water quality report · frequencies and synthetic indices have been used. a brief explanation of...

WATER QUALITY REPORT

HEALTH OF CANANDAIGUA LAKE

AND TRIBUTARY STREAMS

by

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

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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 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .

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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.

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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.

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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.

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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.

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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

8

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.

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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

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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.

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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.

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Deep Run Profile

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Deep Run Profile

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

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Seneca Point Profile

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

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Deep Run Profile

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Deep Run Profile

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

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

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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

21

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

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Lake Clarity (2003)

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Lake Clarity (2004)

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Lake Clarity (2005)

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

24

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.

25

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 Point

1.64 2.77 1.36 3.33 1.65 1.92 3.33 3.78

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 Mean *

1.27 5.80 1.47 2.71 1.84 1.55 2.00 3.58

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 Point

7.16 2.13 2.37 4.46 3.59 2.76 2.26 1.70


4.40 2.29 3.38 3.10 3.11 1.87 1.51 1.31

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 Point

1.30 1.33 1.75 2.00 2.77 2.79 2.77 1.43


1.27 2.34 1.74 1.97 2.48 2.53 2.43 1.82

* adjusted mean = without West River values, this station is excluded because it more often

reflects river conditions rather than lake quality.

26

Mean Algal Abundance (2003)

0

1

2

3

4

5

6

7

4-30 5-27 6-27 7-25 8-29 9-26 10-31 11-26

sampling date

chlo

roph

yll a

(mic

rogr

ams/

liter

)


0

1

2

3

4

5

6

7

4-30 6-04 7-02 7-29 8-23 9-29 10-28 11-23

sampling date

chlo

roph

yll a

(mic

rogr

ams/

liter

)

27


0

1

2

3

4

5

6

7

5-2 5-31 6-25 7-28 8-30 9-28 10-28 12-3

sampling date

chlo

roph

yll a

(mic

rogr

ams/

liter

)

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,

28

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±0.141997 1.55 1.05 0.78 0.82 0.74 0.75 0.72 0.68 0.89±0.291998 0.90 0.54 0.57 0.50 0.86 0.77 0.83 0.77 0.72±0.161999 0.91 0.83 0.71 0.60 0.59 0.50 0.71 0.86 0.71±0.152000 0.94 0.66 0.80 0.59 0.72 0.57 0.47 0.67 0.68±0.152001 1.06 0.98 1.03 0.69 0.90 0.83 0.75 0.48 0.84±0.202002 1.06 0.46 1.05 0.84 1.11 1.63 0.56 0.69 0.93±0.372003 0.80 2.48 0.93 0.63 1.18 0.50 0.41 1.38 1.04±0.672004 0.41 1.03 1.30 0.61 0.81 0.47 0.42 0.79 0.73±0.322005 0.92 2.13 0.91 0.68 0.62 0.84 0.67 1.04 0.98±0.49

29

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

0123456789

10

1996 1997 1998 1999 2000 2001 2002 2003 2004 2005

April - November mean

ug/L

......

....m

eter

s

secchi diskchlorophyll a

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

30

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)

0

2

4

6

8

10

12

14

16

18

SP-2 SP-25 SP-50 DR-2 DR-25 DR-50 WR-2 VV-2 HP-2 FB-2

sampling location

mic

rogr

ams/

liter

31


0

2

4

6

8

10

12

14

16

18


sampling location

mic

rogr

ams/

liter


0

2

4

6

8

10

12

14

16

18


sampling location

mic

rogr

ams/

liter

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

32

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!

33

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

0123456789

10

1996 1997 1998 1999 2000 2001 2002 2003 2004 2005year

mic

rogr

ams/

liter

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

34

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 Depth (m)

Apr

May

Jun

Jul

Aug

Sep

Oct

Nov

Apr-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 Depth (m)

Apr

May

Jun

Jul

Aug

Sep

Oct

Nov

Apr-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

35

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

36

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

37

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 Average1995 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.

38

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).

39

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.

40

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

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,

Date

Precipitation (in) 2 Days

Before

Precipitation (in) 1 Day

Before

Precipitation (in) Day Of

Precipitation (in) Day After (after 8am on

sampling date)

Estimated Percentage of

Rain ending up 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%

41

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.

42

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

43

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.

44

Phosphorus (mg/L)1997-8 1998-9 2000 2001-2 2003 2004 2005 Average of Color Legend

Subwatershed Location RankingsWorst 33%

T-1 Sucker Brook-Clark St. 11 16 11 17 16 13 5 12.7 Middle 33%T-2 Tichner Gully 5 10 6 9 17 14 7 9.7 Best 33%T-3 Menteth 2 5 15 8 12 5 4 7.3T-4 Barnes Gully 1 1 12 3 11 4 3 5.0T-5 Seneca Pt. 6 8 14 12 13 2 9 9.1T-27A Cook's Pt- Mouth 3 4 16 6 2 16 10 8.1T-7 Grimes Ck. 6 3 2 3 1 11 4.3T-8 Eelpot Ck. 11 9 14 5 17 17 12.2T-9 Reservoir Ck. 7 17 7 1 3 16 8.5T-10 Tannery Ck.- East Hill Rd. 2 8 5 4 6 15 6.7T-12 Naples Ck- 245 12 12 5 15 15 15 12 12.3T-13 L. West R.- Sunnyside 7 3 2 1 7 9 1 4.3T-17 Vine Valley 13 14 4 16 14 12 14 12.4T-18 Fisher Gully 4 9 10 13 6 8 8 8.3T-19 Gage Gully 10 17 13 11 10 10 12 11.9T-20 Deep Run 9 15 7 4 9 11 6 8.7T-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



Nitrate/Nitrite (mg/L)1997-8 1998-9 2000 2001-2 2003 2004 2005 Average of Color Legend



45

TABLE 2.3: Combined average concentrations for each of the streams from 1997-2005. (fecal coliform measurements are from 1989-2005).

Stream TP (mg/L)

Nitrate/Nitrite(mg/L)

TSS (mg/L)

Fecal Coliform (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.

46

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.

47

Figu

re 2

.2: T

otal

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rus

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d Av

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199

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48

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.

49

Figu

re 2

.3: T

SS W

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Aver

age

Con

cent

ratio

ns 1

997-

2005

0.0

50.0

100.

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50

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

51

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

52

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

53

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.

54

Figu

re 2

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ted

Aver

age

Conc

entra

tions

199

7-20

05

0.00

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3.00

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rook-C

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mg/LW

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55

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.

56

Feca

l Col

iform

Lev

els

1989

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5

0

100

200

300

400

500

600

700

800

T-1- F

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57

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

58

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(mg/L)

Total Suspended Solids (mg/L)

Nitrate/Nitrite(mg/L)

West River@ Sunnyside 0.050 33 0.31 West River@ Williams Street (hamlet of Middlesex)

0.187 127 2.18

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.

59

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

Tributary Code 2-27 2003

3-09 2004

3-07 2005

2-23 2006

long-term average

long-termminimum

long-termmaximum

Fallbrook T21 103.5 62.0 143.5 63.0 62.5 24.0 166.5Deep Run T20 113.5 62.5 177.0 51.0 66.5 22.2 178.5Gage Gully T19 172.0 78.5 169.0 68.5 95.5 17.2 342.5Fisher Gully T18 18.0 15.5 102.5 13.0 17.4 0.0 102.5Upper Vine Valley T17 50.5 29.0 41.5 29.5 31.6 14.3 86.0Lower Vine Valley T17 45.5 26.0 41.0 28.5 26.1 12.0 53.0Upper West River T14 87.5 49.0 67.0 44.5 51.1 26.0 105.5Lower West River T13 77.5 39.0 51.5 38.5 36.0 17.0 77.5Clark's Gully T16 1.5 0.0 1.0 0.0 0.9 0.0 4.1Conklin Gully T11 7.5 3.5 3.5 2.0 3.3 1.0 7.5Upper Naples Creek T12 47.0 25.5 43.5 28.5 23.8 11.0 49.5Lower Naples Creek T12 46.5 24.0 51.5 38.5 24.6 12.0 51.5Cook's Point Stream T27 322.0 140.0 210.5 121.0 150.3 75.0 322.0Tannery Creek * T10 49.0 14.0 44.0 24.5 31.8 14.0 49.0Reservoir Creek * T9 66.5 29.0 82.0 37.0 50.3 29.0 82.0Eelpot Creek * T8 30.5 22.0 27.5 23.0 24.8 21.0 30.5Hick's Gully T6 148.0 44.5 75.5 45.0 54.8 15.0 148.0Seneca Point Stream T5 92.5 40.5 79.0 38.5 44.7 20.9 93.5Barnes Gully T4 166.0 70.5 118.0 57.0 75.7 29.0 202.5Menteth Gully T3 108.0 66.0 88.5 58.5 59.7 27.0 109.0Tichenor Gully T2 104.0 58.0 70.5 67.0 56.4 27.0 104.0Upper Sucker Brook T1 216.0 119.5 250.5 114.0 142.6 54.4 489.0Lower Sucker Brook T1 278.0 242.5 335.5 63.0 176.4 34.5 607.0Outlet out 39.5 28.0 110.5 33.0 36.3 18.5 110.5 * new sites added to the road salt sampling program in February 2002

60

Tributary Chloride Canandaigua Lake, 2-27-2003

0

50

100

150

200

250

300

350

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

chlo

ride

(mg/

L)


0

50

100

150

200

250

300

350


tributary code

chlo

ride

(mg/

L)

61


0

50

100

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tributary code

chlo

ride

(mg/

L)


0

50

100

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200

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300

350


tributary code

chlo

ride

(mg/

L)

FIGURE 2.6: Road salt contamination in Canandaigua Lake tributaries.

62

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

0

50

100

150

200

250

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

year

chlo

ride

(mg/

L)

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

63

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.

64

• 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.

65

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.

66

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.

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