277 organisms. Ten BMI phylogenetic insect Orders were represented: Diptera (i.e., 32 taxa), Trichoptera (18), Ephemeroptera (10), Hemiptera (2), Homoptera (1), Coleoptera (8), Plecoptera (10), Odonata (4), Megaloptera (3), and Lepidoptera (1). In addition, aquatic crustaceans, arachnids, oligochaetes, gastropods, and bivalves were identified. Index of biotic integrity (IBI) scores ranged from 21 at the site in the North Yuba River upstream of the Middle Yuba River, to 69 at the site in the Middle Yuba River downstream of Oregon Creek. Multi-metric index (MMI) scores ranged from 16 at the site in the North Yuba River upstream of the Middle Yuba River, to 64 at the site in the Middle Yuba River downstream of Oregon Creek (with higher scores being better). Overall, the highest scores were observed consistently on the Middle Yuba River. Lower scores were found on the North Yuba River and Yuba River. Abundance was generally low, and five sites were evaluated with an abundance of less than 500 organisms. The lower abundance reduced the reliability of IBI and MMI scoring at those sites, because at least 500 organisms is the standard count to calculate IBI and MMI (Ode 2007). Figure shows these scores by site and sub-basin. 34 The National Forest Management Act directs the Forest Service to select and track species that are of special interest or indicative of management trends. Exh. E - Environmental Report Application for New License April 2014 Page E ,

189 Index Scores IBI MMI IBI MMI IBI MMI IBI MMI IBI MMI IBI MMI IBI MMI IBI MMI North Yuba River Above Middle Yuba River North Yuba River Sub- Basin Oregon Creek Below Log Cabin Oregon Creek Above Middle Yuba Middle Yuba River Above Oregon Creek Middle Yuba River Below Oregon Creek Middle Yuba Above North Yuba Yuba River Above Colgate Powerhouse Yuba River Below Colgate Oregon Creek Sub-Basin Middle Yuba River Sub-Basin Yuba River Sub-Basin Figure Overview of scores by basin, stream, and indices. Sites with starred symbols represent locations where insufficient organisms were collected to make the resultant IBI and MMI scores reliable. Site scores from both indices found that higher quality sites (as ranked) were found further downstream. This is similar to findings by Rehn (2009), who stated that sites below diversions tend to have similar composition to above-dam or above-diversion sites. Sites below reservoirs generally show a significant difference in reduced quality. Rehn suggests that reduced quality may include: lower diversity, lower EPT (i.e., Ephemoptera, Plecoptera, Trichoptera) richness, and reduced intolerant taxa; and that these issues may lessen with distance downstream. Generally, results from current sampling followed these trends. Available historical BMI data for comparison with the sites evaluated in this study were limited to surveys conducted by SYRCL at three locations: the Middle Yuba River above the confluence with Oregon Creek from and in 2008; the Middle Yuba River below the Oregon Creek confluence in 2009; and Oregon Creek above the Middle Yuba River confluence in 2007 and 2009 (G. Reedy, pers. comm., 2012). Three of the current study sites were located near these historical sites. Stream habitat characteristics, which influence BMI community structure, may have changed since these historic sampling events. Physical habitat data were also not available for the historical sites. In addition, IBI and MMI scores could not be calculated from the historical data, because taxonomic resolution was not consistent with requirements for the IBI and MMI. However, many of the FERC-approved study-specific metrics including species richness and diversity (Shannon Diversity Index), percent composition of EPT taxa, and other BMI constituents, were extracted from the historical data and could be directly compared to April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

190 YCWA s data. Comparison of these metrics with YCWA s sites yielded similar results with some shifts in feeding assemblages. This could be due to sampling a variety of habitat types in 2012 versus targeted riffles in the historical samples. Benthic macroinvertebrate sampling conducted in 2009 as a component of YCWA s Sediment Pass-Through Program took place at two locations one above and one below Our House Diversion Dam located on the Middle Yuba River (Stillwater 2009). Sampling methodology followed the SWAMP, RWB approach, for collecting BMI and documenting physical habitat (Ode 2007). A total of 1,016 organisms were subsampled from the two composite samples. Physical habitat quality scores at both sites were nearly identical with 161 for the upper site and 160 for the lower. MMI scores, based on seven metrics described by Rehn (2008), were formulated for each sample. MMI scores for the site upstream of Our House Dam scored significantly higher (79) than the site downstream (41). Aquatic Macroinvertebrates Surveys Downstream of Englebright Reservoir Information on aquatic macroinvertebrates downstream of Englebright Reservoir is summarized from BMI studies conducted by SYRCL (G. Reedy, pers. comm., 2012) and YCWA s Study 3.2. In 2012, YCWA conducted surveys for Study 3.2. Surveys were conducted at six representative sites on the Yuba River between Englebright Dam and the confluence with the Feather River. YCWA employed methods derived from two protocols suitable for large rivers that cannot be waded: the United States Environmental Projection Agency s Environmental Monitoring and Assessment Program and the Large River Bioassessment Protocol. Historical BMI data from the Yuba River downstream of Englebright Reservoir is limited to the results of surveys conducted at Parks Bar (RM 18) in 2006 and 2007 by SYRCL (G. Reedy, pers. comm., 2012). The historical BMI sampling targeted riffles that could be waded, whereas YCWA sampled various habitats, including areas too deep to wade. The historical data were insufficient to characterize existing conditions. The six sample sites differed markedly in habitat, substrate composition, and depth (Table ). Downstream sites generally had more riffle and glide habitat than upstream sites, with an exception being the large proportion of glide habitat at Site 5 (RM 20). This general trend was accompanied by a shift from larger boulder and cobble substrates in upstream sites to cobble and gravel in downstream sites. The shift in habitat and substrate composition is likely a function of geomorphic controls. Sites 6 and 5 (RM 23 and 20) were confined by valley walls and bedrock outcrops. The downstream sites were in a relatively unconfined floodplain, resulting in more diverse habitat types. Exh. E - Environmental Report Application for New License April 2014 Page E ,

191 Table Water quality and habitat characteristics collected at six sites in the Yuba River downstream of Narrows 2 Powerhouse in July Category Metric Site 6 Site 5 Site 4 Site 3 Site 2 Site 1 (RM 23) (RM 20) (RM 18) (RM 14) (RM 11) (RM 7) Water Quality Water Temperature ( C) Dissolved Oxygen (mg/l) Flow (cfs) 2,225 2,225 2,225 2,225 1,330 1,330 Gradient (%) Average Thalweg Depth (cm) Habitat Composition (% of site) Pool Glide Site Riffle Characteristics Rapid Dominant Thalweg Substrate Composition (% of site) Fines and Sand Gravel Cobble Boulder Bedrock Average Sample Plot Depth (cm) Average Wetted Width (m) Average Bankfull Width (m) Transect Average Bankfull Depth (m) Characteristics Average Incision Height (m) Riparian Canopy Cover (%) No. LWM Pieces (> 0.3 m width, > 5 m length) Key: RM = river mile cm = centimeters C = Celsius cfs = cubic feet per second % = percent µm -= micrometers mg/l = milligrams/liter m = meter An estimated 183,682 organisms were collected from the six sample sites. A randomly sorted subset of 3,665 invertebrates was used to derive BMI metrics. Six aquatic insect orders were represented: Diptera (i.e., 50 taxa), Ephemeroptera (11), Trichoptera (6), Plecoptera (3), Coleoptera (3), and Hemiptera (1). In addition, aquatic crustaceans, arachnids, annelids, gastropods, nemerteans, and turbellarians were identified. Eighteen common BMI metrics were calculated for each site (Table ). The BMI communities in all of the sites were dominated by midges (Diptera, Chironomidae), annelid worms (Oligochaeta), baetid mayflies (Ephemeropetera, Baetidae), and net-spinning caddisflies (Trichoptera, Hydropsychidae). The percentage of EPT taxa varied little among sites 1, 2, 3, and 5, but was much lower at sites 4 and 6. EPTs are generally associated with riffles and gravel sediments. The EPT distribution was positively correlated with coarse gravel (ρ= 0.89) and negatively associated with pools (ρ= -0.85). At each of the sites, the predominant BMI feeding groups were collector-filterers and collector-gatherers, indicating that detritus and suspended particulates are the principal BMI food sources. In addition, the percentage of scrapers and shredders at each site was relatively low, indicating the small component of the community that processes periphyton, allochthonous material, and coarse particulate organic matter. No clear upstream to downstream trend in tolerance was observed; however, the number of intolerant taxa was highest, and the percentage of individuals from the dominant taxa was lowest, at Site 1 (RM 7). The percentage of the population consisting of tolerant individuals was also highest at Site 1. No clear upstream to downstream trend in total estimated BMI abundance or taxa richness was April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

192 observed, although abundance was highest at sites 1 and 2 (RMs 7 and 11), and was lowest at the most upstream location, Site 6 (RM 23). Variability in site BMI abundance is likely related to the presence of productive benthic habitats with gravel, moving water, and food resources. Table BMI metrics from samples collected at six sites in the Yuba River downstream of Narrows 2 Powerhouse in July BMI Metrics Site 6 (RM 23) Site 5 (RM 20) Site 4 (RM 18) Site 3 (RM 14) Site 2 (RM 11) Site 1 (RM 7) ABUNDANCE Total Estimated Abundance 7,422 22,720 23,080 15,500 82,320 32,640 RICHNESS Taxonomic Richness No. EPT Taxa No. Ephemeroptera Taxa No. Plecoptera Taxa No. Trichoptera Taxa No. Coleoptera Taxa COMPOSITION % EPT % Ephemeroptera Shannon Diversity Index (SDI) TOLERANCE/INTOLERANCE California Tolerance Value (CTV) No. of Intolerant Taxa % Tolerant Organisms % Dominant Taxon FEEDING % Collector-filterers + Collector-gatherers % Scrapers % Non-gastropoda Scrapers % Predators % Shredders Available historical BMI data for comparison with the study sites were limited to surveys conducted at Parks Bar (Site 4, RM 18) in 2006 and 2007 by SYRCL (G. Reedy, pers. comm., 2012). The historical BMI sampling sites occurred near YCWA s study sites. However, SYRCL used the California Stream Bioassessment Procedure for sampling, which is adapted to streams that can be waded and therefore results and effort are inherently different from that of YCWA s study. Additionally, stream habitat characteristics, which influence BMI community structure, may have changed from 2007 when SYRCL s study was performed to 2012 when YCWA s study was performed. Therefore, a limited and qualitative comparison of available metrics was conducted. Taxonomic richness was considerably higher in 2012 than in 2006 and 2007 (Table ); however, the EPT richness values changed little among years. The difference in overall taxonomic richness could therefore be due to smaller collection areas in 2006 and 2007, and to less effort devoted to identifying distinct taxa in groups such as the midges. Exh. E - Environmental Report Application for New License April 2014 Page E ,

193 Table BMI metrics from samples collected at Site 1: Hallwood Boulevard (RM 7) on July 19, 2012 compared to historical samples collected by SYRCL in 2006 and BMI Metrics SYRCL s Data Parks Bar 2006 SYRCL s Data Parks Bar 2007 YCWA s Data 2012 RICHNESS Taxonomic Richness No. EPT Taxa No. Ephemeroptera Taxa No. Plecoptera Taxa No. Trichoptera Taxa No. Coleoptera Taxa COMPOSITION % EPT NA 7.3 Shannon Diversity Index (SDI) FEEDING % Collector-filterer+Collector-gatherer Individuals NA 90.9 % Scrapers % Non-gastropoda Scrapers 1.22 NA 2.6 % Predators % Shredders 0 NA 0.2 The percent composition of EPT taxa was much higher in 2006 than in This difference can likely be attributed to the different methodology resulting in historical samples being collected from flowing riffles, whereas 2012 samples came from a variety of flowing and stagnant habitats. Higher SDI values in 2012 than in 2006 and 2007 may be due to the larger sample area and multi-habitat sampling strategy employed, but this is speculative. The relative abundance of collector-filterer and collector-gatherer BMIs varied little between 2006 and 2012, but the relative abundance of all other feeding groups increased in The increased percentages of the other feeding groups in YCWA s study was likely a result of sampling multiple habitats Aquatic Invasive Species Invasive species are defined as species that are non-native to the ecosystem under consideration, and whose introduction causes, or is likely to cause, economic or environmental harm, or harm to human health (National Invasive Species Council 2001). Generally, invasive species are best addressed by preventing their introduction into vulnerable ecosystems (CDFW 2008). Eradication or control of aquatic invasive species, once they are established, is often difficult or impossible to achieve. Information on the occurrence of aquatic invasive species was compiled by YCWA as part of relicensing through reporting of incidental observations. All aquatic field study personnel were instructed to record incidental observations of invasive species observed while conducting field work. The discussion of aquatic invasive species below is focused the potential occurrence of invasive mollusks (snails and bivalves), aquatic vascular plants, and invasive algae. In addition the known occurrences of American bullfrog are summarized (see also Section ). April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

194 American bullfrog is currently categorized as an aquatic invasive species in California, but is already a well-established and widespread species, and is therefore treated separately from aquatic invasive species for which prevention is still possible. Invasive Mollusks YCWA did not find quagga mussel (Dreissena rostriformis bugensis), zebra mussel (D. polymorpha), New Zealand mudsnail (Potamopyrgus antipodarum), Asian clam (Corbicula fluminea), or any other species of invasive mollusk, during Study 3.3 or other relicensing studies. Similarly, YCWA is not aware of any reports of any invasive mollusks occurring in the Project impoundments or Project-affected streams. The closest current known occurrence of quagga mussel is in Lahontan Reservoir in Nevada, approximately 172 mi from the Project (USGS 2013a). Zebra mussels are known to occur in California only at San Justo Reservoir, part of the Central Valley Project located in San Benito County, approximately 250 mi from the Project (USGS 2013b). New Zealand mud snails are a concern to Cal Fish and Wildlife, and the closest known occurrence of the snail with respect to the Project is on the American River downstream of Lake Natoma, approximately 80 mi south of the Project (USGS 2013c). The Asian clam s nearest known occurrence is in the Sacramento River, near the Feather River, approximately 40 mi from the Project (USGS 2013d). Additionally, the potential for quagga and zebra mussels to invade is limited by certain water quality parameters. Currently, the best scientific data indicate quagga mussels need calcium concentration levels of at least 11 milligrams per liter (mg/l) to survive and at least 15 mg/l to moderately infest waterbodies. Other water quality parameters, including ph, hardness and water temperature, may also limit the ability of quagga mussels to invade (Claudi & Prescott 2011). Based on data collected in New Bullards Bar Reservoir during YCWA s Water Quality relicensing study (Technical Memorandum 2-3) in 2012 and historical data, calcium concentration, alkalinity, total hardness, and phosphorus concentration, all fall outside the range currently considered to be necessary for successful mussel invasion. Table below compares the parameters documented in Claudi and Prescott (2011) as necessary for successful mussel invasion with those same parameters measured in New Bullards Bar Reservoir, both historically and during YCWA s Water Quality relicensing study (Technical Memorandum 2-3) in 2012 (YCWA 2012). Table Comparison of Water Quality Parameters Necessary for Mussel Invasion (Unable [red], Potentially Able [yellow], and Able [green]) with Measurements in New Bullards Bar Reservoir. Parameter Calcium (mg/l) Alkalinity (mg CaCo 3/L) Adults Do Not Survive Long-term From Claudi & Prescott (2011), Table 1. Uncertainty of Veliger Survival Moderate Infestation Level High Infestation Level Relicensing Study: New Bullards Bar Reservoir (YCWA 2012) Potential to support Dreissenid mussels Historical Data 1 Study 2-3, Water Quality < 8 to < 10 < Unable < > Unable Exh. E - Environmental Report Application for New License April 2014 Page E ,

195 Table (continued) Parameter Total Hardness (mg CaCo 3/L) ph Mean Summer Temperature ( F) Dissolved Oxygen (mg/l)(% Saturation) Conductivity (µs/cm) Salinity (mg/l) (ppt) Adults Do Not Survive Long-term From Claudi & Prescott (2011), Table 1. Uncertainty of Veliger Survival Moderate Infestation Level High Infestation Level Relicensing Study: New Bullards Bar Reservoir (YCWA 2012) Potential to Historical Data 1 Study 2-3, support Water Quality Dreissenid mussels < Unable/ Uncertain < 7.0 or > 9.5 < 64 < 3 (25%) or or > (25-50%) or or (50-75%) Uncertain/ Moderate Moderate/ High 8 (>75%) Uncertain/ Moderate < 30 < Moderate > (< 0.01) 5-10 ( ) < 5 (< 0.005) Secchi depth or > < 0.1 or > 8 (m) 2.5 Chlorophyll a or < 2.5 or > 25 (µ/l) Total 5-10 or 30- Phosphorous < 5 or > (µg/l) Key: J Estimated value. Results are greater than method detection limit, but lower than the reporting limit 1 Samples were collected from New Bullards Bar Reservoir in 1965, 1967, and Orthophosphate only. 3 N/A = Not Available N/A Unable N/A J J Unable Invasive Plants and Algae Two invasive, submerged, aquatic vascular plants have the potential to occur within the Project Area: Eurasian milfoil (Myriophyllum spicatum) and hydrilla (Hydrilla verticillata), although neither were observed during field efforts. Eurasian milfoil is one of several aquatic milfoils that are invasive. The species is easily spread from stem fragments carried by boaters and fishers, and by waterfowl and other wildlife. Although difficult to eradicate, Eurasian milfoil can be managed with mechanical harvesters, hand removal, water drawdown, and aquatic herbicides (Cal-IPC 2013). Eurasian milfoil is listed by the California of Department of Food and Agriculture (CDFA) as a CDFA C-list species. Hydrilla is native to Eurasia, Africa, and Australia. The species is a pernicious, CDFA A-list noxious weed, easily spread through plant fragments, tubers, and turions (i.e., specialized overwintering buds) transported through commercial and recreational boating, as well as through nurseries and aquaculture companies. The first known established occurrence of hydrilla in California was in Marysville, Yuba County in Infestations of hydrilla have occurred in reservoirs, lakes, irrigation ponds, golf course ponds, and other types of ponds, and in canals. CDFA has an ongoing hydrilla eradication program that includes surveys of infested and vulnerable sites (CDFA 2012). Hydrilla can be successfully treated with a combination of April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

196 manual removal, dredging, lining of waterbodies, biological control, aquatic herbicides, water drawdown, soil fumigation and burying, with eradication achieved only after at least six years in which no hydrilla is found (CDFA 2012). One invasive algae, Didymosphenia geminata (commonly known as didymo ), has the potential to occur within the Project Area, although it was not observed by YCWA during relicensing field efforts. Didymo is a freshwater diatom which occurs attached to rocks or other surfaces, and the extracellular branching stalks form large mats, resistant to decay. To the observer, these mats appear as fiberglass insulation, tissue paper, brown shag carpet, or sheep skins covering the streambed (Spaulding and Elwell 2007). Originally found in the low nutrient cold waters of the far northern hemisphere and common to Scotland, Sweden, Finland, and China s Kanchou region, D. geminata has now expanded its geographic range to include North America, Europe, and even New Zealand (Spaulding and Elwell 2007), where it is considered a nuisance or invasive species. The first documented presence of D. geminata in California was from the mid- 1990s on the South Fork American River, which is located south of the Yuba River (Spaulding and Elwell 2007). Observations of D. geminata were common upstream of the Project in the Middle and South Yuba rivers during previous relicensing studies conducted by PG&E and NID. It should be noted that these occurrences were predominately within higher elevation stream reaches extending to more than 1,525 m (5,000 ft) and in certain lower elevation stream reaches that receive cold water from diversions or deep water releases, conditions not comparable to stream reaches associated with the Project. YCWA field staff did not report any observations of D. geminata in the Project Area, but YCWA is aware of reports of D. geminata in the Yuba River downstream of Englebright Dam. American Bullfrog American bullfrog is a large, highly aquatic frog native to the eastern half of the United States and as far north as southern Quebec, Canada. Bullfrogs were first introduced into California more than a hundred years ago and are now well established in lowland and foothill locales in California, utilizing stock and irrigation ponds, irrigation ditches, low gradients streams, and impoundments, often where fish also occur. Pre-adaptations that have facilitated this successful invasion include capability for long-distance dispersal, late breeding over a long period, and unpalatability to many predatory fish species. Because it is a late breeding species, American bullfrog is well suited to the Mediterranean climate patterns of California. Larval overwintering for one or two years occurs in much of the species native and introduced range. Small-scale, local control or eradication of American bullfrog may be effective early in an invasion or in relatively closed systems. Techniques include hand and net capture, shooting, spearing, gigging, and use of hoop nets or aquatic funnel traps, which in most settings are labor intensive and often fail to produce the desired results. Partial reduction of American bullfrog numbers typically results in higher survivorship and faster growth of the remaining animals (Doubledee et al. 2003). Habitat manipulation, specifically seasonally draining wetlands to kill American bullfrog larvae, may be effective where possible, if performed at a high annual frequency. However, no management approach suitable or effective for large-scale control of Exh. E - Environmental Report Application for New License April 2014 Page E ,

197 existing populations of American bullfrog has been developed (Snow and Witmer 2010). Regional control of American bullfrog in areas with multiple suitable water bodies, including stream systems, limited accessibility, and private property trespass restrictions, has never been attempted. American bullfrog was documented at all of the FYLF Survey study sites on the Middle Yuba River; North Yuba River, New Bullards Bar Dam Reach; and Yuba River, but only one observation occurred at one of the Middle Yuba River sites. In addition, incidental observations of American bullfrog were reported on these reaches and on Oregon Creek. Survey and incidental observations, which are detailed in the Technical Memorandum for Study 3.4, included first-year and second-year tadpoles in mid-channel, side channel, and backwater pools Environmental Effects This section includes a description of the anticipated effects of YCWA s proposed Project, which includes YCWA s proposed conditions (Appendix E2) on aquatic resources. The section below is divided into the following areas: 1) effects on special-status and CESA-listed aquatic species; 2) effects on reservoir fish populations, including minimum reservoir pools; 3) effects of minimum flow releases, including ramping rates; 4) effects of fish entrainment; 5) effects on fish stranding; 6) effects on fish passage; 7) effects on mollusks and benthic macroinvertebrates; 8) effects on aquatic invasive species; 9) effects of sediment passage at Our House and Log Cabin Diversion Dam, and 10) effects of new ground-disturbing activities. YCWA has proposed environmental conditions related to aquatic resources, which are listed in Section and described at length in Appendix 2. Where pertinent, these proposed conditions are discussed in each section below in terms of YCWA s efforts to avoid or reduce potential effects of the Project on aquatic resources. Proposed Condition TE1 (Monitor Water Temperature Downstream of Narrows 2 Powerhouse), TE2 (Monitor Chinook Salmon Downstream of Narrows 2 Powerhouse), and TE3 (Establish Lower Yuba River Anadromous Fish Ecological Group) are also discussed in the Applicant-Prepared Draft EFH evaluation Effects on Special-Status/CESA-Listed Aquatic Species Currently, two aquatic special-status species are known to occur in the Project Area, FYLF, and WPT, and one species is suspected to occur, hardhead. No aquatic species listed as threatened or endangered under the CESA are known or expected to occur in the Project Area. Downstream of the Project, with the exception of spring-run Chinook salmon which is listed as threatened under CESA and occurs within the Project Area in the lower Yuba River in the tailwater pool of Narrows 2 Powerhouse. Downstream of the Project, hardhead and eight other special-status fishes are known to occur: green sturgeon, Pacific lamprey, river lamprey, pink salmon, chum salmon, fall-run Chinook salmon, California roach, and Sacramento splittail. Information regarding these species is summarized below, with potential effects addressed by Project activity (e.g., minimum streamflows and ramping) in subsequent sections. ESA-listed aquatic species are addressed in the Threatened and Endangered Species Section (3.3.5). YCWA s proposed Conditions that generally address special-status aquatic species are addressed in this section. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

198 Special-status Fish Hardhead Hardhead was not documented by YCWA surveys upstream of Englebright Reservoir, but was found in Englebright Reservoir and has been documented in the lower Yuba River. Historical samples indicate that an individual hardhead was identified in the Log Cabin Diversion Dam pool as recently as 2001 (personal communication, Dan Teater, Forest Service). Additionally, Gast et al. (2005) reported observations of hardhead during snorkel surveys within the Middle Yuba River between Our House Diversion Dam and the confluence of Oregon Creek, but did not collect any of the observed fish to confirm identification. The population identified in Englebright Reservoir was in good condition, free of parasites, and with good weights based on measured lengths. There were multiple age classes present including age-0 fishes that indicated successful reproduction and suitable spawning habitat. Given the existing information, the presence of hardhead in the Project is considered to be infrequent. Hardhead primarily occur downstream of Englebright Dam where Project effects on temperature and flow can influence habitat quality and quantity. Temperature and flow can also influence competition and predation, the latter being a primary reason for decline of hardhead throughout its range (Moyle et al 1995). Based on habitat criteria reported above, changes in flow and temperature will not adversely affect hardhead downstream of Englebright Dam. Cooler temperatures throughout the year may reduce predation, and large, deep pools used for adult rearing throughout most of the lower Yuba River will be maintained under Project conditions, which will benefit the Yuba River hardhead population. Pacific Lamprey Under Project conditions, suitable Pacific lamprey spawning and rearing habitats will be comparable in quantity and quality to those that currently support the well distributed and abundant population of Pacific lamprey in the lower Yuba River (YCWA 2012a). The flowhabitat relationships discussed above show that adult lamprey WUA peaked inside of the active channel at DPHZ, DeerHZ, and DryHZ at 622, 600, and 1,700 cfs, respectively. Predicted flows within the DPHZ and DeerHZ under Project conditions (Section Water Resources) will provide at least 80 percent of optimum conditions at least 90 percent of the time. Suitable temperatures will persist during spawning (12-18 C, March June). Overall, Pacific lamprey populations will not be adversely affected. River Lamprey Detailed information on habitat requirements of river lamprey is sparse. As such, river lamprey habitat requirements are considered to be similar to those for Pacific lamprey. Based on the discussion above concerning effects on Pacific lamprey habitat under project conditions, river lamprey habitat quality and quantity would continue to support a viable and unique river lamprey population. The river lamprey population in the lower Yuba River would not be adversely affected. Fall-run Chinook Salmon Potential Project effects on the fall-run Chinook salmon population of the lower Yuba River are discussed in detail in the Applicant-Prepared Draft EFH evaluation. Exh. E - Environmental Report Application for New License April 2014 Page E ,

199 Pink Salmon Pink salmon, along with chum salmon discussed below, are extremely rare to the Central Valley. Pink salmon are infrequently observed in very low numbers in the lower Yuba River, and have not established a population in the Yuba River or elsewhere in the Central Valley. Therefore, pink salmon are not further addressed in this FLA. Chum Salmon As discussed above, the presence of chum salmon in the Central Valley is rare and typically restricted to the lower Yuba River. As with pink salmon, chum salmon have not established a population in the Yuba River or elsewhere in the Central Valley. Therefore, chum salmon are not further addressed in this FLA. California Roach California roach is another species uniquely abundant in the lower Yuba River. The roach is a warmwater species that has been routinely observed in surveys within the lowermost reaches of the lower Yuba River. Conditions that support the current population will persist under Project operations. Temperature and flow regimes under Project conditions will not adversely affect California roach population. Splittail Splittail were not observed in the lower Yuba River during any of the studies reported by YCWA in YCWA (2012a). Splittail are known to occur in the Feather River, downstream of the Yuba River typically within the seasonally flooded areas of the river. Project operations are not expected to affect duration and extent of the floodplain habitats, and, such, would not adversely affect splittail that may occur in the lower Yuba River or Feather River. Foothill Yellow-legged Frog YCWA found breeding populations of FYLF in the Middle Yuba River and Oregon Creek downstream of Our House Diversion Dam and Log Cabin Diversion Dam, respectively. The downstream extent of breeding populations on the Middle Yuba River is not known; however, YCWA recorded few detections of FYLF from surveys or incidental observations downstream of the confluence of Oregon Creek. No FYLF were found on the North Yuba River or Yuba River downstream of New Bullards Bar Reservoir. The reservoir is not suitable habitat for FYLF, but the species has been documented previously at several tributaries of the reservoir, including Slate Creek and Little Oregon Creek. Potential effects of the proposed Project on FYLF downstream of Our House Diversion Dam and Log Cabin Diversion Dam are discussed below in Section (Effects of Minimum Flow Releases, Including Ramping) and (Effects of Sediment Passage). Western Pond Turtle YCWA found WPT at multiple locations in New Bullards Bar Reservoir, usually near the shore. Project operation and maintenance, particularly related to reservoir water level fluctuations, has the potential to affect the availability of basking substrates, habitat for juvenile WPT, nest (i.e., egg-laying) site selection and nest success. At New Bullards Bar Reservoir, Project topography April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

200 and operations influence the frequency, distribution, and accessibility of basking substrates. However, because the most suitable habitats are associated with the mouths of tributaries and changes in water surface elevation are gradual, adult and sub-adult WPT likely shift locations in response. Some of the potential WPT nesting habitat that was mapped around New Bullards Bar Reservoir occurs below the NMWSE. This suggests that WPT may sometimes nest at locations below the NMWSE, although actual nesting locations are unknown. Because incubating WPT eggs are intolerant of inundation or saturated soils, nests below the NMWSE would fail if flooded. However, relatively little suitable nesting habitat below NMWSE is likely to be exposed during most of the May-July egg-laying season or during the day incubation period, because peak water surface elevation in the reservoir generally occurs in May or June. Overall, the possible adverse effect of inundation of WPT nests from Project operation is one of several factors, including abundant predatory fish and scarce habitats for juvenile WPT, which constrain habitat suitability of New Bullards Bar Reservoir for WPT and may limit population recruitment. YCWA also documented WPT at various locations in the Middle Yuba River and Yuba River downstream of Project facilities, and in Oregon Creek upstream of Log Cabin Diversion Dam. Effects of the proposed Project on WPT are discussed below in Section and (Effects of Entrainment). Proposed Conditions The proposed Project includes six proposed conditions that generally address special-status aquatic species. The first measure is, Meet with Agencies and Indian Tribes Annually (GEN1), and would assure that FERC, agencies and Indian tribes have an opportunity to discuss the previous calendar year s license activities and understand YCWA s plans regarding license implementation in the current calendar year. Condition GEN1 does not imply that YCWA may not proceed with license implementation until after the annual meeting, or that agencies or Indian tribe s approval is needed for YCWA to implement the terms and conditions in the license. Nor does the condition imply that YCWA will consult with the agencies or Indian tribes only once each year: YCWA intends to consult as needed during other times of the year and as otherwise necessary. The second measure, Review Special-status Lists and Assess Newly-listed Species (GEN2) requires that YCWA review pertinent special-status species lists (species listed under ESA as endangered or threatened; CESA as endangered, threatened, fully protected or species of special concern; Forest Service sensitive; and PNF and TNF Watch List Species), annually to identify such species. An annual review is appropriate as changes to special-status species lists may vary from year to year. If a species has been added to the list and has a reasonable likelihood of being directly affected by the Project and adequate information is not available to assess likely Project effects, YCWA would consult with the appropriate agencies with jurisdiction over the species to develop a study plan to assess potential Project effects, provide the plan to those agencies for review, file the plan with FERC, perform the study as approved by FERC, and prepare a report, including recommended measures. YCWA would provide the report to the appropriate agencies for review, file the report with FERC, and implement those measures as directed by FERC. Exh. E - Environmental Report Application for New License April 2014 Page E ,

201 The third measure, Provide Environmental Training to Employees (GEN3), proposes that YCWA will train its operations staff annually to familiarize them with general identification and location of known populations of special-status species and other environmentally sensitive areas within or adjacent to the FERC Project Boundary. YCWA will direct staff to avoid disturbance to these areas and discourage the spread of aquatic invasive species. Providing training to staff when they are hired will assure new staff are quickly trained, and periodic training will serve as a refresher for staff to note any changes since the last training. Training would also include procedures for reporting to YCWA s management if staff observes any Project activity directly affecting these special-status species. The fourth measure, Implement Our House and Log Cabin Diversion Dams Sediment Management Plan (GS2), proposes that YCWA implement a plan regarding how sediment will be passed through Log Cabin and Our House diversion dams in most years; and how material will be removed from, transported and disposed of after large storms, which may overwhelm regular sediment bypass operations in other years. Opening the low level outlets is expected to be beneficial to FYLF. Currently, moderate sized sediments (i.e., gravel and small cobbles) and shallow margin habitat are relatively scarce below Our House Diversion Dam, which may limit conditions for FYLF breeding and rearing. Passage of sediments will likely improve habitat by increasing the amount of substrate available for egg-attachment and shallow margins for tadpoles. The fifth measure, Implement Upper Yuba River Aquatic Monitoring Plan (AR7), proposes that YCWA will complete various aquatic monitoring including for one special-status species, FYLF. YCWA s Proposed Condition AR7 would periodically monitor FYLF at representative locations where they were monitored during relicensing, which would provide a comparison between the distribution, relative abundance, and condition of FYLF under pre-license conditions and new license conditions. To facilitate this comparison, Condition AR7 proposes to use the same methods that were used during relicensing, and samples would be taken at the same time of year they were taken during relicensing. Condition AR7 proposes that YCWA record all incidental observations of another special-status species, WPT. In addition, periodic fish, riparian, geomorphology, water quality and water temperature monitoring will also occur to compare various resources under pre-license and new license conditions. The sixth measure, Monitor Water Temperatures Downstream of Narrows 2 Powerhouse (TE1), proposes that YCWA will deploy and maintain temperature recording devices at five locations in the lower Yuba River. The monitoring sites will be distributed to acquire temperature information from reaches with potentially distinct temperature regimes. The monitoring will be provided to various management teams to allow confirmation of compliance and effectiveness in providing temperatures needed to maintain suitable habitat conditions for life stages of species of special concern (e.g., Chinook salmon holding and spawning) Effects on Reservoir Fish Populations, Including Minimum Reservoir Pools Project O&M could affect fish populations in New Bullards Bar and Englebright reservoirs, if fluctuations in water levels reduce availability or access to required habitats or large numbers of fish are entrained into project intakes. However, YCWA s studies showed reservoir fish April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

202 communities were diverse and that fish were in good condition, free of parasites, and with good weights based on measured lengths. In New Bullards Bar and Englebright reservoirs, the presence of age-0 fish indicated successful reproduction had occurred. It is also unlikely that there is substantial entrainment of fish into project intakes. Investigation of the potential for fish to be entrained was completed at both Project powerhouse intakes. Results indicate that entrainment is not likely to affect fish populations within the reservoirs. Effects of entrainment are further discussed in Section below. Suitable spawning habitat that could be utilized by warm and coldwater species was observed throughout the reservoirs and in the tributaries to New Bullards Bar Reservoir. Fish passage studies of tributaries to New Bullards Bar Reservoir indicated that all but one potential barrier located on Mill Creek would be inundated during spring and early summer when fish would move into tributaries from the reservoir. Fish passage out of New Bullards Bar Reservoir is further discussed in Section below. Englebright Reservoir was found to generally be a stable operational environment that supported numerous native fishes, including hardhead, a Forest Service sensitive species. The reservoir storage capacity is used primarily to attenuate power peaking releases from New Colgate Powerhouse and to capture some storm runoff from the upstream watershed. As a result, reservoir water elevation does not vary considerably and generally changes no more than 15 ft annually, with less than 5 ft variations on average monthly. The proposed Project includes two proposed Conditions related to reservoir fish populations. Proposed Condition WR5 will maintain a minimum reservoir pool in New Bullards Bar Reservoir, except for rare drawdowns below this elevation if necessary to meet the minimum streamflow requirements. The minimum pool elevation will be the same as the existing license, which will ensure that current suitable conditions for reservoir fish will be maintained. Accurate and reliable gaging for compliance with Condition WR5 is addressed under proposed Condition WR4 (Implement Streamflow and Reservoir Level Compliance Monitoring Plan). In the second condition, YCWA intends to maintain high quality recreational fishing opportunities at New Bullards Bar Reservoir by implementing a New Bullards Bar Reservoir Fish Stocking Plan under proposed Condition AR6. The plan will continue levels of rainbow trout and kokanee allotments historically planted by Cal Fish and Wildlife. Refer to Appendix E2 for this measure as well as an accompanying rationale statement Effects of Minimum Flow Releases, Including Ramping 35 YCWA s proposed Project has a potential to adversely or beneficially affect aquatic resources, including fish and FYLF, due to changes in minimum streamflows. To evaluate the adequacy of 35 Many of YCWA s proposed minimum streamflow releases are triggered by specific water year types (i.e., Critically Dry, Dry, Below Normal, Above Normal and Wet), which are part of YCWA s proposed Project. Refer to Exhibit B for a description and rationale for YCWA s proposed water year types, and to YCWA s Proposed Measure AR1, in Appendix E2 for the full text of YWCA s proposed measure regarding water year types. Exh. E - Environmental Report Application for New License April 2014 Page E ,

203 existing minimum streamflows and develop the proposed minimum flow releases, 36 YCWA evaluated aquatic resources in the vicinity of the five Project facilities from which releases might be made. Table lists each facility by category and provides for each facility, the length of the affected reach, if the existing license includes a minimum flow release, and the type of instream flow analysis performed by YCWA downstream of the facility. Table Facilities from which YCWA may release flow into a stream. Basin Sub-Basin Stream Yuba River Yuba River Yuba River North Yuba River Middle Yuba River Middle Yuba River North Yuba River Middle Yuba River Release Facility Length of Stream Affected (mile) 1 MAJOR STORAGE/REGULATION DAMS Minimum Flow Release Requirement in Existing License? Type of Instream Flow Analysis Performed New Bullards Bar Dam 9.9 Yes PHABSIM DIVERSION DAMS Our House Diversion Dam 22.3 Yes Oregon Creek Log Cabin Diversion Dam 16.5 Yes PHABSIM & 2D FYLF Habitat PHABSIM & 2D FYLF Habitat POWERHOUSES RELEASING DIRECTLY INTO A STREAM REACH Yuba River Yuba River Yuba River New Colgate Powerhouse 1.7 No PHABSIM Yuba River Yuba River Yuba River Narrows II Powerhouse 24.3 Yes SRH-2D 1 Cumulative length of affected river until reaching the normal high water level of Englebright Reservoir. Upstream of Englebright Reservoir Opening the low level outlets as described in proposed condition GS2 is expected to be beneficial to aquatic resources in the streams below the dams. Fish populations in Project reaches were generally determined by studies performed in the FERC relicensing process to be healthy and persistent transitional fisheries with age class distributions indicative of natural reproduction. However, several studies suggest that availability of suitably sized spawning gravels is limited. According to YCWA s Technical Memorandum 3-10, Instream Flow Upstream of Englebright Reservoir, rainbow trout spawning WUA was quite limited in most reaches due to patchy and limited distribution of suitable spawning substrate. Where suitable substrate was recorded, the preferred combination of depths and velocities often were not present. Passage of sediments will likely improve habitat by increasing the amount of substrate within the wetted channel available for rainbow trout spawning. Similarly, passing large woody material as described in proposed condition GS3 is expected to be benefitial to general ecosystem functions downstream of Our House and Log Cabin Diversion Dams. Proposed Condition WR2, which pertains to WY determinations, will have a beneficial affect on aquatic resources in the stream reaches downstream of Project Facilities by dictating the 36 For the purpose of YCWA s analysis, minimum flow release is considered the flow measured at the designated compliance point and can be the result of any combination of releases through a Project dam (e.g., low-level release and seepage), controlled or uncontrolled spill over a Project dam (e.g., over a spillway), and accretion. This is also sometimes referred to as minimum streamflow or minimum flow release. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

204 streamflow schedule set forth in Condition AR1. The minimum flows outlined in AR1, were developed by WY, to be appropriate to varying watershed hydrology, while being protective of the existing aquatic resources found in the stream reaches downstream of the aforementioned Project Facilities. Proposed Condition WR4, which implements a streamflow and reservoir monitoring plan will be beneficial to aquatic resources throughout the Project-affected streams downstream of Project Facilities. The Plan, designed to monitor compliance, will ensure minimum discharges are met or exceeded in stream reaches downstream of Our House and Log Cabin Diversion Dams and New Bullards Bar Dam. No adverse effects are expected due to the implementation of Proposed Conditions GEN4 or WR6 which pertain to a Coordinated Operations Plan for and Narrows Project and the continued Operation of New Bullards Bar Reservoir for Flood Control, respectively. Proposed Condition AR7, Aquatic Moinitoring in the Upper Yuba River, includes the periodic monitoring of fish and FYLF as well as periodic monitoring of physical processes including riparian, geomorphology, water quality and water temperature. YCWA s proposed increases in minimum flows and management of spill cessation at Our House Diversion Dam, Log Cabin Diversion Dam and New Bullards Bar Dam, which could affect habitat for resident fish species and FYLF resulting from changes in habitat suitability, water temperature, riparian vegetation, and channel morphology. In addition, YCWA proposes a sediment and LWM pass-through program at Our House and Log Cabin diversion dams, which could also affect habitat for fish species and FYLF. YCWA s Proposed Condition AR7 would periodically monitor stream fish and FYLF at representative locations where they were monitored during relicensing, which would provide a comparison between the distribution, relative abundance, and condition of fish populations and FYLF under pre-license conditions and new license conditions. To facilitate this comparison, Condition AR7 proposes to use the same methods that were used during relicensing, and samples would be taken at the same time of year they were taken during relicensing. Since YCWA proposes to pass sediment through Our House and Log Cabin Diversion dams and excavate sediment as needed from those impoundments, YCWA s proposed Condition AR7 includes channel morphology and riparian vegetation monitoring at co-located sites that were sampled during relicensing. In general, and with some modifications, YCWA followed a step-wise process to develop streamflow releases from Our House Diversion Dam, Log Cabin Diversion Dam and New Bullards Bar Dam. Minimum flow releases are not required from the New Colgate Powerhouse. The process relied heavily on existing information and YCWA studies. The first two steps in the process focused on habitat for the rainbow trout adult life stage or the rainbow trout spawning life stage because, in most Project-affected reaches, rainbow trout is the most important game fish and is the dominant fish species in both abundance and biomass. While juvenile rainbow trout also occur in these reaches, based on a comparison of adult, spawning, and juvenile rainbow trout WUA curves, YCWA concluded that providing habitat for rainbow trout adult or spawning life stages would provide adequate habitat for juvenile life stage (e.g., the flow needed Exh. E - Environmental Report Application for New License April 2014 Page E ,

205 to achieve the adult or spawning WUA peak was almost always higher than the flow needed to meet the juvenile WUA peak). As described in more detail below, YCWA relied on the two primary components (i.e., WUA and HDA) of Study 3.10 to assess the effect of streamflow on habitat for adult or spawning rainbow trout life stages under various minimum flow release schedules. First, YCWA examined the appropriate static 37 WUA curves for rainbow trout adult and spawning life stages to better understand flow-habitat relationships. These are provided above in Section Next, using the HDA, YCWA evaluated all rainbow trout life stages in each of the six study reaches under the No Action Alternative and proposed Project Condition AR1. In addition to minimum streamflow conditions, the proposed Project model run incorporates eight of YCWA s Proposed Conditions WR2, WR3, WR5, WR6, AR2, AR3, AR4, and AR6. Each of these conditions individually or in combination, contributes to the overall streamflows observed downstream of YCWA s Our House and Log Cabin Diversion Dams, and New Bullards Bar Dam. Each proposed condition is described in detail in Appendix E2, and where applicable, in specific resource sections below. As an example, Figure shows a HDA Area Under the Curve (AUC) bar chart for adult rainbow trout in the Our House Diversion Dam Reach of the Middle Yuba River. The example compares, for all Water Years, the monthly average habitat that would occur under the proposed Project minimum streamflow releases to habitat that would occur under No Action Alternative at a given hydrologic node. The example shown is for Node 1, the hydrologic mid point of the stream reach between Our House Diversion Dam and the confluence of the Middle Yuba River and Oregon Creek. 37 Static WUA represents habitat availability for a given discharge but does not include a time component. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

206 Figure Example HDA Area Under the Curve bar chart showing YCWA s proposed Project minimum streamflow to the No Action Alternative (i.e., Base Case) by month for rainbow trout adult for the 41 period of record. Figure shows a HDA AUC bar chart for rainbow trout spawning in the Our House Diversion Dam Reach of the Middle Yuba River. The example compares, for all Water Years, the monthly average habitat that would occur under the proposed Project minimum streamflow releases to habitat that would occur under No Action Alternative flow conditions at a given hydrologic node. The example shown is for Node 1, the hydrologic mid point of the stream reach between Our House Diversion Dam and the confluence of the Middle Yuba River and Oregon Creek. Exh. E - Environmental Report Application for New License April 2014 Page E ,

207 Figure Example HDA Area Under the Curve bar chart showing the Proposed Project and No Action Alternatives (i.e., Base Case) by month for rainbow trout spawning for the 41 period of record. Lastly, using the HDA, YCWA evaluated the effects of YCWA s proposed Project to all other fish species (i.e., Sacramento sucker, Sacramento pikeminnow/hardhead) studied as part of Study As an example of the species comparison, Figure below shows AUC for rainbow trout as well as Sacramento sucker, pikeminnow and hardhead. The example compares, for all Water Years, the average habitat that would occur in August, under the proposed Project minimum streamflow releases to habitat that would occur under No Action Alternative flow conditions at a given hydrologic node. The example shown is for Node 1, the hydrologic mid point of the stream reach between Our House Diversion Dam and the confluence of the Middle Yuba River and Oregon Creek. April 2014 Application for New License Exh. E - Environmental Report 2014, Page E

208 Figure Example HDA Area Under the Curve bar chart showing the Proposed Project and No Action Alternative (i.e., Base Case) by species for August in all water years for the 41 period of record. Four aspects of YCWA s minimum streamflow analysis are worth highlighting. First, using the HDA, YCWA compared the habitat produced under the No Action Alternative to the proposed Project streamflows which incorporate the eight additional proposed conditions listed above. The HDA, provides an essential, comprehensive evaluation of the temporal and spatial habitat conditions that result from Project releases, watershed accretion, spill events and operational management decisions. Second, YCWA s analysis assumed that under the No Action Alternative and YCWA s proposed minimum flow releases, the Project would operate and it would continue to rain and snow in a pattern similar to that documented in the period of record. That is, if under normal operations, a dam spills in the spring, water is transported through the reach for water supply or other reasons, or runoff from snow and rain enters the reach, these would also occur with the proposed Project and minimum flow release the dam would still spill (unless the minimum flow releases were high enough that spills stopped), the dam would continue to release water to meet downstream consumptive needs and for other purposes, and runoff would still enter the reach. YCWA believed that to not acknowledge these conditions in future operations (i.e., to base its minimum flow releases on Node 0) is overly conservative and unrealistic. Third, YCWA s Proposed Condition AR1 aimed to enhance minimum flow releases during the rainbow trout spawning periods of April through June, adjusted by water year. For all other months, YCWA targeted enhanced streamflows for adult rainbow trout, commensurate with Exh. E - Environmental Report Application for New License April 2014 Page E ,