Fish faunal changes in Otsego Lake s Shadow Brook watershed following application of best management practices

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1 Fish faunal changes in Otsego Lake s Shadow Brook watershed following application of best management practices Ryan J. Reynolds 1, Joseph C. Lydon 2 and John R. Foster 3 Abstract: This study was conducted to determine if the application of Best Management Practices in the Shadow Brook watershed (Otsego County, NY) implemented had resulted in significant changes in its fish fauna. Electrofishing and seining surveys were conducted at the same locations sampled by Bassista & Foster in In 2010, 1,070 fish were captured representing 24 species and 7 families. A slight reduction in the fish species and families was observed, and four species of salmonids previously found in the watershed were absent in Application of more BMPs may be required to show significant improvements in the Shadow Brook fish fauna. INTRODUCTION At 4,720 ha (11,660 ac), Shadow Brook is the largest watershed in the Otsego Lake basin and is largest contributor of phosphorus and sediments to Otsego Lake (Harman et. al 1997). Since 46% of the Shadow Brook watershed is farmed (Albright 1996), the USDA Environmental Quality Incentive Program was utilized from 1999 to 2004 to support ten Best Management Practices projects designed to reduce negative effects of agriculture on water quality. Water quality monitoring of Shadow Brook, including temperature, dissolved oxygen, phosphorus, nitrogen, and ammonia have indicated significant improvements in recent years (Denby 2008, Albright & Waterfield 2009). While the application of Best Management Practices has focused on reducing nutrient and sediment pollution of Otsego Lake (Albright 2003), improving the water quality of Shadow Brook is in itself a substantial outcome. Water quality improvements are expected to result in changes in the fish fauna of Shadow Brook. The relative abundance and species composition of stream fishes provide good indicators of the impacts of land use, nutrient input, sediment load and alteration of riparian vegetation (Karr 1981). Prior to the application of Best Management Practices the fish fauna in the Shadow Brook watershed was surveyed by the Department of Environmental Conservation in 1970, Hayes (1990) in 1989, and Bassista and Foster (1995) in Until this study was initiated, no follow-up surveys have been conducted to determine if the watershed management initiatives were resulting in positive changes in the fish fauna of Shadow Brook. The goal of this study was to compare the fish populations of Shadow Brook watershed in 2010 to that of the earlier studies in order to determine if the application of Best Management Practices has resulted in changes in the fish fauna. It is expected that watershed management initiatives that have resulted in improvements in water quality will result in an increase in richness and abundance of intolerant species. 1 Fisheries & Aquaculture Student, Fisheries & Wildlife Dept., SUNY Cobleskill, NY. 2 Robert C. MacWatters Intern in Aquatic Sciences BFS/Fisheries & Wildlife Dept., SUNY Cobleskill, NY. 3 BFS Visiting Researcher/Fisheries & Wildlife Dept., SUNY Cobleskill, NY.

2 MATERIALS AND METHODS In August 2010, the fish fauna of the Shadow Brook watershed was sampled following the protocol and locations utilized by Bassista and Foster (1995). Sites 1, 2, 3, 4, 5, 6, 7, 9, 10, 11, and 13 were too dry to hold fish. All other sites (0, 8, 12, 14, 15, and 16) were sampled (Figure 1). Before sampling, main-stem and tributary sites were cordoned off with blocking seines upstream and downstream. The mouth of Shadow Brook (Site-0) was sampled with a 175 foot long, 8 foot deep, ½ inch mesh haul seine and a 25 foot, fine mesh (1/4 inch) shore seine. Mainstem sites (12, 14, 15, and 16) and tributary site (8) were sampled with a 25 foot, fine mesh shore seine and a Halltech HT-2000 backpack shocker. Fish captured were identified, counted, and returned to the point of capture. Total length of each game fish was measured. Voucher specimens were collected and preserved for unusual species.

3 RESULTS Changes in Species Richness The number of fish captured in this study was 25% higher (1070 fish vs. 854 fish) than in 1994 (Table1). However, the number of species captured dropped from 28 in 1994 to 24 in There was also a drop in the number of fish families captured from 8 families in 1994 to 7 families in Table 1. The species of fish captured at various sample sites in the Shadow Brook watershed in August Family Scientific Name Common Name Mouth 0 Trib. Sites 8 Main Stem Sites Clupeidae Alosa pseudoharengus Alewife Catostomidae Catostomus commersoni White Sucker Cyprinidae Exoglossum maxillingua Cutlips Minnow Luxilus cornutus Common Shiner 2 2 Cyprinella spilopterus Spotfin Shiner 8 8 Phoxinus eos Redbelly Dace Pimephales notatus Bluntnose Minnow Pimephales promelas Fathead Minnow Notemigonus crysoleucas Golden Shiner 9 9 Notropis atherinoides Emerald Shiner 6 6 Notropis hudsonius Spottail Shiner Rhinichthys cataractae Longnose Dace Rhinichthys atratulus Blacknose Dace Semotilus atromaculatus Creek Chub Esocidae Esox niger Chain Pickerel 2 2 Ictaluridae Ameiurus nebulosus Brown Bullhead Noturus insignis Margined Madtom Centrarchidae Micropterus salmoides Largemouth Bass Micropterus dolomieu Smallmouth Bass Lepomis gibbosus Pumpkinseed Lepomis macrochirus Bluegill 1 1 Ambloplites rupestris Rock Bass Percidae Etheostoma olmstedi Tessellated Darter Perca flavescens Yellow Perch Total

4 The family that was absent in the 2010 survey was Salmonidae. Historically four species of trout and salmon have been captured in Shadow Brook. In 1989 brown trout and Atlantic salmon were captured, in 1970 and 1994 brook trout were captured, and in 1994 rainbow trout were captured (Table 2). However, in 2010 none of these four salmonid species were present in Shadow Brook. Table 2. Relative Abundance (%) of fish captured at the mouth, main-stem, and tributaries of Shadow Brook in Family Species Mouth Main Stem Tributaries Salmonidae Brook Trout.8 Rainbow Trout.5 Clupeidae Alewife Catostomidae White Sucker Cyprinidae Cutlips Minnow Common Shiner Spotfin Shiner 3.1 Redbelly Dace Bluntnose Minnow Fathead Minnow Golden Shiner Emerald Shiner Spottail Shiner Longnose Dace Blacknose Dace Creek Chub Fall Fish.5 Pearl Dace 5.4 Redside Dace.2 Esocidae Chain Pickerel Ictaluridae Brown Bullhead Margined Madtom 1.1 Channel Catfish.7 Centrarchidae Largemouth Bass Smallmouth Bass Pumpkinseed Bluegill.3.3 Redbreast Sunfish 2.1 Rock Bass Percidae Tessellated Darter Yellow Perch

5 Changes in Relative Abundance The minnow family (Cyprinidae) dominated the fish fauna of Shadow Brook in 1994 and 2010 (Table 3). The relative abundance of minnows, sunfish (Centrarchidae), catfish (Ictaluridae) and pickerels (Esocidae) throughout the Shadow Brook watershed were similar in the 1994 and 2010 samples. However, there was a substantial increase in the relative abundance of perch/darters (Percidae) and herrings (Clupeidae), while there were decreases in suckers (Catostomidae) and trout (Salmonidae). Table 3. The relative abundance of fish families in Shadow Brook in 1994 and Fish Family 1994 Relative Abundance % 2010 Relative Abundance % Cyprinidae Clupeidae Centrarchidae Percidae Catostomidae Ictaluridae Esocidae.2.1 Salmonidae.4 Changes in Species Diversity While most species were captured in moderate to low numbers, a few species dominated the fish fauna (Table 4). Creek chub (16.1%), alewife (12.5%), tessellated darter (10.1%), and fathead minnow (9.2%) were the dominant species captured in In 1994 white sucker (21.5%), creek chub (19.0%) and blacknose dace (13.4%) were the dominate species in Shadow Brook. Fish communities in which a small number of species are numerically dominate are less diverse than communities in which several different species have similar abundances. Although slightly fewer species were captured in 2010 in comparison to 1994 the fish fauna appeared to be much more evenly distributed in 2010 (Table 4). In 1994 five species were considered abundant, i.e. they made up more than 5% of the total fish captured. These five species accounted for 68.8% of the fish captured, leaving 23 species to make up the remaining 31.2% of the catch. In 2010 nine species were considered abundant making up more than 5% of the total fish captured. The nine species made up 84% of the total fish captured and 15 species making up the other 16%. One of the more abundant species, the fat head minnow is a non-native species commonly sold as bait. Its proportion of the Shadow Brook fish fauna has increased substantially

6 from 3.4% of the fish fauna in 1994 to 9.2% in In 2010 fat head minnows were the 4 th most numerous species captured; while in 1994 it was the 8 th most numerous fish. Fat head minnows made up 46.1% of the tributary fish fauna (Table 2). Table 4. Abundant species, making up at least 5% of the fish fauna of Shadow Brook in 1994 and Family Scientific Name Common Name Clupeidae Alosa pseudoharengus Alewife 12.5 Catostomidae Catostomus commersoni White Sucker Cyprinidae Exoglossum maxillingua Cutlips Minnow 8.6 Luxilus cornutus Common Shiner 6.9 Pimephales promelas Fathead Minnow 9.2 Rhinichthys cataractae Longnose Dace 8.3 Rhinichthys atratulus Blacknose Dace Semotilus atromaculatus Creek Chub Centrarchidae Micropterus salmoides Largemouth Bass 6.6 Lepomis gibbosus Pumpkinseed 8.0 Percidae Etheostoma olmstedi Tessellated Darter 10.1 Changes in Stream Mouth Fish Fauna In 2010, 252 fish representing 16 species and 7 families were captured in the mouth of Shadow Brook (Table 2). This was a slight increase over the 15 species captured in Many of the species (e.g. alewife, emerald shiner, spottail shiner and chain pickerel) and families (e.g. Clupeidae and Esocidae) were only found at the mouth of Shadow Brook and are more typical of the lake ecosystem. In 2010 alewives dominated the catch in the mouth of Shadow Brook. Changes in Main-Stem Fish Fauna In 2010 the four main-stem sites (12, 14, 15, and 16) sampled contained the largest number of fish (621), in 16 species, and 5 families. This represents a net loss of two species in comparison to the 1994 survey. Cyprinids made up 68.1% of the total population of fish in the main-stem. The creek chub made up 21.5% of the total population in the Cyprinidae family. Centrachids, a family of fish most associated with warm-water were noted at every site and made up 41.5% of the total population. The main-stem site-16 at the Mill Road crossing is the last site sampled before the stream mouth, and thus it is the site that should show the cumulative effect of Best Management Practices in the Shadow Brook Watershed. This site was sampled in 1989 (Hayes), 1994

7 (Bassista and Foster) and in 2010 (this study). In 1989 the cobble-pebble substrate of this poolriffle environment had a dusting of silt and the fish fauna was indicative of clean, clear streams. However, in 1994 this site was turbid and covered with a thick layer of silt and the fish that normally occur in clean water, such as margined madtom, longnose and black nose dace, Atlantic salmon and brown trout, were absent. The number of species present fell from 11 in 1989 to 5 in 1994, (Bassista and Foster 1994). While the water was also turbid in 2010 the level of silt appeared to be much less and the number of fish species had increased to 8 (Table 5). However, the clear-water species observed in 1989 had still not returned in Table 5. Presence of fish at Shadow Brook main-stem site-16 at three sample years (1989, 1994 & 2010). Family Species Salmonidae Brown Trout Atlantic Salmon Site-16 Survey Catostomidae White Sucker Cyprinidae Cutlips Minnow Common Shiner Bluntnose Minnow Fathead Minnow Blacknose Dace Creek Chub Longnose Dace Ictaluridae Brown Bullhead Margined Madtom Centrarchidae Largemouth Bass Smallmouth Bass Pumpkinseed Rock Bass Percidae Tessellated Darter Main-stem site-15 was one of the most disturbed areas surveyed. During the survey several cows were in the stream to cool-off and there were no buffer zones to minimize run-off from the pastures. The effects on the stream were apparent with high nutrient input, algae and silt-covered substrate, and warm water. In spite of this, site-15 contained the greatest abundance of fish compared to the other main-stem sites, as well as the highest number of species (14).

8 Changes in Tributary Sites The fish fauna of tributary sites were most influenced by dry conditions. In the summer of 2010 most tributary sites were dry or did not contain fish due to very low water levels (1, 2, 3, 4, 5, 6, 7, 9, 10, 11, and 13). Similarly in 1994 relatively few of the tributary sites (2, 4 and 6) had enough water to support fish. In early spring and late fall most of these tributary sites were observed to contain fish. In 1994 site-8 was not surveyed due to the lack of landowner permission. This site was surveyed for the first time in 2010 and contained 197 fish, 8 species and 4 families. The tributary had relatively little flowing water, and the fish were confined to pools. Site-8 had the third highest number of fish compared to the mouth and main stem sites. Fathead minnow was the dominant species and all other species captured were in small numbers. DISCUSSION Water quality improvements in Shadow Brook in recent years (Denby 2008, Albright & Waterfield 2009) following the application of Best Management Practices were expected to result in fish faunal changes. Reduced nutrients, sediment and temperature were expected to increase species richness and diversity (Karr 1981). However, over the entire Shadow Brook watershed, the number of fish species present was lower in 2010 compared to 1994 in spite of a 25% increase in the number of fish captured in Some positive changes may be occurring in the lower portions of Shadow Brook. At the stream mouth there was an increase in number of species, as well as in the next sample site upstream - main-stem site-16. Site-16 had less silt and turbidity than observed in Further, at this site the number of fish species had increased from five in 1994, (Bassista & Foster 1995) to eight. However, the clear-water species observed in 1989 had still not returned in While it is well established that fish abundance and species composition are impacted by land use, nutrient input, sediment load and alteration of riparian vegetation (Karr 1981), the relationship between the application of BMPs (to reduce nutrient and sediment input and restore riparian buffers) and positive changes in the fish fauna is not as clear cut. For example in Minnesota s Whitewater River watershed, a comparison of instream physical habitat and invertebrate and fish assemblages from farms with BMP to farms with conventional agricultural practices, found that biotic indicators did not respond to local changes and that greater improvements in watershed condition were necessary for changes in biota to be apparent (Nerbonne & Vondracek 2001). In Pennsylvania, several years after BMP implementation (a combination of stream bank fencing, bank stabilization, and installing of rock-lined animal crossings) stream macro-invertebrate density increased in two of the four streams, but fish biomass increased in only one (Carline and Spotts 1998). The lack of dramatic changes in Shadow Brook fish fauna may be because not enough time has elapsed since their implementation. Fish faunal changes in response to the application of BMPs in two Wisconsin streams only occurred after a long period of time had elapsed after implementation (Wang et al. 2002). Their study showed a significant increase in intolerant fishes

9 with a concomitant decrease in the percentage of tolerant fish, which was expected in this study. Perhaps more time needs to have elapsed to allow the BMPs to take effect in Shadow Brook. The application of more BMPs may also be necessary for more dramatic changes to occur in the Shadow Brook fish fauna. For example, during the survey of main-stem site-15 several cows were wading in the stream and there were no buffers to minimize run-off from the pastures. The effects on the stream were apparent with high nutrient input, algae and silt-covered substrate and warm water. Previous research indicates that streams with both riparian and upland BMPs had significant increases in densities of all fish, particularly intolerant coldwater species (Wang et al 2002). In recent surveys Shadow Brook was a marginal trout stream. Only one brook trout, one brown trout, one Atlantic salmon and three rainbow trout were captured in the last three surveys. The lack of salmonid species captured in 2010 indicate that Shadow Brook no longer provides the cold, clean and well oxygenated water that these species require. A Colorado trout stream study showed that three years after stream bank fencing, which excluded grazing livestock from the stream, stream bank vegetation recovered, the channel became narrow and deeper, and trout standing crop was twice the standing crop in the unfenced areas (Stuber 1985). If trout are to return to Shadow Brook more BMPs are needed. ACKNOWLEDGEMENTS Cory Tizzio and Kerry DeMarco assisted in the collection of field data. LITERATURE CITED Albright M.F A preliminary report on the evaluation of changes in water quality in a stream following the implementation of agricultural best management practices. Biological Field Station Annual Report (2003). SUNY Oneonta Biological Field Station. Albright. M. and Waterfield. H Water quality monitoring of five major tributaries in the Otsego lake watershed, summer In 42nd Ann. Rept. (2008). SUNY Oneonta Biol. Fld. Sta., SUNY Oneonta. Bassista,T.P. and J.R. Foster Relative abundance and species composition of fish in Shadow Brook, Otsego County, New York. In 27nd Ann. Rept. (1994). SUNY Oneonta Bio. Field Station. SUNY Oneonta. pp Carline, R. F. and D. E. Spotts, Early reponses of stream communities to riparian restoration in agricultural watersheds, eastern USA. In: Headwaters: Water resources and soil conservation, M. J. Haigh, J. Krecek, G. S. Rajwar, and M. P. Kilmartin (Editors). Proceedings of Headwater 98, the Fourth International Conference on Headwater Control, Merano, Italy.

10 Denby, J Water quality monitoring of five major tributaries in the Otsego Lake watershed, summer In 41 st Ann. Rept. (2008). SUNY Oneonta Biol. Fld. Sta., SUNY Oneonta. Harman, W.N., L.P. Sohacki, M.R. Albright, and D.L. Rosen The State of Otsego Lake, Occasional Paper #30. SUNY Oneonta Bio. Fld. Sta., SUNY Oneonta. Hayes, S. A Preliminary fish survey of the Otsego Lake watershed. In 22th Ann. Rept. SUNY Oneonta Bio. Fld. Sta., SUNY Oneonta. Pp Karr, J.R Assessment of Biotic Integrity Using Fish Communities. Fisheries 6(6): Nerbonne, B. A. and Vondracek B Effects of local land use on physical habitat, benthic macroinvertebrates, and fish in the Whitewater River, Minnesota, USA. Environmental Management, Vol. 28, No. 1, pp Sturber, R. J., Trout habitat, abundance, and fishing opportunities in fenced vs. unfenced riparian habitat along Sheep Creek, Colorado. In: Riparian ecosystems and their management: Reconciling conflicting uses. U.S. Forest Services General Technical Report, RM120, Ft. Collins, Colorado, pp Walker, J.F. & D. J. Graczyk Preliminary evaluation of effects of best management practices in the Black Earth Creek, Wisconsin, priority watershed. Water Science Echnology 28: Wang, L., J. Lyons and P. Kanehl. "Effects of watershed best management practices on habitat and fish in Wisconsin Streams." Journal of the American Water Resources Association 38.3 (2002):

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