Niagara Power Project FERC No. 2216
ECOLOGICAL CONDITION OF GILL, FISH, AND CAYUGA CREEKS
HTML
Format. Text only
Prepared for: New York Power Authority
Prepared by: URS Corporation; Gomez and Sullivan Engineers, P.C.; and E/PRO Engineering & Environmental Consulting, LLC
August 2005
Copyright © 2005 New York Power Authority
___________________________________________________
ABBREVIATIONS
Agencies
EC Environment Canada
FERC Federal Energy Regulatory Commission
INBC International Niagara Board of Control
NYSDEC New York State Department of Environmental Conservation
NYSDOT New York State Department of Transportation
USACE United States Army Corps of Engineers
USEPA United States Environmental Protection Agency
USGS United States Geological Survey
Units of Measure
C Celsius, Centigrade
cfs cubic feet per second
ft feet
L liter
μ micro (prefix for one-millionth)
mg milligram
MW megawatt
NTU Nephelometric Turbidity Unit
Regulatory
SPDES State Pollution Discharge Elimination System
Environmental
DO dissolved oxygen
EAV emergent aquatic vegetation
PCB polychlorinated biphenyl
SAV submerged aquatic vegetation
The New York Power Authority is in the process of applying for a new federal license to operate the Niagara Power Project in New York. At the request of stakeholders, this study was completed to describe the ecological condition of Fish, Gill, and Cayuga Creeks using available aquatic and riparian habitat, fish community, surface and groundwater hydrology, water quality, and land use information. In addition, this study summarizes the primary issues and concerns affecting each creek. Due to the many constraints and impediments inherent in each watershed, restorative actions to improve the ecological and geomorphic function of the creeks are not addressed in this study.
Major issues affecting the ecological condition of Fish, Gill, and Cayuga Creeks include sediment contamination, groundwater flow patterns, stream channelization, natural and man-made fish barriers, and land use and management practices.
Dioxin and PCB contaminated sediment has been dredged from the lower reaches of Gill and Cayuga Creeks. Both Gill (from its mouth upstream to Hyde Park Dam) and Cayuga Creek (from its mouth upstream to Walmore Road) are on the state’s Priority Waterbodies List for “fish consumption precluded” due to toxic and contaminated sediment (NYSDEC 2000). Cayuga Creek is also under a fish consumption advisory from the NYSDOH to “eat none” due to dioxin contamination (NYSDOH 2003).
Lewiston Reservoir acts as a local area of groundwater recharge, and seepage from Lewiston Reservoir acts to increase flow in both Fish and Gill Creeks. In addition, water from Lewiston Reservoir is discharged to Gill Creek to augment naturally occurring flow conditions. The augmentation flow of approximately 3 cfs is typically provided annually from early June to late September. Groundwater is pumped from Redland Quarry, located in the headwaters of the Cayuga Creek watershed, and discharged to a tributary of Cayuga Creek. This circumstance acts to increase streamflow within the tributary, and the cycling of water withdrawals may result in relatively minor water fluctuations
In the lower portion of Fish Creek, reaches have been diverted underground and lined with concrete to facilitate water conveyance through a golf course and recreational park. Fish Creek was also realigned to allow for the construction of Lewiston Reservoir by NYPA. Similarly, the lower reaches of Gill Creek have been channelized to increase water conveyance through industrial areas, including significant sections that have been lined with concrete. Near residentially and commercially developed areas, Gill Creek has been culverted for significant distances. Gill Creek was also realigned to allow for the construction of Lewiston Reservoir by NYPA. In the Cayuga Creek headwaters, several tributaries have been ditched to facilitate drainage from agricultural fields. Reaches in the lower portion of the watershed have been straightened and armored in an effort to reduce shoreline erosion and flooding near residentially and commercially developed area. Also, Cayuga Creek has been realigned and conveyed through culverts to allow for the construction of the Niagara Falls airport runways and related facilities.
Along Fish Creek, six fish barriers (3 culverts, 2 small check dams, and a ATV trail) were identified. Within Gill Creek, two culverts and four small check dams represent barriers to fish movement. Hyde Park Lake Dam prevents movement of fish upstream from the Niagara River as well. In Cayuga Creek, three culverts and several woody debris jams inhibit fish movement.
In the upper portion of the Fish, Gill, and Cayuga watersheds, land use is principally agricultural with some residential development, while the Village of Lewiston is a center of residential and commercial development in the lower portion of the Fish Creek watershed. The City of Niagara Falls is a heavily developed area within the Gill and Cayuga watersheds. Heavy industrial activity is located along the southern part of the city near the mouths of Gill and Cayuga Creeks.
The New York Power Authority (NYPA) is engaged in the relicensing of the Niagara Power Project in Lewiston, Niagara County, New York. The present operating license of the plant expires in August 2007. As part of its preparation for the relicensing of the Niagara Project, NYPA is developing information related to the ecological, engineering, recreational, cultural, and socioeconomic aspects of the Project. This report is part of that effort.
The 1,880-MW (firm capacity) Niagara Power Project (NPP) is one of the largest non-federal hydroelectric facilities in North America. The Project was licensed to the Power Authority of the State of New York (now the New York Power Authority) in 1957. Construction of the Project began in 1958, and first electricity was produced in 1961.
The Project has several components. Twin intakes are located approximately 2.6 miles above Niagara Falls. Water entering these intakes is routed around the Falls via two large low-head conduits to a 1.8-billion-gallon forebay, lying on an east-west axis about 4 miles downstream of the Falls. The forebay is located on the east bank of the Niagara River. At the west end of the forebay, between the forebay itself and the river, is the Robert Moses Niagara Power Plant (RMNPP), NYPA’s main generating plant at Niagara. This plant has 13 turbines that generate electricity from water stored in the forebay. The east end of the forebay is the Lewiston Pump Generating Plant (LPGP). Under non-peak-usage conditions (i.e., at night and on weekends), water is pumped from the forebay via the plant’s 12 pumps into the 22-billion-gallon Lewiston Reservoir, which lies east of the plant. During peak usage conditions (i.e., daytime Monday through Friday), the pumps are reversed for use as generators, and water is allowed to flow back through the plant, producing electricity. The forebay therefore serves as headwater for the RMNPP and tailwater from the LPGP. South of the forebay is a switchyard, which serves as the electrical interface between the Project and its service area.
For purposes of generating electricity from Niagara Falls, two seasons are recognized: tourist season and non-tourist season. By the 1950 Niagara River Water Diversion Treaty, at least 100,000 cfs must be allowed to flow over Niagara Falls during tourist season (April 1 – October 31) daytime and evening hours, and at least 50,000 cfs at all other times. Canada and the United States are entitled by international treaty to produce hydroelectric power with the remainder, sharing equally.
The objectives of this study were to gather scientific information to describe the current ecological condition of Fish, Gill, and Cayuga Creeks. Over time, the Fish, Gill, and Cayuga watersheds have been impacted by several human activities. These activities are associated with social and infrastructural influences in the study area, and to a certain extent power production.
Non-power production influences include the construction of dams and other instream barriers, industrial and municipal waste disposal practices, stream channelization, as well as land use conversion/development. These activities are a direct result of the social, institutional, and infrastructural pressures in the area and may represent significant constraints to restoring the ecological condition of the watersheds. Power production related influences include water level fluctuations, flow diversions, alterations to groundwater flow patterns, and stream channelization.
Section 2.0 of this report describes the ecological condition of Fish, Gill, and Cayuga Creeks in terms of water quality, surface and groundwater hydrology, fish community, land use and ownership, and aquatic and riparian habitat conditions. Section 3.0 describes the influences currently affecting the ecological integrity of each creek Due to the many constraints and impediments inherent in each watershed; restorative actions to improve the ecological and geomorphic function of the creeks are not addressed in this study.
The investigation area includes the watersheds of Fish, Gill, and Cayuga Creeks (Figure 2.1-1). Fish Creek drains a 4.7 square mile watershed and flows westerly approximately 4 miles before emptying into the Lower Niagara River. Elevations in the watershed range from approximately 620 feet at the headwaters, located on the Tuscarora Nation, to approximately 530 feet at the Niagara River confluence in the Town of Lewiston.
The 7.6 mile long Gill Creek originates on the Tuscarora Nation and has a total drainage area of 13.9 square miles. Gill Creek flows south before emptying into the Upper Niagara River approximately 1,000 feet downstream of the NYPA water intake structures. Elevations in the watershed range from approximately 620 feet at headwaters to approximately 560 feet at the Niagara River confluence in the City of Niagara Falls.
The headwaters of the 10.9 mile long Cayuga Creek originate in the Town of Lewiston before flowing through the Tuscarora Nation. The watershed has a total area of 38.6 square miles, and elevations range from approximately 620 feet at the headwaters to approximately 560 feet at the Niagara River confluence in the City of Niagara Falls. Cayuga Creek flows southerly before emptying into the Upper Niagara River via the Little River. Bergholtz Creek, a major tributary, joins Cayuga Creek from the east approximately 5,000 feet upstream from its mouth. The Bergholtz Creek subwatershed has a total drainage area of 14.3 square miles.
The Fish, Gill, and Cayuga watersheds include lands of the Tuscarora Nation and the City of Niagara Falls, Town of Niagara, Town of Wheatfield, Town of Lewiston, and the Village of Lewiston (see Figure 2.1-1). The communities vary in population density from the highly urbanized City of Niagara Falls to less populated areas such as the Towns of Lewiston and Niagara. The lower portions of both Gill and Cayuga Creek flow through heavily urbanized portions of the City of Niagara Falls.
The watersheds are generally located within the central lowlands province of the interior plains physiographic division, near the northern limit of the large Allegheny sedimentary basin, with the Precambrian Shield to the north and the Appalachian tectonic front to the south. The Fish, Gill, and Cayuga watersheds lie between the Niagara Escarpment to the north and Onondaga Escarpment to the south. The land surface between the escarpments is poorly drained and relatively flat.
The Fish, Gill, and Cayuga watersheds are underlain by rocks of the Lockport Dolomite Formation. This middle Silurian aged formation consists of five members: the DeCew, Gasport, Goat Island, Eramosa, and Oak Orchard. The formation is light to medium gray, thin to thick bedded, and contains occasional gypsum or calcite. It is fine to coarsely crystalline, moderately hard, with numerous shale partings.
Soils formed in lake-laid clays and silts cover the majority of the study area, with lesser amounts of soils formed in glacial till and lake-laid silts and very fine sands covering the remaining area.
The waters of Fish, Gill, and Cayuga Creeks are classified as Class C by the NYSDEC. According to NYSDEC standards, the best usage for Class C waters is fishing. In addition, the standards state “the water quality shall be suitable for fish propagation and survival. The water quality shall be suitable for primary and secondary contact recreation, although other factors may limit the use for these purposes” (NYSDEC 1998).
Segments of Gill and Cayuga Creek are on the New York State’s Priority Waterbodies List (NYSDEC 1998). Specifically, Cayuga Creek from Walmore Road to its mouth, and Gill Creek from Hyde Park Dam to its mouth are rated as precluded. A precluded listing indicates that frequent/persistent water quality, or quantity conditions and/or associated habitat degradation prevent all aspects of the waterbody use. These segments of Gill and Cayuga Creeks are classified as precluded due to fish consumption advisories. The cause of fish contamination is primarily priority organic pollutants from contaminated sediment (NYSOH 2003).
Several water quality parameters were monitored during the period from April to November of 2003 (URS and Gomez and Sullivan 2005). Discrete measurements of dissolved oxygen (DO) and turbidity data were collected during both wet and dry conditions from April to November 2003, while continuous temperature data were collected for the same period.
Fish Creek had two water quality sampling sites along its 4.7-mile length (Figure 2.2.1-1). The Fish Creek-01 sampling site (TFC-01) was located adjacent to, and directly east of, the Lewiston Reservoir just before the creek is diverted northward around the reservoir. Four total samples were taken at TFC-01 from May to July 2003 and the data are summarized in Table 2.2.1-1. The creek at this site is often visibly brown and turbidity at this site is high at an average of 18.9 NTU. Dissolved oxygen at site TFC-01 averaged 6.2 mg/L (59.7% saturation) and dropped to an extremely low level on 6/26/03 with a minimum measurement of 0.6 mg/L (5.6% saturation). This was due to extremely low flow conditions at the sampling site. Average monthly temperature ranged from 9.4°C (April) to 21.5°C (July). Sampling stopped in July because Fish Creek went dry upstream of Garlow Road (URS and Gomez and Sullivan 2005).
The Fish Creek-02 site (TFC-02), where 17 DO/turbidity samples were collected from April to November (Table 2.2.1-1), is located to the north of the Lewiston Reservoir as the creek flows west, about 1.5 miles downstream of site TFC-01 (Figure 2.2.1-1). Turbidity at this site is also high at an average of 17.2 NTU, but DO is higher relative to TFC-01 with an average of 9.2 mg/L (88.2% saturation) and a minimum of 7.7 mg/L (74.3% saturation). Average monthly temperature ranged from 8.3°C (November) to 16.5°C (July & August). Temperature at the downstream site TFC-02 is consistently lower than at TFC-01. This was especially true during the summer months of June and July when monthly average water temperatures were 3.5 to 5.0°C cooler at TFC-02.
The 7.6 mile long Gill Creek also has two sampling sites located adjacent to the reservoir (Figure 2.2.1-1). The Gill Creek-02 site (TGLC-02) is located directly east of the Lewiston Reservoir just before the creek is diverted south around the reservoir. Turbidity at this site is high with an average of 15.7 NTU (Table 2.2.2-1). DO at GC-02 averaged 7.6 mg/L (73.4% saturation) with a low of 4.1 mg/L (39.8% saturation). Average monthly temperature ranged from 7.6°C (November) to 21.0°C (July). The TGLC-02 site was moved approximately 10,000 feet downstream just above the confluence with the flow augmentation channel on July 10 due to low flow conditions at the original site.
The Gill Creek-01 site (TGLC-01) is located within the flow augmentation channel along the south side of the reservoir approximately 1.5 miles downstream of the original site TGLC-02. Water from Lewiston Reservoir is discharged to Gill Creek through the augmentation channel to supplement naturally occurring flow conditions. This augmentation flow from Lewiston Reservoir ranges from a high of approximately 3 cfs in the summer and falls to zero in the winter and spring. In 2003, flow from the Lewiston Reservoir was supplied to Gill Creek from June 2 through September 23. The purpose of the augmentation flow is to enhance recreational use of Gill Creek in the Hyde Park area.
DO in the flow augmentation channel is higher than in the main stream channel with an average of 9.2 mg/L (91.8% saturation) and turbidity is lower at an average of 4.6 NTU (Table 2.2.2-1). The minimum DO measurement at TGLC-01 was 7.2 mg/L (69.4% saturation). Average monthly temperature ranged from 9.1°C (April) to 23.3°C (August).
Cayuga Creek is the longest of the three creeks at 10.9 miles and had three sampling locations (Figure 2.2.1-1). Cayuga Creek-03 (CC-03) is the most upstream site, located just below Porter Road, where turbidity averaged 16.6 NTU and DO levels averaged 9.6 mg/L (96.7% saturation) with a minimum of 6.6 mg/L (73.2% saturation) (Table 2.2.3-1). Average monthly temperature ranged from 11.6°C (April) to 21.6°C (August).
The next station is Cayuga Creek-02 (CC-02) located approximately 1.4 miles downstream from CC-03 at the confluence with Bergholtz Creek. Turbidity at this site is higher than at CC-03 (average 36.4 NTU) and DO is slightly lower averaging 5.6 mg/L (57.2% saturation) with a minimum of 3.8 mg/L (41.1% saturation). This effect is likely due to the inflow of the slow-moving and turbid Bergholtz Creek. Average monthly temperature ranged from 11.4°C (April) to 21.6°C (August).
The most downstream site is Cayuga Creek-01 (CC-01) and it is located at the mouth of the creek in the Little River. Turbidity levels averaged 16.1 NTU and DO averaged 7.3 mg/L (76.5% saturation) with a minimum of 5 mg/L (55.7% saturation). Average monthly temperature ranged from 8.5°C (April) to 24.4°C (August). Overall, temperatures at the three sites are very similar with the exception of August and September at CC-01 remaining approximately 3ºC higher than at the upstream gages.
There are no historic flow data available for Fish, Gill, and Cayuga Creeks. However, annual and monthly (10%, 30%, 50%, 70%, and 90%) flow exceedances for Fish, Gill, and Cayuga Creeks were estimated using a multiple regression analysis (between drainage area and precipitation) based on observed average daily flows at thirteen USGS gage stations located on unregulated streams in the Niagara River region (URS et al. 2005a). The results of this analysis are described below, as well as other characteristics related to the groundwater hydrology of several areas within the Fish, Gill, and Cayuga watersheds (URS et al. 2005b).
Table 2.3.1-1 illustrates the estimated flow exceedances for Fish Creek at its confluence with the Lower Niagara River. The estimated annual median flow (50% flow exceedance) for Fish Creek is 3.7 cfs, while the median monthly flow ranges from a low of 0.7 cfs (October) to a high of 13.2 cfs (March). These flows would be the expected total runoff at the mouth of Fish Creek, absent any wastewater discharges or other man-made inputs. Fish Creek is not influenced by water level fluctuations in the lower Niagara River due to a steep man-made outfall at the mouth of the creek just before it enters the river. The outfall is located above the elevation of the lower Niagara River; therefore, the river flow does not backwater the creek.
The construction of Lewiston Reservoir has resulted in increased groundwater table elevations in the immediate vicinity of the reservoir. Specifically, Lewiston Reservoir acts as a local area of groundwater recharge. This situation has acted to increase groundwater input to Fish Creek near the reservoir; thus, increasing streamflow (URS et al. 2005b). The streamflow estimates described in the previous paragraph do not reflect additional groundwater input attributable to Lewiston Reservoir.
Estimates of flow exceedance for Gill Creek at its confluence with the Upper Niagara River are depicted in Table 2.3.2-1. The estimated annual median flow (50% flow exceedance) is 10.4 cfs, while the median monthly flow ranges from 2.5 cfs (September and October) to 35.7 cfs (March). These flows would represent total runoff at the mouth of Gill creek, absent any wastewater discharges or other man-made inputs.
There are no official water level data available along Gill Creek and it is not known how far upstream Niagara River water level fluctuations affect Gill Creek. The upstream extent of water level fluctuations will depend on the discharge and channel slope of Gill Creek and will not extend farther than approximately 7,000 feet where the Hyde Park Dam serves as a barrier.
Water from Lewiston Reservoir is discharged to Gill Creek to augment naturally occurring flow conditions. The purpose of this augmentation is to enhance the recreational use of Gill Creek as it flows through Hyde Park by reducing stagnation and improving the appearance of the creek. The augmentation flow of approximately 3 cfs is typically provided annually from early June to late September. For instance in 2003, flow from the Lewiston Reservoir was supplied to Gill Creek from June 2 through September 23.
Similar to Fish Creek, Gill Creek in the vicinity of
Lewiston Reservoir also receives additional streamflow from increased
groundwater input (URS et al. 2005b). The streamflow estimates described in the
previous paragraphs do not reflect additional groundwater input or flow
augmentation attributable to Lewiston Reservoir.
Shown in Table 2.3.3-1 are the estimated flow exceedances for Cayuga Creek at its confluence with the Upper Niagara River. The estimated annual median flow (50% flow exceedance) is 27.5 cfs, while the median monthly flow ranges from a low of 7.1 cfs (September) to a high of 91.3 cfs (March). The estimate includes contributions made from Bergholtz Creek, which enters Cayuga Creek approximately 5,600 feet upstream of Cayuga Creek's confluence with the Upper Niagara River (Table 2.3.3-2). The annual median flow is 17.7 cfs at Bergholtz Creek, while the monthly median flows ranged from 4.4 cfs (September) to 59.6 cfs (March). These flows would represent total runoff at the mouth of each creek, absent any wastewater discharges or other man-made inputs.
Hydraulic modeling of Cayuga Creek indicates that Upper Niagara River flow fluctuations affect approximately 10,800 feet of the creek under annual median flow conditions (27.5 cfs). This length would extend to a point approximately 2,000 feet downstream of the Porter Road bridge crossing. In addition, Upper Niagara River fluctuations would influence Bergholtz Creek water levels for approximately 10,950 feet for annual median flow conditions (17.7 cfs) (URS et al. 2005a).
Based on sampling conducted during 2003, near the mouth of Cayuga Creek and extending upstream to Bergholtz Creek, water levels fluctuate about 1 foot daily. Water level information collected further upstream near Porter Road indicated fluctuations of around 0.3 feet daily (URS and Gomez and Sullivan 2005).
Water withdrawn from the Redlands Quarry is discharged into Cayuga Creek via a small tributary that enters within the Niagara Falls Naval Air Station. This circumstance acts to increase streamflow within the tributary, and the cycling of water withdrawals may result in relatively minor water fluctuations. The streamflow estimates described in the previous paragraphs do not reflect inputs attributable to the Redlands Quarry discharge.
Surveys of fish have been conducted by several state and
federal agencies in the last 15 years, and a survey was also conducted by the
State of New York Conservation Department in 1928. NYPA has not conducted any formal surveys of
the fish communities in the three creeks, but observations of several fish
species were made during the habitat mapping described in Section 2.5. In general, Gill and Cayuga Creeks have a
warmwater fish community that is dominated by forage fish species (e.g.,
minnows). Some sport fish species (e.g.,
northern pike, bass, perch, bullhead, and crappie) reside in Gill and/or Cayuga
Creeks as well. Fish Creek appears to
contain minnow species as well, but less is known about the fish species that
are present in Fish Creek.
No surveys of the fish community in Fish Creek have been conducted by state or federal agencies. While conducting the habitat mapping of Fish Creek (Section 2.5), minnows (Cyprinidae family) were observed although no fish were identified to the species level.
During a survey of Gill Creek in 1928, several fish
species were collected (Greeley 1929). These species were “common sunfish”
(pumpkinseed sunfish, Lepomis gibbosus),
grass pickerel (Esox americanus
vermiculatus), golden shiner (Notropis
cornutus), bluntnose minnow (Pimephales
notatus), white sucker (Catostomus
commersoni) and brown bullhead (Ictalurus
nebulosus). NYSDEC collected fish at
the mouth of Gill Creek in 1988 as part of a “Statewide Toxics Monitoring
Program” (NYSDEC 1988). Only three fish species (Cyprinus carpio, common carp; Aplodinotus
grunniens, freshwater drum; and Moxostoma
spp., redhorse species) were
caught in the 100 feet of 4 inch gill net.
Because the gill net mesh was large (4 inches), small individuals (less
than <approximately 16 inches) would not likely have been caught. Therefore, smaller species would not have
been documented during this survey.
Currently, crappies (Pomoxis spp.), bullheads (Ictalurus spp.), and other panfish (presumably Lepomis spp.) are stocked into Hyde Park Lake (NCDPDT 2001).
While conducting the habitat mapping of Gill Creek (Section 2.5), several fish species were observed. A single yellow perch (Perca flavescens) and a small school of approximately a dozen suckers around 12” in length were observed where the augmentation channel enters the creek. The suckers were likely either white suckers or northern hog suckers (Hypentelium nigricans). Common carp were also observed in the section below the rail yard and through the Hyde Park Golf Course.
Several fish collections have been made in various locations in Cayuga from 1928 to 2001 by state and federal agencies. The present fish community is dominated by warm water forage species. Very few sport fish species are found in Cayuga Creek, and those species are represented by very few individuals. Table 2.4.3-1 lists the fish species collected in Cayuga Creek since 1928.
While conducting the habitat mapping of Cayuga Creek (Section 2.5), several fish species were observed. In the upper reaches (on the Tuscarora Nation to around Lockport Road), there were isolated pools which contained small fish.. Some of the fish found associated with these isolated pools were found dead. The fish species observed in these areas were brook stickleback (Culaea inconstans), central mudminnow (Umbra limi), and unidentified minnow species. Also observed was a dead sunfish, most likely a green sunfish (Lepomis cyanellus) or a rock bass (Ambloplites rupestris). In Cayuga Creek on the Niagara Falls Airport, a large (approximate size) northern pike (Esox lucius) was observed. Also, in the airport vicinity, fish were observed that were most likely common carp.
For the purposes of this study, Fish, Gill, and Cayuga Creeks and their tributaries can be divided into several discrete reaches based on distinctive physical characteristics, surrounding land use, and human alterations made to each stream. The aquatic and riparian habitat conditions of each reach within the study creeks are discussed below. This discussion is based on reconnaissance level habitat mapping of the creeks that occurred during the summer of 2003. For each creek, the entire reach of stream was walked with the exception of Bergholtz Creek, and the unnamed tributary of Gill Creek. For the two tributaries, a desktop analysis using 2002 digital orthophotos was conducted to estimate average stream width, riparian buffer widths, and potential fish barriers. For both tributaries, additional habitat information described below was gathered at road crossings and also to verify the orthophoto interpretations.
Habitat
types were designated as riffle, run, pool, dry streambed, and wetland
habitats, based on visual flow, turbulence, depth, gradient, and
vegetation. Habitats or “stream
sections” were mapped for a distance of 656 feet (200 meters), or until the
habitat type changed. Stream section length,
average wetted width, average depth, gradient, substrate, bank slope (mean for
both sides of the creek in percent slope), turbidity, water odor, average
riparian buffer width (mean for both sides of the creek), dominant riparian
vegetation type and species, and species of emergent and submergent aquatic
vegetation were measured or estimated for each section. Stream section length was measured from the
upstream to downstream end of each section using GPS. Depth was measured at three transects within
the stream section (middle of the habitat and the upstream and downstream quarter
points) and across each transect at three locations (thalweg, non thalweg river
right, non thalweg river left).
Measurements were then averaged to determine a mean depth for each
stream section. Gradient was measured
with a clinometer from the upstream to downstream end (water surface) of each
section. Dominant substrates, average
riparian buffer width, bank slope (percent slope), turbidity, and dominant
instream cover were estimated visually as an average over the entire stream
section. Substrate categories are
described in Table 2.5-1
and dominant riparian vegetation types are described in Table 2.5-2. Bank slopes were grouped into four categories
shallow (<30% slope), moderate (30-50% slope), steep (>50% slope), and
undercut, and turbidity was classified according to four categories (clear,
opaque, slightly turbid, and turbid)
Reach F0 begins at the Niagara Falls Country Club and continues downstream approximately 1,400 feet to where it empties into the Niagara River Gorge (Figure 2.5.1-1). The entire reach from the Country Club to the gorge is diverted underground through a culvert. The only portion not underground is where the creek descends into the gorge over a waterfall referred to as the Slime Chute (Figure 2.5.1-2). The steep drop into the gorge isolates Fish Creek from any water level fluctuations that occur within the lower river, and prevents any fish movement upstream into Fish Creek from the Niagara River. Due to its nature, this reach was not mapped in any detail during the habitat reconnaissance portion of the study.
Reach F1 located just upstream of where Fish Creek goes underground at the Robert Moses Parkway, traverses approximately 1,900 feet through the Niagara Falls Country Club Golf Course (Figure 2.5.1-3). This is a highly altered portion of Fish Creek. The creek parallels Lewiston Road through 400 feet of straightened stream channel with one small road crossing consisting of approximately 20 feet of corrugated culvert pipe (Figure 2.5.1-4). The creek then bends 90 degrees to the west and continues under Lewiston Road approximately 100 feet through another corrugated culvert pipe. The remaining stream section through the golf course is characterized by a concrete lined stream channel that extends downstream nearly 1,400 feet (Figure 2.5.1-5). Within the reach there are no barriers or obstructions that would prevent fish movement; however, water depths within the concrete lined portion of the channel are most likely not sufficient to support fish.
The channelized section of creek along Lewiston Road is comprised of 50% riffle and 50% run habitat types. The average wetted width in the riffle sections was 7.9 feet, and the average depth 0.3 feet. Sections identified as run habitat had an average wetted width of 9.3 feet and an average depth of 0.5 feet. Stream banks along the right side of the creek are shallow while banks on the left side of the creek along Lewiston Road are moderately steep; however, both sides of the creek are devoid of forested riparian buffers. Stream banks are dominated by Kentucky bluegrass (Poa pratensis), redtop (Agrostis gigantea), and purple loosestrife (Lythrum salicaria) a common invasive species. This section also supports two species of submerged aquatic vegetation including water milfoil (Myriophyllum spp.), and elodea (Elodea spp.), Watercress (Rorippa nasturtium-aquaticum), a species of emergent aquatic vegetation, is also found. Substrate is dominated by small and large cobble which appears to be broken concrete and riprap from alongside Lewiston Road. Cobble is also the most dominant instream cover within this portion of the reach.
The concrete lined portion of the reach is also devoid of forested riparian buffers and supports no aquatic vegetation. Riparian vegetation consists primarily of Kentucky blue grass and yellow clover (Trifolium aureum) that is mowed to the edge of the concrete channel. The habitat type within the concrete lined channel was classified as a riffle with an average wetted width of 14.0 feet, and an average depth of 0.2 feet. Water depth across the channel is uniform, and instream cover is completely absent.
Reach F2 is located between two portions of the Niagara Falls Country Club (Figure 2.5.1-6). The approximately 2,500 feet of meandering stream reach crosses under Military Road for a distance of 55 feet, and continues downstream through a forested section, and behind a residential neighborhood on Meadow Brook Road. Within the neighborhood portion of the reach, some residential properties directly abut the stream channel (Figure 2.5.1-7). In this section, individual management practices vary greatly, ranging from rip-rap and plantings to grasses mowed to the edge of the stream; however, nothing within the reach was identified as a potential barrier to fish movement.
Habitat within the reach is a mix of 67% run, 25% riffle, and 8% pool habitat types. Runs, riffles, and pools had an average wetted width of 9.8, 10.6, and 10.4 feet, and an average depth of 0.6, 0.4, and 0.8 feet respectively. There is little gradient throughout the reach (generally <1%), and stream banks are mostly shallow except for a short (approximately 265 feet) rip-rapped portion with steep banks located in the residential section. Riparian buffers dominated by a mix of tree, shrub and herbaceous species are generally less than 50 feet in width. Within the reach, five invasive species including common buckthorn (Rhamnus cathartica), garlic mustard (Alliaria petiolata), multiflora rose (Rosa multiflora), Norway maple (Acer platanoides), and tartarian honeysuckle (Lonicera tatarica) were identified. Aquatic vegetation was generally sparse with a few sections containing Lizard’s Tail (Saururus cernuus), water milfoil and curly leaf pond weed (Potamogeton crispus), an invasive species in New York. Substrate is a mix of large and small cobble except at the upstream end of the reach near the golf course where substrate is dominated by silt. The dominant instream cover is a mix of large cobble and overhanging cover.
Located upstream of Military Road, reach F3 flows through the upstream section of the Niagara Falls Country Club Golf Course (Figure 2.5.1-8). The reach, slightly less than 1,400 feet in length, crosses under four small golf cart path bridge crossings. Unlike reach F1 discussed above, this portion of stream channel has not been concrete lined. Throughout the reach no obstructions that may inhibit fish movement were identified.
Habitat within the reach consisted of a series of low gradient (<0.5%) runs with an average wetted width of 7.6 feet and an average depth of 0.8 feet. Stream banks have a shallow slope and riparian buffers dominated by herbaceous vegetation are all less than 25 feet in width. Similar to reach F1, riparian buffers along the creek are mowed to the edge of the stream (Figure 2.5.1-9). Two invasive species including multiflora rose and purple loosestrife were also identified within the reach. Emergent aquatic vegetation consists of watercress, and spike rush (Eleocharis palustris), while submergent species include elodea, water milfoil, coontail (Ceratophyllum demersum), and curly leaf pond weed an invasive species. The aquatic vegetation was the only instream cover within the reach, and no overhanging cover was available for stream shading. Substrate is dominated by silt and muck, and very turbid water was noted throughout the reach at the time of sampling.
Reach F4 begins where Fish Creek is diverted around the Lewiston Reservoir and extends downstream approximately 6,900 feet to the N