Water Quality Report

WATER QUALITY REPORT

HEALTH OF CANANDAIGUA LAKE AND TRIBUTARY STREAMS

Dr. Bruce A. Gilman ([email protected]) Department of Environmental Conservation and Horticulture Finger Lakes Community College 4355 Lakeshore Drive Canandaigua, New York 14424

and

Kevin Olvany ([email protected]) Watershed Program Manager 205 Saltonstall Street Canandaigua, New York 14424

Prepared for:

Canandaigua Lake Watershed Council 205 Saltonstall Street Canandaigua, New York 14424 Table of Contents:

Executive Summary ...... 3

Acknowledgments ......

List of Figures ......

List of Tables ......

Introduction to Water Quality......

Chapter 1 – Canandaigua Lake Research

Canandaigua Lake Sampling and Monitoring Parameters ......

Methods ......

Results and Discussion ......

Chapter 2 – Tributary Research

Methods ......

Results and Discussion ......

Recommendations and Topics for Future Research ......

Literature Cited ......

2 Executive Summary:

1. Over the last three years, the health of Canandaigua Lake remained good to excellent. Dissolved oxygen was available throughout the water column at all monitoring times and often was at or near 100% saturation, ideal conditions for the survival of aquatic life. Seasonal temperature profiles characterized the development of thermal stratification typical of deep lakes. The pH was always above 7.00 (due to high buffer capacity of lake water), helping to protect the lake from the damaging effects of acidic precipitation storm events. Conductivity, a measure of ions dissolved in the water, averaged between 350 and 400 μS/cm. Recent increases in conductivity may stem from watershed development activities. Total phosphorus, the critical nutrient governing lake productivity and the element most responsible for lake eutrophication, was often below 10 μg/L during the monthly sample periods. Algal productivity, estimated by the concentration of chlorophyll a, ranged from 0.62 to 9.48 μg/L with a mean of 2.41 μg/L.

2. The average Carlson trophic state index of lake health continues to suggest that Canandaigua Lake remains an oligotrophic water body, however, the index based solely on chlorophyll a levels points to a mesotrophic state. Winter total phosphorus measurements should be conducted to prove or disprove this apparent trend towards nutrient enrichment.

3. Eelpot Creek contains the highest long-term total phosphorus concentration of all sampling locations (0.269 mg/L) and slightly exceeds the median concentration levels for total phosphorus in the NURP study. While steep gradient is one possible explanation, but it seems likely that excess sediments may also enter the creek where it flows over the Valley Heads moraine.

4. Gage Gully had the highest average nitrogen concentration over the last nine years with 4.11 mg/L. Deep Run was second with 2.95 mg/L. Fall Brook was third with 2.37 mg/L. Sucker Brook was fourth with 1.55 mg/L. Vine Valley was fifth with 1.21 mg/L. The long-term data show consistency from year to year. The National Urban Runoff Program (NURP) studies list a median concentration of 0.53 mg/L, thus these five streams are substantially higher than the NURP threshold.

4. Fisher Gully had the highest long-term concentration of total suspended solids with 398.8 mg/L. A substantial portion of the total suspended solids found in the watershed result from anthropogenic activities.

5. Based on approximately 70 samples from 1989 to 2005, Sucker Brook had the highest long- term concentration of fecal coliform with 725 colonies per 100 ml . These results suggest that the water is impacted by human wastes.

6. The annual road salt monitoring revealed lower than normal chloride concentrations (mg/L) in most tributary streams, with critical levels being exceeded only in Sucker Brook and the stream entering the lake at Cook’s Point. Although sampling is a “once a year snapshot”, these data reflect the severity of the winter seasons and the subsequent amounts of de-icing agents applied to highway surfaces.

3 Acknowledgments:

This research was supported by the 14 municipalities comprising the Canandaigua Lake Watershed Council (Town of Bristol, City of Canandaigua, Town of Canandaigua, Town of Gorham, Town of Hopewell, Town of Italy, Town of Middlesex, Town of Naples, Village of Naples, Village of Newark, Town of Palmyra, Town of Potter, Village of Rushville, Town of South Bristol). We thank them for their continuing financial support and cooperative work in safeguarding the water quality of the lake.

We also thank our interns, Alison Nihart, Alison Muehe, Kim Babcock and Valerie George for helping with data summary, graph preparation and editorial comments.

Finger Lakes Community College provided administrative assistance from the Office of Resource Development and document reproduction through Central Office Services. The Science and Technology Department generously donated laboratory facilities. Use of boats and sampling equipment were provided by the Department of Environmental Conservation and Horticulture. Practicum students at the college helped collect scientific information, gained experience with equipment, presented findings at local conferences, and learned the value of limnological research programs.

4 List of Figures:

1.1 Development of thermal stratification in Canandaigua Lake, Deep Run Station. 1.2 Development of thermal stratification in Canandaigua Lake, Seneca Point Station. 1.3 Dissolved oxygen profiles in Canandaigua Lake, Deep Run Station. 1.4 Dissolved oxygen profiles in Canandaigua Lake, Seneca Point Station. 1.5 Secchi disk readings in Canandaigua Lake. 1.6 Chlorophyll a concentrations among sample stations in Canandaigua Lake. 1.7 Recent water quality trends in lake clarity and algal abundance. 1.8 Long-term trends in mean annual total phosphorus in Canandaigua Lake. 2.1 Canandaigua Lake sub-watersheds and direct drainage basins. 2.2 Total phosphorus weighed concentrations 1997-2005. 2.3 TSS weighted average concentrations 1997-2005. 2.4 NO3-NO2 weighted average concentrations 1997-2005. 2.5 Fecal coliform levels, 1989-2005. 2.6 Road salt contamination in Canandaigua Lake tributaries. 2.7 Long-term watershed chloride trends based on mid-winter sampling, 1990-2006.

List of Tables:

1.1 Secchi disk readings (m) in Canandaigua Lake. 1.2 Chlorophyll a concentrations (μg/L) in Canandaigua Lake. 1.3 Ratio between shoreline (n = 3) and mid-lake (n = 2) chlorophyll a concentrations. 1.4 Total phosphorus data exceeding 10 μg/L, April 2003 through November 2005. 1.5 Seasonal profiles for total phosphorus (μg/L) at the two mid-lake sampling stations. 1.6 Monthly variation in mean inorganic nitrogen (NO3 + NO2 mg N/L) for mid-lake and shoreline sampling stations. 1.7 Information pertaining to the Carlson Trophic State Index (TSI). 1.8 Carlson TSI values for Canandaigua Lake. 2.1 Precipitation measurements and runoff totals during each storm event, 2001-2005. 2.2 Stream rankings, 1997-2005. 2.3 Combined average concentrations for each of the streams from 1997-2005. 2.4 Concentrations of nitrate/nitrite in Grimes Creek Raceway. 2.5 Concentrations of phosphorus, TSS, and nitrate/nitrite in the West River. 2.6 Chloride concentration (mg/L) in Canandaigua Lake tributaries, 2003-2006.

5 Introduction to Water Quality:

This three year report updates our knowledge on the water quality of Canandaigua Lake and its tributary streams. The comprehensive, holistic approach utilized here draws on our research efforts and the historic work of others in order to better understand the consequences of human activities on water quality. Our primary goal is to inform and educate the Council and general public about significant issues that can adversely affect the lake. Our activities include extensive sampling and monitoring as well as a recent emphasis on predictive modeling utilizing many resource data bases in a geographic information system (GIS).

While certain aspects of lake ecology have been studied since the early 1900’s, until recently the scientific research efforts have been sporadic. For the last 13 years, a regular sampling and monitoring program has reported on lake quality. This program provides an annual assessment of lake health and long-term analyses that, overall, suggest the lake remains clean and relatively pollution-free. However, concerns about the impacts of changing watershed land uses (e.g., residential development, forestry, agriculture, storm-water management) on lake water quality have arisen. Therefore, monitoring of perennial tributary streams and direct drainage sub-basins became a focus of our research during the mid 1990’s. Watershed drainages have been sampled under baseflow conditions and during meteorological events (e.g., storm runoff and snow melt runoff episodes). Streams contributing significant pollutants to the lake have been studied through segment analysis, helping to identify pollutant sources so remedial actions could be put in place.

Point and non-point sources of pollution are well known for most water bodies but the relative significance among sources is not as clearly understood. Consistent and comprehensive sampling and monitoring programs can help determine the importance of point and non-point sources of pollution. Lake research coupled with watershed-wide stream pollutant sampling and monitoring for indicators of environmental degradation are essential steps in determining water condition. Knowledge of water condition should assist local municipalities in policy decisions and in the selection of watershed best management practices (BMPs) designed to restore, enhance and protect water quality.

6 CHAPTER 1 – CANADAIGUA LAKE RESEARCH

Canandaigua Lake Sampling and Monitoring Parameters: To better understand the health of Canandaigua Lake, the following water quality tests, sampling frequencies and synthetic indices have been used. A brief explanation of each water quality parameter is provided here. 1. temperature - heat content of a water body expressed in Centigrade degrees (ºC). It is important to water circulation patterns in the lake (e.g., seiches and timing of fall turnover), stability of lake stratification, prediction of winter ice cover, metabolic rate of lake organisms, buoyancy afforded to the planktonic community and habitat diversity. Patterns in lake temperature across the water column document the extent of the summer warm water zone at the surface (the epilimnion) and the cold water zone near the bottom (the hypolimnion).

2. dissolved oxygen - oxygen present as a gas (O2) dissolved in the lake water. It is essential for the respiration of most desirable aquatic organisms, particularly fish and invertebrates. Cold water has the potential to hold greater amounts. Relative content of dissolved oxygen (DO) is measured as percent saturation. It is desirable to be at or near 100% saturation. Absolute content of DO is measured as parts per million (ppm) or its equivalent, milligrams per liter (mg/L). It has low solubility in water, with maximum amounts seldom exceeding 14.6 mg/L. Cold water fish species like trout require a minimum DO of 7 to 8 mg/L. Warm water fish species like bass are more tolerant but still require a minimum DO of 5 mg/L. DO is positively correlated with atmospheric pressure. DO concentration is influenced by replenishment rates (contribution from aerated tributary streams, surface exchange with the atmosphere, amount of aquatic photosynthesis) and consumption factors (respiratory demands of lake organisms, amount of oxygen demanding wastes). If DO levels drop to near zero, the lake water is anoxic, nutrients are released from bottom sediments and undesirable anaerobic biota will predominate. Such conditions have not been recorded in Canandaigua Lake. 3. conductivity - the ability of water to support an electrical current. It is strongly influenced by ionic concentrations (Ca++, Mg++, Na+ and K+) and water temperature. Expressed as micromhos/cm or its equivalent, microsiemens (μS/cm). Addition of suspended soil particles

7 from storm runoff and watershed erosion activities will temporarily increase conductivity. Seiches that re-suspend bottom sediments may locally increase conductivity readings. 4. chlorophyll a – a plant pigment that estimates algal abundance and, therefore, indicates plant growth conditions. Measured as μg/L or its equivalent mg/m3. Primary production refers to organic molecules synthesized by plants according to this formula:

6CO2 + 12H2O + energy → C6H12O6 + 6O2 + 6H2O Energy for this photosynthetic reaction is provided when sunlight penetrates water in the epilimnion. Plant pigments, especially chlorophyll a, are receptors for this incoming sunlight. 5. water clarity - the depth of light penetration in the surface waters of a lake. It is determined with a secchi disk and expressed in meters. When compared with underwater photometer measurements, the secchi disk reading approximates the depth where 5% of the surface light remains. This is the compensation level for most aquatic plants. For the Finger Lakes, it is estimated that all surface light is gone at two to three times the secchi disk reading. Lake clarity is influenced by suspended sediment and planktonic organisms. 6. lake nutrients - compounds that promote biological growth in water. Several elements are considered essential, but the critical elements in lakes are phosphorus and nitrogen. Phosphorus is often considered the limiting factor for biological productivity in freshwater ecosystems. Phosphorus is needed for the production of cellular energy compounds. It is present as both inorganic and organic substances, including particulate and dissolved forms. Total phosphorus (TP) includes dissolved and particulate forms. It is expressed as parts per billion (ppb) or its equivalent, micrograms per liter (μg/L). The desirable threshold is 10 μg/L. TP concentrations that exceed 20 μg/L suggest nutrient enrichment. Up to ten percent of the TP is likely to be found in a dissolved form known as soluble reactive phosphorus (SRP). Most phosphorus is biologically absorbed or temporarily bound to bottom sediments from which it is released back to the water if benthic DO is low. During rapid growth of aquatic plants, all of the SRP can be absorbed. Then, lake processes would slow until phosphorus again became available through biological decay, bottom release or watershed contributions. Recycling of phosphorus in small lakes has been estimated to be a matter of days or weeks while for larger lakes it can take months. Also a macronutrient, nitrogen contributes to protein synthesis in lake organisms. Nitrogen compounds commonly enter lakes through fertilizer runoff and biological decay.

8 Decomposition processes release ammonia (NH3), which may be harmful to aquatic life in high

concentrations. In most lakes, ammonia is oxidized to inorganic nitrite (NO2) and then nitrate

(NO3). Their combined measure is expressed as milligrams of nitrogen per liter (mg N/L) and levels exceeding 1 mg N/L suggest pollution from anthropogenic sources. Scientists suggest that winter data, when biological activity is low, may give the best estimate of a lake nutrient budget. Our sampling and monitoring program collects winter data about once every five years. 7. trophic status - a synthetic index that describes the lake health by examining water clarity, winter TP levels and summer chlorophyll a according to modeling equations. The equations derived years ago need refinement to take into account the significant clearing of the water column resulting from the filter feeding of the introduced zebra mussels. Trophic status is also related to lake morphometry, lake age and watershed activities. Large volume lakes dilute pollutants and tend to remain nutrient poor (oligotrophic). As lakes age, they usually gain sediment and nutrients from watershed activities. Then, lakes pass through the mesotrophic stage to the eutrophic condition (nutrient rich). When human activities in the watershed contribute sediment and nutrients, lakes are referred to as being culturally eutrophic. 8. chloride - a corrosive substance that may be found in water as a result of the application of de-icing agents to watershed highways, or from natural leaching of bedrock salts. Expressed in parts per million (ppm) or its equivalent, milligrams per liter (mg/L). A critical threshold of 250 mg/L is thought to be damaging to sensitive stream and lake organisms.

Methods: In 2003, lake studies began on April 30 and concluded on November 26. In 2004, lake studies began on April 30 and concluded on November 23. In 2005, poor weather slightly altered the schedule. Lake studies began on May 2 and concluded on December 3. The same methodology was used each year. Two mid-lake stations (Deep Run and Seneca Point) were visited monthly, April through November, by boat. At each mid-lake station, secchi disk depths were recorded, water samples were collected for chlorophyll a analyses and nutrient determinations, and a water quality profile was completed. Four additional stations were sampled in the lake: near-shore at Hope Point and Vine Valley, and at the mouths of Fallbrook Stream and the West River. Here samples were taken for chlorophyll a analyses and determination of surface nutrient levels. This

9 monthly experimental design is consistent with previous lake monitoring conducted by Finger Lakes Community College. Sampling protocols are described below:

Water clarity was measured through use of a secchi disk near noon (sun directly overhead), if possible, on a cloudless day. Readings were taken on the shady side of the boat to minimize glare from the water surface. Secchi disk depths were recorded as the average of when the disk disappeared from view while being lowered and when it reappeared while being retrieved. Readings were expressed to the nearest tenth of a meter.

For chlorophyll a analysis, integrated water column samples were collected with TYGON tubing extending through the epilimnion. Samples were stored on ice in 2 liter dark bottles to minimize changes in algal abundance. Samples were processed within 6 hours using the alkaline acetone procedure (Wetzel and Likens 1991).

A nonmetallic Van Dorn sampler was used to collect lake water at depths of 2, 25 and 50 meters. Each water sample was transferred to a bottle containing acid preservative, then stored on ice. All samples were tested for nutrient content following EPA analytical methods at the NYS certified (DOH ELAP # 10248) Life Science Laboratories, Inc.

Profile analyses of the water column were taken with a Yellow Springs Instrument 6920 water quality sonde and 650 data logger. Instrument calibration was checked prior to each sampling. Mid-lake sites on Canandaigua Lake were sampled at one meter intervals from the surface to a depth of fifteen meters (approximate summer depth of the epilimnion), then at five meter intervals to a maximum depth of 60 meters. Boat drift on the surface often prevented reaching maximum depths.

10 Results and Discussion: Background information on the limnology of Canandaigua Lake is found in Eaton and Kardos (1978), Sherwood (1993), Olvany (2000) and previous reports by the authors. It is a warm, monomictic lake that thermally stratifies during the summer and generally remains ice-free during the winter. Typically, open surface water allows wind to keep the lake well mixed during the winter months. The lake gradually gains heat at the surface during the spring and summer months. It is during this time period that wind works to displace some of the surface heat downward about 15 meters to establish a thermocline. As fall approaches, lake heat is slowly lost to a cooling atmosphere and lake turnover occurs in late November or early December. The development of thermal stratification in the lake is presented in the monthly temperature profiles (Figures 1.1, 1.2). These profiles are typical of all earlier work conducted in Canandaigua Lake, and resemble profiles for other deepwater lakes of the Finger Lakes region.

Dissolved oxygen (DO) increases with depth in the lake (Figures 1.3, 1.4). Limnologists refer to this pattern as an orthograde profile and it is typical of deep, clean water lakes. DO in the epilimnion was always close to 100% saturation. In the hypolimnion, the summer DO was maintained between 9 and 13 mg/L, indicating excellent conditions for survival of important game fish like trout. Slight decreases in DO were detected at the end of summer near the bottom of the lake. Increased oxygen demand, perhaps related to benthification by zebra mussels may be responsible. Fall turnover redistributes surface DO downward. High DO levels are presumed present throughout the water column during the winter. These seasonal DO patterns indicate that the lake remains a high quality habitat for many aquatic organisms.

11 Deep Run Profile

temperature (Co) 0 5 10 15 20 25 0

10 30-Apr-03 20 no May data 27-Jun-03 25-Jul-03 30 29-Aug-03 26-Sep-03

depth (meters) 40 31-Oct-03 26-Nov-03 50

Deep Run Profile

temperature (Co) 0 5 10 15 20 25 0

10 30-Apr-04 20 4-Jun-04 2-Jul-04 29-Jul-04 30 23-Aug-04 29-Sep-04

depth (meters) 40 28-Oct-04 23-Nov-04 50

12 Deep Run Profile

temperature (Co) 0 5 10 15 20 25 30 0

10 2-May-05 20 31-May-05 25-Jun-05 28-Jul-05 30 30-Aug-05 28-Sep-05

depth (meters) 40 28-Oct-05 3-Dec-05 50

FIGURE 1.1: Development of thermal stratification in Canandaigua Lake, Deep Run Station.

13 Seneca Point Profile

temperature (Co) 0 5 10 15 20 25 0

10 30-Apr-03 20 no May data 27-Jun-03 25-Jul-03 30 29-Aug-03 26-Sep-03

depth (meters) 40 31-Oct-03 26-Nov-03 50

Seneca Point Profile

temperature (Co) 0 5 10 15 20 25 0

10 30-Apr-04 20 4-Jun-04 2-Jul-04 29-Jul-04 30 23-Aug-04 29-Sep-04

depth (meters) 40 28-Oct-04 23-Nov-04 50

14 Seneca Point Profile

temperature (Co) 0 5 10 15 20 25 30 0

10 2-May-05 20 31-May-05 25-Jun-05 28-Jul-05 30 30-Aug-05 28-Sep-05

depth (meters) 40 28-Oct-05 3-Dec-05 50

FIGURE 1.2: Development of thermal stratification in Canandaigua Lake, Seneca Point Station.

15 Deep Run Profile

dissolved oxygen (mg/L) 0 5 10 15 0

10 30-Apr-03 20 no May data 27-Jun-03 25-Jul-03 30 29-Aug-03 26-Sep-03 depth (meters) 40 31-Oct-03 26-Nov-03 50

Deep Run Profile

dissolved oxygen (mg/L) 02468101214 0

10 30-Apr-04 20 4-Jun-04 2-Jul-04 29-Jul-04 30 23-Aug-04 29-Sep-04 depth (meters) 40 28-Oct-04 23-Nov-04 50

16 Deep Run Profile

dissolved oxygen (mg/L) 02468101214 0

10 2-May-05 20 31-May-05 25-Jun-05 28-Jul-05 30 30-Aug-05 28-Sep-05

depth (meters) 40 28-Oct-05 3-Dec-05 50

FIGURE 1.3: Dissolved oxygen profiles in Canandaigua Lake, Deep Run Station.

17 Seneca Point Profile

dissolved oxygen (mg/L) 02468101214 0

10 30-Apr-03 20 no May data 27-Jun-03 25-Jul-03 30 29-Aug-03 26-Sep-03 depth (meters) 40 31-Oct-03 26-Nov-03 50

Seneca Point Profile

dissolved oxygen (mg/L) 0 5 10 15 0

10 30-Apr-04 20 4-Jun-04 2-Jul-04 29-Jul-04 30 23-Aug-04 29-Sep-04 depth (meters) 40 28-Oct-04 23-Nov-04 50

18 Seneca Point Profile

dissolved oxygen (mg/L) 02468101214 0

10 2-May-05 20 31-May-05 25-Jun-05 28-Jul-05 30 30-Aug-05 28-Sep-05

depth (meters) 40 28-Oct-05 3-Dec-05 50

FIGURE 1.4: Dissolved oxygen profiles in Canandaigua Lake, Seneca Point Station.

19 Mean monthly specific conductance showed minor monthly fluctuation, and little change from top to bottom in the water column. Based on previous research since 1996, conductivity has been in the approximate range of 350 – 400 μS/cm. This does represent an increase from 271 μS/cm in 1955 (Berg 1963), 285 μS/cm in 1973 (Oglesby in: Eaton and Kardos 1978), but is similar to the 350 μS/cm in 1993 (Gilman 1993). It is unclear whether the historic values were obtained from multiple sites sampled monthly April through November like the more recent monitoring. However, the recent data show only minor monthly variation, suggesting a comparison of potentially different monitoring intensities may still be valid. The data sets suggest a long-term trend of increasing conductivity in the lake, perhaps associated with sediment delivered to the lake as a consequence of erosion associated with watershed activities.

Secchi disk readings for oligotrophic lakes often average greater than 8 meters but exhibit seasonal variability. Readings are lower when light is blocked by substances in the water, including eroded soil particles, re-suspended bottom sediment and planktonic organisms. Readings can also be affected by cloud cover and wave action at the time of sampling. Typically, winter lake clarity will be high because only a few planktonic organisms are in the water. As winter ends, longer days facilitate the growth of phytoplankton (algae). Small-bodied zooplankton (e.g., rotifers) feed on the algae. During this time, nutrients are moving from the water into the planktonic community. As slower growing but large-bodied zooplankton (e.g., copepods and water fleas) proliferate, feeding is intensified resulting in a clearing of the water column by late spring. Then, fish reproduce and their young begin feeding on the larger zooplankton. With warm summer conditions, the phytoplankton recover because young fish have consumed zooplankton, thereby reducing the feeding pressure on the algae. Algal population densities can increase but are limited primarily by the low concentration of available phosphorus. Nutrient additions from watershed activities can have significant impacts at any time but especially during the summer when many species of phytoplankton can be present. When phosphorus and nitrogen are depleted, a shift to dominance by nitrogen-fixing cyanobacteria usually occurs. The cyanobacteria (formerly called blue-green algae) are known for the taste and odor problems they may cause in lake water. Eventually, cooler autumn conditions coupled with a reduction in nutrients will initiate a clearing event and bring about

20 improvements in the secchi disk readings. By winter, most planktonic organisms have entered a resting stage on the lake bottom. Winter winds will mix nutrients throughout the water column.

From 2003 to 2005, clarity from April through November averaged 7.15 meters and reached a maximum of 10.00 meters. Lake clarity declined over the three year period, continuing a trend that began in 1999. Monthly data are presented in Table 1.1 and Figure 1.5. Additional historic data on lake clarity are discussed in Gilman (2000).

TABLE 1.1: Secchi disk readings (m) in Canandaigua Lake.

Date Deep Run Station Seneca Point Station Mid-Lake Average 30 April 2003 8.4 7.6 8.00 27 May 2003 8.3 8.3 8.30 27 June 2003 7.3 7.4 7.35 25 July 2003 6.5 8.0 7.25 29 August 2003 7.7 7.8 7.75 26 September 2003 7.4 6.6 7.00 31 October 2003 8.4 8.1 8.25 26 November 2003 6.5 7.3 6.90

30 April 2004 7.8 6.7 7.25 4 June 2004 6.5 5.0 5.75 2 July 2004 5.5 8.1 6.80 29 July 2004 7.0 6.1 6.55 23 August 2004 6.4 6.4 6.45 29 September 2004 6.6 7.2 6.90 28 October 2004 10.0 9.5 9.75 23 November 2004 7.9 7.7 7.80

2 May 2005 5.1 4.8 4.95 31 May 2005 9.1 7.3 8.20 25 June 2005 8.3 7.6 7.95 28 July 2005 8.1 8.6 8.35 30 August 2005 6.3 7.0 6.65 28 September 2005 5.4 5.0 5.20 28 October 2005 6.9 6.2 6.55 12 December 2005 4.9 6.7 5.80

21 Lake Clarity (2003)

month 4-30 5-27 6-27 7-25 8-29 9-26 10-31 11-26 0 1 2 3 4 5 6 7 secchi disk reading(meters) 8 9

Lake Clarity (2004)

month 4-30 6-04 7-02 7-29 8-23 9-29 10-28 11-23 0 1 2 3 4 5 6 7 8 secchi disk reading(meters) 9 10

22 Lake Clarity (2005)

month 5-2 5-31 6-25 7-28 8-30 9-28 10-28 12-3 0 1 2 3 4 5 6 7

secchi disk reading(meters) 8 9

FIGURE 1.5: Monthly mean secchi disk readings from mid-lake stations in Canandaigua Lake.

23 The levels of chlorophyll a during the monthly sampling season are presented in Table 1.2 and Figure 1.6. Algal populations developed quickly and phytoplankton species sequentially replaced one another as lake conditions changed during the growing seasons. During 2003 and 2004, a peak in chlorophyll a (algal abundance) occurred in late April to late May followed by lower amounts during the summer. These patterns may be caused by rapid species replacements but may also be related to the onset of zebra mussel filter feeding in the warming summer waters. The 2005 peak occurred in late August. A bloom in nitrogen-fixing cyanobacteria populations appears to be responsible. The dominant cyanobacteria species in the fall of 2005 was Microcystis aeruginosa and it is known to be unpalatable to zebra mussels and may produce taste and odor problems in the water. Another cyanobacteria bloom was detected in the late May 2006 and the responsible organism has been tentatively identified as Gloeocapsa sp. or Chroococcus sp.

Algal abundance estimated by the concentration of chlorophyll a averaged 2.53 μg/L in 2003, 2.63 μg/L in 2004 and 2.07 μg/L in 2005. The 2003 and 2004 data represent an increase from 2003 (2.45 μg/L) and these data approach the historic levels reported in 1973 (Oglesby in: Eaton and Kardos 1978) as well as the pre-zebra mussel levels from the early 1990’s. Algal abundance had declined following zebra mussel invasion but then it began increasing in 1999. This indirect evidence suggests that intraspecific competition among zebra mussels for food resources intensified in 1999, and by the summer of 2001 zebra mussel populations crashed lake-wide. The increasing chlorophyll a levels from 2002 to 2004 point to a recovery in algal populations as they experienced less filter feeding by zebra mussels, however, the decline in chlorophyll a in 2005 points to a resurgence in the numbers of zebra mussels. This may mark the beginning of a dynamic cycle between zebra mussels, algae and lake clarity.

24 TABLE 1.2: Chlorophyll a concentrations (μg/L) in Canandaigua Lake.

2003 Station 4-30 5-27 6-27 7-25 8-29 9-26 10-31 11-26 Fallbrook 0.93 10.68 1.25 1.58 1.88 0.81 1.02 7.53 Hope Point 1.16 2.71 1.57 2.60 2.05 1.27 1.53 1.59 Deep Run 1.24 3.37 1.71 3.65 1.66 2.51 2.88 2.05 Seneca 1.64 2.77 1.36 3.33 1.65 1.92 3.33 3.78 Point Vine Valley 1.36 9.48 1.44 2.41 1.95 1.24 1.24 2.95 West River 1.58 7.91 2.60 3.63 1.35 1.30 2.41 3.36

Mean 1.32 6.15 1.66 2.87 1.76 1.51 2.07 3.54 Adjusted 1.27 5.80 1.47 2.71 1.84 1.55 2.00 3.58 Mean * 2004 4-30 6-04 7-02 7-29 8-23 9-29 10-28 11-23 Fallbrook 0.97 2.85 1.58 1.83 4.01 1.43 0.62 1.46 Hope Point 2.26 1.70 8.26 2.83 2.16 1.64 1.60 1.19 Deep Run 6.40 2.36 3.36 3.63 3.42 2.72 2.37 1.48 Seneca 7.16 2.13 2.37 4.46 3.59 2.76 2.26 1.70 Point Vine Valley 5.19 2.42 1.33 2.77 2.37 0.79 0.68 1.13 West River 8.51 8.86 1.79 3.62 1.61 4.41 3.82 1.01

Mean 5.08 3.38 3.12 3.19 2.86 2.29 1.89 1.33 Adjusted 4.40 2.29 3.38 3.10 3.11 1.87 1.51 1.31 Mean * 2005 5-02 5-31 6-25 7.28 8-30 9-28 10-28 12-03 Fallbrook 1.06 1.02 2.25 1.78 1.41 3.06 1.81 1.21 Hope Point 1.58 1.17 1.52 2.09 2.75 2.27 2.51 1.16 Deep Run 1.36 1.46 1.92 2.88 3.66 2.82 3.28 2.14 Seneca 1.30 1.33 1.75 2.00 2.77 2.79 2.77 1.43 Point Vine Valley 1.05 6.72 1.24 1.10 1.82 1.70 1.81 3.16 West River 1.51 1.36 2.19 3.28 3.69 3.63 3.23 7.16

Mean 1.31 2.18 1.81 2.19 2.69 2.71 2.57 2.71 Adjusted 1.27 2.34 1.74 1.97 2.48 2.53 2.43 1.82 Mean *

* adjusted mean = without West River values, this station is excluded because it more often reflects river conditions rather than lake quality. 25 Mean Algal Abundance (2003)

(micrograms/liter) 3 a

1 chlorophyll 0 4-30 5-27 6-27 7-25 8-29 9-26 10-31 11-26 sampling date

Mean Algal Abundance (2004)

(micrograms/liter) 3 a

1 chlorophyll 0 4-30 6-04 7-02 7-29 8-23 9-29 10-28 11-23 sampling date

26 Mean Algal Abundance (2005)

(micrograms/liter) 3 a

1 chlorophyll 0 5-2 5-31 6-25 7-28 8-30 9-28 10-28 12-3 sampling date

FIGURE 1.6: Mean chlorophyll a concentrations among sample stations in Canandaigua Lake.

There has also been a change in the seasonal pattern of chlorophyll a concentrations between shoreline and mid-lake stations (Table 1.3). Again, data from the West River station is excluded in the analyses. Ratios above 1.00 document more algal productivity along the shoreline. Conversely, when the ratio falls below 1.00, more algal productivity has been detected in the open water of the mid-lake stations. For a number of years, the ratio has favored less algal productivity along the shoreline and this effect had been attributed to efficient filter feeding by zebra mussels in the shallow near-shore environment (Gilman 2000). Now another change may be complicating the explanation. With improving water clarity along the shoreline, aquatic macrophyte communities have expanded into deeper waters. As this occurred, the number of macrophyte stems in the weed-bed community increased. These stems are a substrate where zebra mussels can attach and begin filter feeding. The mussels regurgitate “pseudo-fecal pellets”, nutrient rich masses that accumulate on the bottom, decay and eventually release nitrogen and phosphorus to the near-shore waters. Some mussels die during the growing season, 27 presumably due to increased competition (i.e., there are more mussels because the weeds offer more points for attachment). They decay and release more nutrients. When the macrophytes die at the end of their growing season, the attached zebra mussels collect along the bottom and a significant proportion of them die, decompose and release even more nutrients back to the water. Planktonic algae increase whenever more nutrients are available, and the ratio could return to or even exceed 1.00. The recent trends have begun to show increased algal productivity along the shoreline of the lake. It is possible that some of the planktonic chlorophyll a originated from the breakup of bottom dwelling algal mats. Wave energy can be a powerful force near the shoreline. It is also possible that selective filter feeding by zebra mussels has shifted the dominance of the algal community to unpalatable species that now can proliferate. However, the increase in the standard deviation suggests that single events (months or sites with extremely high chlorophyll a levels) may also play an important role. These single events may be triggered by human activities in the watershed and they can produce lingering effects that upset lake ecology for many months.

TABLE 1.3: Ratio between shoreline (n = 3) and mid-lake (n = 2) chlorophyll a concentrations. 1996-2000 samples were collected at a depth of 2 meters, 2001-2005 samples collected by integrated column method.

Year Apr May Jun Jul Aug Sep Oct Nov Mean ± 1 standard deviation 1996 1.05 1.13 0.84 0.75 0.87 0.79 0.77 0.94 0.89±0.14 1997 1.55 1.05 0.78 0.82 0.74 0.75 0.72 0.68 0.89±0.29 1998 0.90 0.54 0.57 0.50 0.86 0.77 0.83 0.77 0.72±0.16 1999 0.91 0.83 0.71 0.60 0.59 0.50 0.71 0.86 0.71±0.15 2000 0.94 0.66 0.80 0.59 0.72 0.57 0.47 0.67 0.68±0.15 2001 1.06 0.98 1.03 0.69 0.90 0.83 0.75 0.48 0.84±0.20 2002 1.06 0.46 1.05 0.84 1.11 1.63 0.56 0.69 0.93±0.37 2003 0.80 2.48 0.93 0.63 1.18 0.50 0.41 1.38 1.04±0.67 2004 0.41 1.03 1.30 0.61 0.81 0.47 0.42 0.79 0.73±0.32 2005 0.92 2.13 0.91 0.68 0.62 0.84 0.67 1.04 0.98±0.49

28 An inverse relationship exists between chlorophyll a concentrations and secchi disk readings over the last ten years (Figure 1.7). Algal abundance strongly influences lake clarity, moderated to some degree by zebra mussel populations and human activities in the watershed. In 2005, however, lake clarity and chlorophyll a both declined, suggesting an ever growing role of importance for suspended sediment rather then algae in reducing the secchi disk reading. The figure provides further support for the need to regulate human activities that can have negative consequences on lake processes.

Canandaigua Lake recent water quality trends

10 9 8 7 6 secchi disk 5 chlorophyll a 4 3 ug/L...... meters 2 1 0 1996 1997 1998 1999 2000 2001 2002 2003 2004 2005 April - November mean

FIGURE 1.7: Recent water quality trends in lake clarity and algal abundance.

29 Phosphorus is the limiting nutrient for plant productivity and TP has been measured since 1996. Its concentration varies by site (Figure 1.8), by sampling month, and with depth below the lake surface. Based on 243 samples collected from multiple sites and depths over the last three years, the TP average was 6.14 μg/L with the range running from undetectable to 43.0 μg/L. For the 83 samples collected in 2003, total phosphorus averaged 5.28 μg/L. For the 80 samples collected in 2004, total phosphorus averaged 6.16 μg/L. For the 80 samples collected in 2005, total phosphorus averaged 7.00 μg/L. In all three study years, the highest site average was for the station at the mouth of the West River. The mean annual concentration there has increased by 60% during the last two years, perhaps related to severe storm events that produced many “gully washers” that drained to the West River.

Mean Total Phosphorus (2003)

18 16 14 12 10 8 6 micrograms/liter 4 2 0 SP-2 SP-25 SP-50 DR-2 DR-25 DR-50 WR-2 VV-2 HP-2 FB-2 sampling location

30 Mean Total Phosphorus (2004)

18 16 14 12 10 8 6 micrograms/liter 4 2 0 SP-2 SP-25 SP-50 DR-2 DR-25 DR-50 WR-2 VV-2 HP-2 FB-2 sampling location

Mean Total Phosphorus (2005)

18 16 14 12 10 8 6 micrograms/liter 4 2 0 SP-2 SP-25 SP-50 DR-2 DR-25 DR-50 WR-2 VV-2 HP-2 FB-2 sampling location

FIGURE 1.7: Mean total phosphorus in Canandaigua Lake by sampling station.

31 Between 2003 and 2005, there have been 26 instances (10.7%) when TP levels exceeded the desirable ecological threshold of 10 μg/L. Most of the high results were for samples collected at the mouth of the West River during the early spring when wetland vegetation is dormant or during late fall when wetland vegetation is going senescent (Table 1.4), substantiating the changing role of the High Tor wetlands. During the growing season they usually act as a nutrient sink; in the dormant season they may act as a nutrient source to the lake.

TABLE 1.4: Total phosphorus data exceeding 10 μg/L, April 2003 through November 2005. Samples from the West River account for 13 (50.0%) of the instances.

Total Phosphorus (μg/L) Sampling Site Depth (m) Date 43.0 West River 2 6-4-2004 30.0 Deep Run 2 4-30-2003 27.0 West River 2 9-29-2004 26.0 Hope Point 2 6-27-2003 26.0 West River 2 8-30-2005 25.0 West River 2 9-28-2005 23.0 West River 2 10-28-2005 22.0 Hope Point 2 8-30-2005 22.0 West River 2 12-3-2005 21.0 West River 2 10-31-2003 20.0 West River 2 8-29-2003 18.0 West River 2 7-28-2005 16.0 West River 2 7-29-2004 15.0 Deep Run 2 8-30-2005 15.0 Fallbrook 2 4-30-2003 14.0 Vine Valley 2 11-26-2003 13.0 Deep Run 2 9-28-2005 12.0 Deep Run 2 9-26-2003 12.0 Fallbrook 2 9-26-2003 12.0 Fallbrook 2 8-30-2005 12.0 West River 2 7-25-2003 12.0 West River 2 8-23-2004 11.0 Deep Run 25 9-28-2005 11.0 Fallbrook 2 8-23-2004 10.0 Deep Run 25 4-30-2003 10.0 West River 2 7-2-2004

The station at the mouth of the West River had the highest total phosphorus levels in 50 of the 76 months of sampling (65.8%) conducted since August 1996!

32 During the summer of 1973, total phosphorus in the surface waters (probably mid-lake at Black Point) of Canandaigua ranged from 8 to 10 μg/L (Eaton and Kardos 1978). This was one year after Hurricane Agnes had brought tremendous rainfall that produced flooding throughout the watershed. Tributary streams contributed eroded sediment and nutrients to the lake, and the highest lake levels on record were noted. The mean annual TP results collected since 1996 are displayed in Figure 1.8. A trend line has been added to emphasize the subtle increases over this ten year period. The large increase beginning in 1999 corresponds with the decline and subsequent 2001 die-off of zebra mussels in the lake. While the mean annual TP levels have fluctuated between 5 and 10 μg/L, other data tells us that more enters the lake then leaves through the Outlet. The absence of drastic increases in TP over time is the result of sound watershed practices (e.g., the restriction of phosphate builders in detergents, the vigilance of the watershed inspection program, the expansion of municipal sewer lines and the broader use of

Mean Total Phosphorus

10 9 8 7 6 5 4 3 micrograms/liter 2 1 0 1996 1997 1998 1999 2000 2001 2002 2003 2004 2005 year

FIGURE 1.8: Long-term trends in mean annual total phosphorus in Canandaigua Lake.

33 best management practices in agriculture). Phosphorus is also known to mineralize with iron in lake bottom sediments. A growing watershed population coupled with an increase in impervious surfaces, however, represent threats to lake health that could significantly increase phosphorus loading to the lake unless proper land use controls are in place regulating future development.

Table 1.5 presents mean monthly depth profiles of TP for the two mid-lake stations from 2003 to 2005. Higher values are associated with the near surface depth of two meters. It is this upper region that receives sediment and nutrients from erosive watershed activities. Deep Run data are more variable but most often higher than Seneca Point data for the same reason.

TABLE 1.5: Seasonal profiles for total phosphorus (μg/L) at the two mid-lake sampling stations.

Deep Run Station

Apr-Nov Depth (m) Apr May Jun Jul Aug Sep Oct Nov mean 2 12.33 4.50 4.03 4.07 7.13 10.80 5.20 3.17 6.40 25 5.03 4.07 4.07 4.13 4.40 5.87 3.47 4.47 4.44 50 4.67 3.67 3.40 5.53 5.17 4.60 5.10 3.63 4.47 Monthly mean 7.34 4.08 3.83 4.58 5.57 7.09 4.59 3.76

overall mean = 5.10 μg/L Seneca Point Station

Apr-Nov Depth (m) Apr May Jun Jul Aug Sep Oct Nov mean 2 3.57 4.20 4.53 4.97 5.97 6.90 4.43 3.50 4.76 25 3.83 3.73 5.03 3.50 4.00 5.47 2.17 6.50 4.28 50 5.23 4.23 4.43 3.30 3.97 5.03 3.73 3.53 4.18 Monthly mean 4.21 4.06 4.67 3.92 4.64 5.80 3.44 4.51

overall mean = 4.41μg/L

34 The ecological threshold for inorganic nitrogen (NO3 and NO2) is 1.00 mg N/L. Inorganic nitrogen had a mean of 0.28 mg N/L based on 580 samples collected from April 1996 through November 2002. In 2003, inorganic nitrogen averaged 0.30 mg N/L based on 83 samples while in 2004 inorganic nitrogen averaged 0.29 mg N/L based on 80 samples. Eaton and Kardos

(1978) report a mean of 0.31 mg/L NO3-N for July 1972 based on 52 samples, and a mean of

0.32 mg/L NO3-N for July 1973 based on 28 samples. These results suggest little change in the nitrogen compounds available for the support of lake productivity during the last three decades. Inorganic nitrogen testing was discontinued in 2005. Over the years, our long-term results showed a seasonal pattern of nitrogen depletion along the shoreline during the height of the growing season. At the mid-lake station, depth profile data indicated nitrogen depletion near the surface.

Lake eutrophication is a natural process resulting from the gradual accumulation of sediments and organic matter. As a lake basin slowly fills, nutrients accumulate and biological productivity is enhanced. The rate of eutrophication and, hence, the life span of the lake, will depend on the morphometry of the basin and the stability of watershed soils. Human activities (e.g., land development, agriculture, waste water discharges) accelerate the process bringing about cultural eutrophication. When this occurs, changes in trophic condition happen so fast that aquatic organisms cannot adapt and so they are lost from the natural lake communities. Tolerant, invasive species often take their place, much to the detriment of watershed residents.

Typical lake succession passes through this series of trophic states: Oligotrophy: nutrient-poor, biologically unproductive Mesotrophy: intermediate nutrient availability and biological productivity Eutrophy: nutrient-rich, highly productive Hypereutrophy: extremely productive, "pea soup" conditions

Oligotrophic lakes have low productivity due to low nutrient supplies. Water is exceptionally clear. These lakes are often deep and have steep basin walls. Water in mesotrophic lakes receives a moderate supply of nutrients from the watershed. Primary productivity is enhanced despite water clarity being somewhat reduced by suspended sediment and plankton. Eutrophic

35 lakes have a high nutrient supply and experience pulses of extremely rapid plant growth. Water clarity can be greatly reduced at times. Dissolved oxygen along the lake bottom may be depleted by decomposers as they break down organic materials.

Identification of a lake's trophic status is a useful way to determine overall lake "health". Comparisons can be made to other lakes, or from year to year in the same lake, to evaluate the effectiveness of lake restoration techniques and watershed BMPs. Early studies of Canandaigua Lake (Gilman and Rossi 1983, Gilman 1994) suggested that it was oligotrophic but nearing the mesotrophic state. To update the trophic status of Canandaigua Lake, the Carlson Trophic State Index (TSI) is used. This index is based on values for chlorophyll a concentration, winter total phosphorus and summer water clarity. The variables are interrelated in complex ways. Equations have been developed for each variable used to estimate trophic state (Table 1.6).

TABLE 1.6: Information pertaining to the Carlson Trophic State Index (TSI).

Variable Oligotrophic State Mesotrophic State Eutrophic State total phosphorus < 10 μg/L 10 - 26 μg/L > 26 μg/L chlorophyll a < 2 μg/L 2 - 8 μg/L > 8 μg/L secchi disk depth > 4.6 m 1.9 - 4.6 m < 1.9 m

Carlson TSI < 37 37 - 51 > 51

The TSI formulas are: TSISD = 60 - 14.41(ln secchi disk reading) TSIChl = 30.6 + 9.8(ln chlorophyll a concentration) TSITP = 4.15 + 14.42(ln total phosphorus level) where ln = natural logarithm = log10 x 2.30

The TSI can be useful in determining the extent of eutrophication in any given lake but other factors should also be considered. Carlson's equations were based on data from lakes throughout the United States, and may not necessarily apply to the Finger Lakes. In fact, since the equations represent averages for many lakes, any one specific lake may not exactly follow the relationships described by the equations. In addition, each of these lake variables can be affected by other factors. For example, lake clarity can be influenced by highly colored water, suspended 36 sediment and the presence of zebra mussels which filter feed on plankton community. Every trophic state can support a variety of human uses. Eutrophic lakes can have excellent warmwater fisheries while oligotrophic lakes can provide an excellent source of public drinking water. Summer (June, July, August) monthly mean secchi disk readings, chlorophyll a concentrations and winter TP, when available, were used to calculate the TSI values in Table 1.7.

TABLE 1.7: Carlson TSI values for Canandaigua Lake.

Based on: Secchi disk Chlorophyll a Total phosphorus Average 1995 data 36.9 46.3 36.0 39.7 1996 data 33.0 39.1 46.5 39.5 1997 data 30.2 40.6 27.4 32.7 1998 data 29.1 36.8 - 33.0 1999 data 28.6 35.6 - 32.1 2000 data 28.6 35.5 - 32.0 2001 data 33.3 37.9 22.7 31.3 2002 data 29.6 38.9 22.8 30.4 2003 data 31.1 37.4 - 34.3 2004 data 32.8 42.0 - 37.4 2005 data 30.7 37.7 - 34.2

During the last three years, average TSI values for Canandaigua Lake fall closest to the oligotrophic (<37) condition. TSI based on chlorophyll a concentrations had declined steadily from 1995 to 2001 as a result of filter feeding on algae by zebra mussels. Since the 2001 zebra mussel die-off, the TSI based on chlorophyll a concentrations has rebounded. The winter TP analysis produces a TSI that is relatively independent of zebra mussel effects and may provide a more realistic trophic status rating for Canandaigua Lake. It shows a downward TSI trend since 1996 suggesting that the watershed sources of phosphorus are being managed effectively. However, winter TP has not been measured since 2002 and with increasing watershed development, it would be timely and appropriate to schedule an update.

37 CHAPTER 2 – TRIBUTARY RESEARCH Methods: Seventeen tributary streams were monitored during 40 storm/melt events between 1997 and 2005 (Figure 2.1). Dr. Makarewicz’s reports from 1997-2000 document the sampling methodologies used during those years. Dr. Gilman’s 2001/2002 report provides the methodology for 2001 and 2002. Years 2003-2005 followed very similar sampling methodologies to the previous work in order to maintain overall consistency.

Grab samples were collected by the Watershed Manager once during the events listed in Table 2.1 and tested for phosphorus, nitrate/nitrite, and total suspended solids at Life Science Laboratories (NELAP certified with multiple labs in upstate NY). These dates corresponded to storm events and/or significant snow melt events. Precipitation readings are done on a daily basis at the Canandaigua Water Treatment Plant approximately 3 miles south on West Lake Rd. Readings are recorded at 8am each day and count for that day. Example: 3/13/2001 precipitation measurement would be from 8am on the 12th until 8am on the 13th. Table 2.1 shows the precipitation levels the day after due to the fact that precipitation occurring after 8am will be counted in the next day’s precipitation total. Precipitation occurring two days previous to the event is shown to better understand possible antecedent wetness conditions.

Grab samples were collected in sections of typical flow. Two pre-coded bottles were used for each sample; one had acid preservative that was used to preserve the sample for nutrient analysis and the second unpreserved bottle was for Total Suspended Solids (TSS). The unpreserved bottle (TSS) was used to collect stream water for the bottle with preservative, and was emptied into that bottle making sure that the acid preservative was kept in the bottle. The two bottles were pre-coded to ensure accuracy. Samples were stored in ice-filled coolers until transport to Life Science Laboratories (LSL), a certified lab out of Syracuse and Canandaigua, New York (NYS DOH ELAP #10248).

Subwatersheds 1 Sucker Brook 2 Tichenor Gully 3 Menteth Gully 4 Barnes Gully 5 Seneca Pt. Gully 6 Hicks Pt. 7 Grimes Creek 8 Eelpot Creek 9 Reservoir Creek 10 Tannery Creek 11 Parrish Gully 12 North Naples 13 Lower W. Rr 14 Middle W. Rr 15 Upper W. Rr 16 Clark Gully 17 Vine Valley 18 Fisher Gully 19 Gage Gully 20 Deep Run 21 Fall Brook

Direct Drainage 22 Butler Road 23 Foster Road 24 Deuel Road 25 Coy Road 26 Stid Hill 27 South Bristol 28 W Rr Naples Cr Jc 29 Hi-Tor 30 South Hill 31 Bare Hill 32 Jones Road 33 Cottage City 34 Lincoln Hill

FIGURE 2.1: Canandaigua Lake sub-watersheds and direct drainage basins.

39 TABLE 2.1: Precipitation measurements and runoff totals during each storm event, 2001-2005.

Precipitation Precipitation Precipitation Precipitation Estimated Date (in) 2 Days (in) 1 Day (in) Day Of (in) Day After Percentage of Before Before (after 8am on Rain ending up sampling date) as streamflow 3/13/2001 0.00 0.00 0.44 0.07 134% 9/25/2001 0.00 0.00 2.52 0.21 1% 12/17/2001 1.04 0.00 0.04 1.11 6% 2/1/2002 0.37 0.40 1.15 0.01 58% 3/26/2002 0.01 0.05 0.03 0.82 59% 3/26/2003 trace 0.00 0.50 trace 123% 6/1/2003 0.00 0.00 1.63 0.00 49% 7/23/2003 0.02 0.95 0.98 0.45 11% 10/27/2003 0.00 0.00 0.66 0.22 6% 11/19/2003 0.19 0.01 0.03 1.09 47% (sampled early in event) 3/27/2004 0.04 0.00 0.42 0.03 220% 4/1/2004 0.00 0.11 0.03 0.87 35% 4/13/2004 0.00 0.00 0.33 1.10 87% 7/14/2004 0.52 0.45 0.66 0.21 10% 9/9/2004 0.00 0.22 2.31 0.58 33% 4/2/2005 0.00 0.00 0.42 1.73 92% - no snow- 2 foot rise in lake 8/31/2005 0.00 0.23 2.44 0.51 2%-Katrina-dry low antecedent 10/25/2005 0.93 0.07 0.50 1.26 29%

The last column in Table 2.1 documents the percentage of precipitation ending up as runoff to the lake and the potential loading occurring for each of the storm events sampled. This percentage is calculated by determining the net inflow (which is based on lake level change, outflows, precipitation on the lake, and withdrawals) into the lake and dividing it by the amount of precipitation landing on the entire watershed. The percentage ending up as streamflow is based on four days of net inflows and precipitation in order to capture the entire hydrograph or runoff event. Some storm events show greater than 100% of the precipitation that landed during those four days ending up as streamflow. This occurs during the spring snowmelt events where the existing snow pack melts and adds to the runoff estimate.

There are limitations to using this approach to determine individual stream discharge. The first limitation is assuming that the percentage of precipitation ending up as streamflow is uniform throughout the subwatersheds sampled. Differences in landcover, impervious cover, slope, soils,

40 precipitation, and other variables bring some inaccuracy into this uniform approach. However, due to the inaccuracy of discharge measurements in previous studies (where total annual discharge in many of the streams was measured to be greater than the total precipitation in the drainage area), the authors believe this approach to be a substantially more accurate estimate of storm event streamflow. It also gives us an approach to compare runoff amounts between storms. The higher the percentage the more overland flow occurred.

The monitoring program is not capable of detecting subtle changes or trends in streams. As described in Dr. Makarweicz’s 1997-2000 report the sampling design started nine years ago does not allow us to scientifically document annual trends in the data. “Trend analyses would require sampling the discharge of streams continuously with appropriate nutrient sampling during events and baseline conditions.” To document year to year trends on 17 streams would require automated sampling and flow equipment at each site and a much higher frequency of sample analysis. The costs to do this on a yearly basis would easily exceed $100,000 in cash and labor. All variables would still not be accounted for, thus still requiring some estimation and assumption in the interpretation of the data that is collected.

Although the current sampling program does not provide reliable year to year trends, it does allow us to observe trends that are maintained over multiple years. The sampling program also allows us to prioritize streams based on multiple events and years of sampling. Finally, it allows us to make rough comparisons between the results from our streams to national standards and research.

41 Results and Discussion: From 1997 to 2005 the monitoring team collected 40 storm/melt event samples across seventeen tributaries to Canandaigua Lake. Events sampled span a broad cross section of precipitation/melt events that can substantially impact the spectrum of results including: time of year, time sampled within a storm event, antecedent moisture conditions, storm intensity, duration, and amount, along with land use changes between storm events. However, because of the growing number of results we feel fairly confident that the long term average concentrations and rankings provided in this report reflect an accurate estimate of what is going on in these subwatersheds.

Table 2.1 in the NYS Stormwater manual lists the National Median Concentrations for Chemical Constituents in Stormwater. This data came from the comprehensive National Urban Runoff Program (NURP) that sampled urban type streams across the United States during storm events. The results from the NURP study document that median concentration of total phosphorus (TP) was 0.26 mg/L, total suspended solids (TSS) was 54.5 mg/L, and nitrate/nitrite concentrations was 0.53 mg/L. Although there are multiple variables involved with comparing these concentrations to our sampling effort, the NURP study provides a decent benchmark to use as a guide when comparing our streams to national level research. National research has documented that urban type streams usually have elevated levels of phosphorus, sediment, nitrates, and bacteria when compared to streams with rural land cover, so if we come close to these levels there is cause for concern. Also, the NURP study was completed back in the 1970s and early 1980s when many of the treatment technologies for point sources of pollution were being upgraded and most of the non-point source pollution control techniques were not in place. Therefore, the levels reported in the NURP study should be even more elevated than the samples collected within the Canandaigua Lake Watershed during the 1997-2005 timeframe.

Rankings vs. Raw Averages: Grab samples are snapshots in time and a couple of samples that are either substantially higher or lower can impact averages (even with 40 samples). The annual ranking approach shown in Table 2.2 was used in order to try to reduce the impact of extremely high or low individual storm event results that are atypical and may be skewing the raw average data. The table is broken

42 down into three categories of pollution with green being the lowest concentration ranking, yellow being the middle and red having the highest concentration ranking. The streams with the higher rankings are the ones with higher average concentration for that year.

The annual rankings document that there is substantial year to year variability in the data. It also demonstrates that in some cases multiple year trends begin to stand out. The variability and trends will be discussed for each parameter sampled.

Following page: TABLE 2.2: Stream rankings, 1997-2005.

43 Phosphorus (mg/L) 1997-8 1998-9 2000 2001-2 2003 2004 2005 Average of Color Legend Subwatershed Location Rankings Worst 33% T-1 Sucker Brook-Clark St. 11 16 11 17 16 13 5 12.7 Middle 33% T-2 Tichner Gully 5106 917147 9.7 Best 33% T-3 Menteth 2 5 15 8 12 5 4 7.3 T-4 Barnes Gully 1 1 12 3 11 4 3 5.0 T-5 Seneca Pt. 6 8 14 12 13 2 9 9.1 T-27A Cook's Pt- Mouth 3 4 16 6 2 16 10 8.1 T-7 Grimes Ck. 6 3 2 3 1 11 4.3 T-8 Eelpot Ck. 11 9 14 5 17 17 12.2 T-9 Reservoir Ck. 7 17 7 1 3 16 8.5 T-10 Tannery Ck.- East Hill Rd. 2 8 5 4 6 15 6.7 T-12 Naples Ck- 245 12 12 5 15 15 15 12 12.3 T-13 L. West R.- Sunnyside 7 3 2 1 7 9 1 4.3 T-17 Vine Valley 13 14 4 16 14 12 14 12.4 T-18 Fisher Gully 4 9 10 13 6 8 8 8.3 T-19 Gage Gully 10 17 13 11 10 10 12 11.9 T-20 Deep Run 9 15 7 4 9 11 6 8.7 T-21 Fall Brook 8 13 1 10 8 7 2 7.0

Total Suspended Solids (mg/L) 1997-8 1998-9 2000 2001-2 2003 2004 2005 Average of Color Legend Subwatershed Location Rankings Worst 33% T-1 Sucker Brook-Clark St. 6 9 6 10 10 2 2 6.4 Middle 33% T-2 Tichner Gully 4 5 5 5 14 5 5 6.1 Best 33% T-3 Menteth 3 3 15 13 17 8 6 9.3 T-4 Barnes Gully 1 4 13 9 13 11 4 7.9 T-5 Seneca Pt. 7 7 11 11 15 10 7 9.7 T-27A Cook's Pt- Mouth 9 6 17 6 2 16 3 8.4 T-7Grimes Ck. 1682519 6.8 T-8 Eelpot Ck. 1716148 1713 14.2 T-9 Reservoir Ck. 10148 3 1314 10.3 T-10 Tannery Ck.- East Hill Rd. 2 2 7 4 9 10 5.7 T-12 Naples Ck- 245 13141016161511 13.6 T-13 L. West R.- Sunnyside 2 1 1 1 1 6 1 1.9 T-17 Vine Valley 10 11 3 12 12 12 15 10.7 T-18 Fisher Gully 8 8 12 17 9 14 17 12.1 T-19Gage Gully 51591511316 10.6 T-20Deep Run 121274 6 412 8.1 T-21 Fall Brook 11 13 4 3 7 7 8 7.6

Nitrate/Nitrite (mg/L) 1997-8 1998-9 2000 2001-2 2003 2004 2005 Average of Color Legend Subwatershed Location Rankings Worst 33% T-1 Sucker Brook-Clark St. 11 13 13 14 15 14 13 13.3 Middle 33% T-2 Tichner Gully 8 121113139 15 11.6 Best 33% T-3 Menteth 7 7 5 4 7 8 8 6.6 T-4Barnes Gully 4415212 2.7 T-5 Seneca Pt. 2 3 4 8 8 5 9 5.6 T-27A Cook's Pt- Mouth 3 2 3 3 4 3 4 3.1 T-7 Grimes Ck. 5 8 6 6 6 3 5.7 T-8 Eelpot Ck. 111211111211 11.3 T-9 Reservoir Ck. 7 10 9 10 10 10 9.3 T-10 Tannery Ck.- East Hill Rd. 1 2 2 1 2 1 1.5 T-12Naples Ck- 245 6667577 6.3 T-13 L. West R.- Sunnyside 1 9 9 1 9 11 6 6.6 T-17 Vine Valley 9 14 14 12 12 13 12 12.3 T-18 Fisher Gully 5 10 7 10 3 4 4 6.1 T-19 Gage Gully 13 17 17 17 16 17 17 16.3 T-20 Deep Run 10151616171516 15.0 T-21 Fall Brook 12 16 15 15 14 16 14 14.6 44 TABLE 2.3: Combined average concentrations for each of the streams from 1997-2005. (fecal coliform measurements are from 1989-2005).

Stream TP Nitrate/Nitrite TSS Fecal Coliform (mg/L) (mg/L) (mg/L) (Colonies per 100ml) T-1 Sucker Brook 0.218 1.55 116.5 725 T-2 Tichenor Gully 0.154 1.05 138.7 89 T-3 Menteth Gully 0.126 0.57 208.8 140 T-4 Barnes Gully 0.101 0.36 161.7 122 T-5 Seneca Pt. Gully 0.154 0.51 186.2 260 T-27A Cook’s Pt 0.153 0.41 208.0 385 T-7 Grimes Creek 0.083 0.55 111.2 - T-8 Eelpot Creek 0.269 0.95 335.5 - T-9 Reservoir Creek 0.201 0.83 260.5 - T-10 Tannery Creek 0.119 0.27 133.8 - T-12 Naples Creek 0.196 0.55 313.9 259 T-13 L. West River 0.081 0.62 54.6 33 T-17 Vine Valley 0.206 1.21 274.6 625 T-18 Fisher Gully 0.125 0.69 398.8 161 T-19 Gage Gully 0.182 4.11 275.0 259 T-20 Deep Run 0.142 2.95 178.9 230 T-21 Fall Brook 0.118 2.37 147.0 369

Total Phosphorus (Figure 2.2): Eelpot Creek had the highest average concentration of phosphorus over the last nine years with 0.269 mg/L (Table 2.3). Sucker Brook was second with 0.218 mg/L. Vine Valley was third with 0.206 mg/L and Reservoir Creek was fourth with 0.201 mg/L. Naples Creek was fifth with 0.196 mg/L, but it is important to point out that both Eelpot and Reservoir Creek feed into Naples Creek, thus potentially causing the increased levels in Naples Creek.

The long-term average for Eelpot Creek slightly exceeds the median concentration levels for total phosphorus in the NURP study. We could not look at median concentration levels for our sampling program because individual event data from 1997-2000 was not available from SUNY Brockport. The averages in the other four subwatersheds are slightly below the median levels for phosphorus.

45 Further investigation needs to take place as to why Eelpot Creek is showing the highest long- term concentrations of phosphorus. Eelpot Creek is a high gradient stream that originates in the southwest portion of Naples with small portions that extend into Steuben and Livingston Counties. There may be significant stream bank erosion occurring because the stream gradient is steep. However, Grimes Creek also is a high gradient stream with only slightly higher forest cover and has the second lowest long-term phosphorus concentrations. A substantial portion of the watershed of Eelpot Creek (along with Reservoir Creek) does drain across the recessional Valley Heads moraine, with soils that could have higher potential for erosion.

Table 2.2 shows the average rankings for the three parameters sampled. Sucker Brook has a slightly higher ranking than Eelpot using this approach. Vine Valley and Naples Creek also show up on the higher third of the overall rankings. Gage Gully moves from 6th to 4th and Reservoir Creek moves from 4th to 9th. Average concentrations and average rankings both have their advantages and disadvantages. Used in combination they can help us better understand which streams have the highest long-term concentration of phosphorus.

ll Broo ll

Run

Deep

Weighted Average

y Ga

er Gull er

Fis

Valley

t R.- Sunnyside R.- t

L. We L.

y C y

Naples Ck- 245 Ck- Naples r

nne

a k.

voir

t Ck t

p l

Ck.

es es

m i

Gr th

ok's Pt ok's

Seneca Pt Seneca ly

es es

Bar

Menteth

Figure 2.2: Concentrations Total Phosphorus 1997-2005 Weighted Average l Sample Site Sample

or Gul or

n Tiche

0.300 0.250 0.200 0.150 0.100 0.050 0.000

Brook-Clark St. Brook-Clark r

mg/L Sucke 47 Total Suspended Solids (TSS) (Figure 2.3): Fisher Gully had the highest average TSS concentration over the last nine years at 398.8 mg/L. Eelpot Creek was second with 335.5 mg/L. Naples Creek was third with 313.9 mg/L. Gage Gully and Vine Valley were tied for fifth with 275.0 mg/L. All streams except Lower West River significantly exceed the TSS levels reported in the NURP study of 54.6 mg/L. The annual ranking shows the same five streams as the highest five with some minor differences in order, with the largest being that Fisher Gully drops to third.

Fisher Gully is a high gradient (steep) gully, located along the southern portion of the Town of Gorham and at the beginning of the Appalachian Plateau. Fisher Gully is an important tributary because it outlets approximately 100 feet from the Village of Rushville’s intake pipe. In the past few years a logging operation occurred in the lower reaches of the drainage area and a golf course is currently being built in the upper reaches of drainage area. Both of these activities are potential sources of sediment loading to the gully, along with in-stream bank erosion. Both sites were monitored and the owner/operators made any necessary erosion control changes that were requested. Protecting Fisher Gully is a high priority for the Town of Gorham. They are currently teaming with several entities, including New York State and the Finger Lakes Land Trust to permanently protect approximately 95 acres of the gully’s drainage area.

Major sources of sediment within the watershed include any land disturbing activity such as development, agriculture, impervious surfaces, road bank erosion, mined lands, and timber harvesting. Stream bank erosion is also another major source of sediment. Stream erosion does occur naturally, but is exacerbated when upland activities disturb the riparian buffer or increase the volume and velocity of water entering the stream system as overland flow.

ll Br ll

ully G

Weighted Average

age age

Fisher Gully Fisher

e l

Val

ne i

nnyside

t R.- S R.- t

L. L.

ples Ck- ples

k Ta

r C r

rv Site Sample

Eelpot Ck. Eelpot .

rimes Ck rimes

- t

Pt.

ok's P ok's

Sene y

Figure 2.3: TSS Weighted Average Concentrations 1997-2005 Figure 2.3: TSS Weighted Average

Barne

lly

or Gu or

che

Ti k S k

-C 0.0 k

50.0

450.0 400.0 350.0 300.0 250.0 200.0 150.0 100.0 roo

r B r

uck

S mg/L 49 Sediment accumulation in trout spawning areas of the southern watershed streams is a major concern. As sediment accumulates, it fills the void spaces in the gravelly stream bed thus blocking or covering fish eggs. Sediment is also a major concern at the northern end of the lake because of the shallow shoreline areas. Sediment with phosphorus attached to it will provide the appropriate bottom substrate for increased aquatic vegetation growth. There is some evidence of increased vegetation along the near shore littoral zone. Exotic, invasive species such as Eurasian milfoil tend to dominate areas with recent sediment deposition.

Special monitoring of watershed development sites: The northern half of the Canandaigua Lake watershed is experiencing significant development as compared to the rest of upstate New York. Several developments that are in various stages of approval and/or construction along both sides of the lake could eventually add close to 1,000 new homes to the watershed. In addition to these larger developments, there is also the steady stream of individual lot development that continues throughout the watershed.

While developments can add significantly to the local economy through several important multipliers, the developers need to give high priority to the proper installation and maintenance of stormwater and erosion/sediment control practices so as to protect the place that is drawing their customers, Canandaigua Lake. The Wisconsin Department of Natural Resources has documented that residential construction sites produce 4-10 times more sediment than other land uses including agriculture and rural residential. We need to hold these new developments up to high standards so as to make sure there will not be substantial long-term irreversible impacts on Canandaigua Lake and its surrounding watershed. The recommendations section will describe a few of these standards.

East Lake View case study: On 4/19/04, the outfall from the recently started East Lake View Estates located just south of Turner Rd on State Rt. 364 was sampled for total suspended solids. Test results documented 1,800 mg/L of TSS leaving the outfall based on 0.5 inches of rain as measured at the Canandaigua Water Treatment Plant approximately one mile away. Visual observations by the

50 Watershed Manager documented much clearer running streams and small gullies to the north and south of the development site. Based on multiple years of sampling experience, the Watershed Manager estimates that a stream begins to look muddy at about 90-100 mg/L of TSS. Only during the most extreme storm events do we get values exceeding 1,000 mg/L.

On 9/9/2004 samples were collected throughout the watershed including the East Lake View development site. The stormwater outlet from East Lake View Estates had a concentration of 60 mg/L. The next similar sized gully to the north was sampled approximately 2 minutes later and had a concentration of 32 mg/L. Although this concentration is much lower than the April storm event it was still almost twice as much as a similar sized gully approximately 300 meters to the north. It is also important to point out that each rain event is different and the time within the hydrograph that samples are taken is going to be different. Therefore, it is inappropriate to compare results between storm events.

On 8/31/05, all the streams were sampled during a three inch rain event (remnants of Hurricane Katrina) including the East Lake Rd. subdivision. The stormwater outlet from East Lake View Estates had a concentration of 150 mg/L. None of the other seventeen streams sampled exceeded 100 mg/L! All streams were sampled within four hours and streams such as Gage Gully (8 mg/L) and Deep Run (17 mg/L) were sampled within minutes of the East Lake View site. On 10/8/2005 the stormwater outlet from East Lake View Estates had a concentration of 85 mg/L. Sucker Brook was also sampled within twenty minutes of this event (1.45inches) and had a concentration of 8.5 mg/L.

Over the last two years, the Town of Gorham and the DEC have issued fines and stop work orders to mandate that the development come into compliance with the Town’s Erosion and Sediment Control regulations as well as with the State DEC Phase II stormwater regulations. Although the developer had installed the sediment pond early on in the development process, other basic practices were either not installed or not maintained properly. This past fall the development installed and improved many of the basic erosion and sediment control practices necessary to come into compliance. However, in the spring of 2006, the Town of Gorham, the

51 Town’s engineer and the Watershed Council have documented numerous maintenance problems that must be fixed, otherwise the water quality issues will continue. Increased fines and a stop work order will be issued if the developer does not come into compliance.

Fox Ridge case study: The next phase of the Fox Ridge development along Middle Cheshire Road and just off of Butler Road, began in the early summer of 2005. The developer took the right first step by installing two sediment ponds along with a silt fence at the beginning of the development. Major site clearing and grading commenced during the summer and then work stopped on the site in mid- August and did not re-commence for approximately two months. Over 10 acres of land with some significant slope (>5%) was left bare with no erosion control practices implemented. Phase II stormwater regulations require that if no work within a section of a site will occur for 21 days, then within 14 days of that 21 day period that section of the site needs temporary seed and mulch to stabilize the area. Studies have documented that mulch alone can reduce erosion by up to 90%. This is a classic example of developers relying solely on sediment control practices (i.e. ponds and silt fence) to stop eroded material from leaving the site instead of also implementing the erosion control practices that stop erosion from starting in the first place.

On 9/29/05, initial sampling of the stormwater pond area occurred during a 0.62 inch rain event. Two samples each were collected between the first and second pond and just after the second pond to test the pond’s effectiveness. The two samples collected before the second pond were both 450 mg/L TSS. The two samples collected at the outfall of the second pond were 91 mg/L and 97 mg/L. All samples were collected within 5 minutes. The pond system does show that it is effective in removing significant sediment, however, there was some visible contrast between the second pond outfall and other streams in the area.

During the same 10/8/2005 storm that East Lake View was sampled, the outfall from the second pond on Fox Ridge was also sampled and had a concentration of 130 mg/L of TSS. East Lake View had 85 mg/L and Sucker Brook was 8.5 mg/L. On 10/23/2005 the Fox Ridge outfall from the second pond was sampled again and had a concentration of 62 mg/L. The stream that Fox

52 Ridge drains to was also sampled just upstream of the influence of Fox Ridge and had a concentration of <4 mg/L (below the detection limit). Sucker Brook was also sampled and had a concentration of 8.5 mg/L. All sampling was completed within 20 minutes to minimize any time/hydrograph influences.

During the two month timeframe that the site was left dormant, several calls were made by the Town of Canandaigua to get the developer to implement erosion control activities on the site. No progress was made. Using the water quality data and photographs of the site, the DEC was called in to remedy the situation. The DEC issued a water quality violation ticket and fined the developer $7,000 for water quality violations. The developer was also mandated to implement erosion control practices. Stormwater ponds are designed to remove suspended solids in conjunction with erosion control practices. Stormwater ponds are overwhelmed when the erosion control part of erosion and sediment control is left out of the equation.

In 2006, as site clearing begins for new developments, the watershed program will continue to sample for TSS to make sure that the proper erosion and sediment control practices are put in place and maintained.

Nitrate/Nitrite (Figure 2.4): Nitrate/Nitrite is a measure of the dissolved forms of inorganic nitrogen in the environment. Gage Gully had the highest average concentration over the last nine years with 4.11 mg/L. Deep Run was second with 2.95 mg/L. Fall Brook was third with 2.37 mg/L. Sucker Brook was fourth with 1.55 mg/L. Vine Valley was fifth with 1.21 mg/L. The rankings approach shows the same order and also shows multiple year consistency of this parameter. The NURP studies provided a median concentration of 0.53 mg/L, thus these five streams are substantially higher than the NURP threshold. Although Nitrate/Nitrite is not the limiting nutrient to the lake, it is an indicator of pollution and can impact the levels of algae in the lake. Sources of nitrates are many and include septic systems, barnyard waste, manure, fertilizers (agricultural and residential) and atmospheric deposition. Continued monitoring of Nitrate/Nitrite levels is warranted to determine if any long-term changes occur in nitrate concentrations.

all all

Deep Run Deep

y Weighted Average l

e e

y Gag l

sher G sher

F e

e e

Sunny

L. West R.- West L.

Ck.

Naples Ck- 2 Ck- Naples ry

. an

ir ir

r Site Sample

t Ck. t

Eelp

rimes Ck. rimes

h G

- -

k's k's P

ca ca

Coo e

S y l

s s

Figure 2.4: NO3-NO2 Weighted Average Concentrations 1997-2005 Figure 2.4: Weighted NO3-NO2 Average Barne

Menteth

or Gull or

k Tiche

lar

ok-

4.50 4.00 3.50 3.00 2.50 2.00 1.50 1.00 0.50 0.00 ro mg/L

54 B Sucker Fecal Coliform: Fecal coliform is an indicator bacteria found in the feces of warm blooded animals and is used to determine the presence of harmful bacteria and potential pathogens in water. Approximately 70 samples have been collected during non-event conditions on a fairly regular basis between the months of April through November since 1989. Sampling during dry weather conditions reduces the sources of bacteria and, therefore, provide better detection for presence of human sewage.

During this 16 year span, Sucker Brook had the highest long term average levels of recorded fecal coliform with 725 colonies per 100 ml. Vine Valley was second highest with 625 colonies per 100 ml. Cook’s Point was third highest with 385 colonies per 100 ml. Fall Brook was fourth highest with 369 colonies per 100 ml. Seneca Point Gully was fifth highest with 260 colonies per 100 ml. There are several instances within the top five streams where the sample was “too numerous to count” (TNTC) on the petri dish and were assigned a value of 5,000 colonies in order to have an impact on averages. This number is somewhat arbitrary, but it is an reasonable estimate of the actual total had they been countable.

For finished treated drinking water, current regulations prohibit fecal coliforms in numbers exceeding one colony per 100 ml. The threshold for swimming is 200 colonies per 100 ml. Using these thresholds, the data suggests that some of the streams are impacted by human waste. The main sources of fecal coliform include: failed septic systems, sanitary sewer cross connection with storm sewer, warm blooded animal waste (e.g., livestock, waterfowl, pets, deer), and manure spreading.

Series1

St.

rish r

or k-

Tichne

cke

ee Su

T-18- T-18-

- Men -

l 7

1 ul

s G s

- -

P outfa P T-1

- str

t- t-

eca

Seneca Po Seneca

s Poin s

-15-

1 T

T oo

C e

Cre

s s T-13- T-13-

ple

Na ully ully

r r

rk o

Cla

Fecal 1989-2005 Coliform Levels -

T-12- T-12- T

ey l

wer West River West wer

ne Val ne i

T-8- L T-8-

l l

T-5- V T-5-

er Gu er

s i

ully

- G

ge ge

G -

Run

T-3

Deep Deep

k - -

- oo T

Fall Br Fall

800 700 600 500 400 300 200 100 -

T-1 cfu/100ml

Village of Naples: The Village of Naples has expressed interest in pursuing some type of centralized management of human sewage. Part of their research and analysis included studying whether the current situation of privately owned septic systems in the Village is having any demonstrated water quality impacts. The Watershed Manager was asked to monitor Grimes Creek Raceway, which runs from south to north through the low point of the Village just east of Main Street. Two locations were sampled, the culvert at Ontario Street and at a private residence on East Monier Street, where the Raceway first daylights. Fecal coliform bacteria were also sampled at this location. Results were occasionally elevated, however, the lack of pattern did not allow for any interpretations. The results in Table 2.4 document that there are consistently elevated levels of Nitrate/Nitrite at both locations with the Grimes Creek Raceway. All samples were collected during dry/non-melt conditions to try to isolate the source of nitrogen as septic systems.

TABLE 2.4: Concentrations of Nitrate/Nitrate in Grimes Creek Raceway. Date T-B Ontario St. (mg/L) T-C East Monier St. (mg/L) 3/26/2003 4.8 8.1 4/16/2003 5.4 8.1 6/1/2003 4.2 6/17/2003 7.6 5.5 8/25/2003 6.0 8.4 9/19/2003 5.8 7.9 10/27/2003 4.3 12/21/2003 5.2 7.7 3/11/2004 4.9 7.5

Wetland creation/restoration projects: A series of samples were collected on different segments of the West River during five storm events. Table 2.5 provides the average of those results and documents the positive impact that wetlands and floodplains have on water quality. Williams Street is located in the hamlet of Middlesex approximately 4 miles upstream of the Sunnyside Road sampling station. The West River travels through a broad floodplain and then enters the state owned Hi-Tor wetland complex before reaching the Sunnyside sampling location. There is a dramatic drop in each of the

57 parameters (phosphorus, TSS, and nitrates) along West River from Williams Street to Sunnyside probably due to wetland and floodplain processes (absorption and filtration).

TABLE 2.5: Concentrations of Phosphorus, TSS, and Nitrate/Nitrate in the West River. Location Phosphorus Total Suspended Solids Nitrate/Nitrite (mg/L) (mg/L) (mg/L) West River@ Sunnyside 0.050 33 0.31 West River@ Williams 0.187 127 2.18 Street (hamlet of Middlesex)

Road Salt: Mid-winter visits were made to tributary streams and collected samples were analyzed for road salt contamination (chloride [Cl-] concentration) at the Finger Lakes Community College chemistry lab using the argentometric titration procedure (Standard Methods, 17th edition). This monitoring has been conducted since 1990.

Road salt contamination of tributary streams varies with location and winter severity (Table 2.6 and Figure 2.6). Chloride levels remain high in Lower Sucker Brook, Upper Sucker Brook, Gage Gully and the Cook’s Point Stream. Low results at Clark's Gully and Conklin Gully document background levels typical of forested watersheds lacking major highway corridors.

58 TABLE 2.6: Chloride concentration (mg/L) in Canandaigua Lake tributaries, 2003 - 2006.

2-27 3-09 3-07 2-23 long-term long-term long-term Tributary Code 2003 2004 2005 2006 average minimum maximum Fallbrook T21 103.562.0 143.5 63.0 62.5 24.0 166.5 Deep Run T20 113.5 62.5 177.0 51.0 66.5 22.2 178.5 Gage Gully T19 172.0 78.5 169.0 68.5 95.5 17.2 342.5 Fisher Gully T18 18.0 15.5 102.5 13.0 17.4 0.0 102.5 Upper Vine Valley T17 50.5 29.0 41.5 29.5 31.6 14.3 86.0 Lower Vine Valley T17 45.526.0 41.0 28.5 26.1 12.0 53.0 Upper West River T14 87.5 49.0 67.0 44.5 51.1 26.0 105.5 Lower West River T13 77.5 39.0 51.5 38.5 36.0 17.0 77.5 Clark's Gully T16 1.5 0.0 1.0 0.0 0.9 0.0 4.1 Conklin Gully T11 7.5 3.5 3.5 2.0 3.3 1.0 7.5 Upper Naples Creek T12 47.025.5 43.5 28.5 23.8 11.0 49.5 Lower Naples Creek T12 46.524.0 51.5 38.5 24.6 12.0 51.5 Cook's Point Stream T27 322.0140.0 210.5 121.0 150.3 75.0 322.0 Tannery Creek * T10 49.0 14.0 44.0 24.5 31.8 14.0 49.0 Reservoir Creek * T9 66.5 29.0 82.0 37.0 50.3 29.0 82.0 Eelpot Creek * T8 30.5 22.0 27.5 23.0 24.8 21.0 30.5 Hick's Gully T6 148.0 44.5 75.5 45.0 54.8 15.0 148.0 Seneca Point Stream T5 92.5 40.5 79.0 38.5 44.7 20.9 93.5 Barnes Gully T4 166.0 70.5 118.0 57.0 75.7 29.0 202.5 Menteth Gully T3 108.0 66.0 88.5 58.5 59.7 27.0 109.0 Tichenor Gully T2 104.0 58.0 70.5 67.0 56.4 27.0 104.0 Upper Sucker Brook T1 216.0119.5 250.5 114.0 142.6 54.4 489.0 Lower Sucker Brook T1 278.0242.5 335.5 63.0 176.4 34.5 607.0 Outlet out 39.528.0 110.5 33.0 36.3 18.5 110.5

* new sites added to the road salt sampling program in February 2002

59 Tributary Chloride Canandaigua Lake, 2-27-2003

350

300

250

200

150 chloride (mg/L) chloride

100

0 T21 T20 T19 T18 T17 T17 T14 T13 T16 T11 T12 T12 T27 T10 T9 T8 T6 T5 T4 T3 T2 T1 T1 out tributary code

Tributary Chloride Canandaigua Lake, 3-09-2004

350

300

250

200

150 chloride (mg/L) chloride

100

0 T21 T20 T19 T18 T17 T17 T14 T13 T16 T11 T12 T12 T27 T10 T9 T8 T6 T5 T4 T3 T2 T1 T1 out tributary code

60 Tributary Chloride Canandaigua Lake, 3-07-2005

350

300

250

200

150 chloride (mg/L) chloride

100

0 T21 T20 T19 T18 T17 T17 T14 T13 T16 T11 T12 T12 T27 T10 T9 T8 T6 T5 T4 T3 T2 T1 T1 out tributary code

Tributary Chloride Canandaigua Lake, 2-23-2006

350

300

250

200

150 chloride (mg/L) chloride

100

0 T21 T20 T19 T18 T17 T17 T14 T13 T16 T11 T12 T12 T27 T10 T9 T8 T6 T5 T4 T3 T2 T1 T1 out tributary code

FIGURE 2.6: Road salt contamination in Canandaigua Lake tributaries.

61 Seventeen years of chloride record now exist for these tributary streams to Canandaigua Lake. Figure 2.7 presents a graphical summary where each year is represented by the mean chloride concentration in tributary streams. The years 2000, 2003 and 2005 stand out as harsh seasons where more road salt was being applied during mid-winter months. While the winter cumulative road salt application totals may vary only slightly from year to year, the event-based application rates produce the significant differences captured in these data.

Watershed Chloride Canandaigua Lake 1990-2006

250

200

150

100 chloride (mg/L) chloride

0 1990 1991 1992 1993 1994 1995 1996 1997 1998 1999 2000 2001 2002 2003 2004 2005 2006 year

FIGURE 2.7: Long-term watershed chloride trends based on mid-winter sampling, 1990-2006.

62 Recommendations and Topics for Future Research:

• Continue the lake sampling and monitoring program. Winter total phosphorus measurements should be conducted to further investigate the apparent trend towards nutrient enrichment revealed in the Carlson trophic state index. Identify phytoplankton species contributing to unusual blooms, and attempt to determine causes of such blooms. • Increases in nutrient and sediment loading are a significant threat to the long-term health of Canandaigua Lake. Local municipalities and DEC need to strictly enforce regulations involving erosion/sediment control and stormwater management . This is immediately critical where development is near water supply intake pipes. With inadequate control, increased sediment will raise filtration costs and make the water supply more susceptible to biological contamination. Sediment loading also adversely affects fish spawning, aquatic foodwebs and may lead to establishment/expansion of undesirable aquatic vegetation. • Consider adoption of updated standards involving local erosion/sediment control laws that are at least as strict as the New York State standards. Increase fine amounts and the ability to issue stop work orders to assure compliance with the local law. Adopt the State standards in the local laws. Consider increasing the local water quality standards for new development from the general State standards, in recognition of the need to protect Canandaigua Lake’s function as a drinking water reservoir. • Conduct a segment analysis of Eelpot stream to identify potential sources of pollution. • Develop a non-point source pollution model using the newly acquired landcover data, aerial imagery, soils data and LiDAR slope measurements. Compare model predictions to actual stream data. Use model to help prioritize streams most suited to implementation of best management practices. • Investigate whether sediment loads are correlated with high gradient vs. low gradient streams. Also investigate the land cover/land use patterns within a defined stream buffer zone. Partner with landowners to install appropriate stream buffer land uses. • Continue the Agricultural Environmental Management Program under the leadership of the Ontario County Soil and Water Conservation District and the Agricultural Program Committee. 63 • Continue to pursue adoption of timber harvesting law, coupled with educational programs for the local forestry industry. • Educate watershed residents on the relationship between land use activities and water quality, with a special emphasis on the reduction of phosphorus.

64 Literature Cited: Berg, C.O. 1963. Middle Atlantic States in: Frey, D.G. (ed.) Limnology in North America. Univ. of Wisconsin Press. Madison, Wisconsin. pp 191-237.

Cole, G.A. 1994. Textbook of Limnology. Waveland Press, Inc. Prospect Heights, Illinois. 412 p.

Dodson, S.I. 2005. Introduction to Limnology. McGraw Hill Companies, Inc. New York, New York. 400 p.

Eaton, S.W. and L.P. Kardos. 1978. The limnology of Canandaigua Lake in: Bloomfield, J. (ed.) Lakes of New York State, Volume 1: Ecology of the Finger Lakes. Academic Press. New York, New York. pp 225-311.

Gilman, B.A. 1993. Summer monitoring of Canandaigua and Honeoye Lakes. Finger Lakes Community College. Canandaigua, New York. 39 p.

Gilman, B.A. 1994. 1994 water quality monitoring program for Canandaigua Lake and Honeoye Lake. Finger Lakes Community College. Canandaigua, New York. 54 p.

Gilman, B.A. 1996. 1996 water quality monitoring program for Canandaigua Lake. Finger Lakes Community College. Canandaigua, New York. 36 p.

Gilman, B.A. 1997. 1997 water quality monitoring program for Canandaigua Lake. Finger Lakes Community College. Canandaigua, New York. 26 p.

Gilman, B.A. 1998. 1998 water quality monitoring program for Canandaigua Lake. Finger Lakes Community College. Canandaigua, New York. 24 p.

Gilman, B.A. 1999. 1999 water quality monitoring and trend analyses for Canandaigua Lake. Finger Lakes Community College. Canandaigua, New York. 41 p.

Gilman, B.A. 2000. Year 2000 water quality monitoring and trend analyses for Canandaigua Lake. Finger Lakes Community College. Canandaigua, New York. 47 p.

Gilman, B.A. 2002. 2001-2002 water quality research for Canandaigua Lake and its watershed. Finger Lakes Community College. Canandaigua, New York. 87 p.

Gilman, B.A. and K.L. Olvany. 2003. 2002-2003 water quality research for Canandaigua Lake and the watershed. Finger Lakes Community College. Canandaigua, New York. 69 p.

Gilman, B.A. and L. Rossi. 1983. Weedbed productivity at the south end of Canandaigua Lake. Community College of the Finger Lakes. Canandaigua, New York. 12 p.

65 Makarewicz, J.C. and T.W. Lewis. 1998. Nutrient and sediment loss from watersheds of Canandaigua Lake. SUNY Brockport. Report to Canandaigua Lake Watershed Taskforce. 45 p.

Makarewicz, J.C. and T.W. Lewis. 1999a. The loss of nutrients and materials from the Naples Creek watershed. SUNY Brockport. Report to Canandaigua Lake Watershed Taskforce. 21 p.

Makarewicz, J.C. and T.W. Lewis. 1999b. Nutrient and sediment loss from watersheds of Canandaigua Lake: January 1997 to January 1999. SUNY Brockport. Report to Canandaigua Lake Watershed Taskforce. 46 p.

Makarewicz, J.C. and T.W. Lewis. 2000. Nutrient and sediment loss from watersheds of Canandaigua Lake: January 1997 to January 2000. SUNY Brockport. Report to Canandaigua Lake Watershed Taskforce. 52 p.

Makarewicz, J.C. and T.W. Lewis. 2001a. Canandaigua Lake subwatersheds: Time trends in event loading and the watershed index. SUNY Brockport. Report to Canandaigua Lake Watershed Taskforce. 32 p.

Makarewicz, J.C. and T.W. Lewis. 2001b. An addendum to segment analysis of Sucker Brook: The location of sources of pollution. SUNY Brockport. Report to Canandaigua Lake Watershed Taskforce. 19 p.

Makarewicz, J.C. and T.W. Lewis. 2001c. Stressed stream analysis of Deep Run and Gage Gully in the Canandaigua Lake watershed. SUNY Brockport. Report to Canandaigua Lake Watershed Taskforce. 76 p.

Olvany, K. (editor). 2000. The Canandaigua Lake Watershed Management Plan: A strategic tool to protect the lifeblood of our region. Canandaigua Lake Watershed Council.

Sherwood, S.D. 1993. Report on the determination of existing and potential pollutants affecting the Canandaigua Lake watershed. Center for Governmental Research. Rochester, New York. 127 p.

Wetzel, R.G. 1983. Limnology. Saunders College Publishing. New York, New York. 767 p.

Wetzel, R.G. and G.E. Likens. 1991. Limnological analyses. Springer-Verlag New York, Inc. 391 p.