ML20027E843
| ML20027E843 | |
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|---|---|
| Site: | Summer  |
| Issue date: | 11/11/1982 |
| From: | DAMES & MOORE |
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| NUDOCS 8211160245 | |
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E ENVIRONMENTAL MONITORING REPORT JANUARY 1981 - DECEMBER 1981 I
FOR THE FEDERAL ENERGY REGULATORY COMMISSION PROJECT LICENSE NUMBER 1894, THE SOUTH CAROLINA DEPARTMENT OF HEALTH AND ENVIRONMENTAL CONTROL, AND THE NUCLEAR REGULATORY COMMISSION I
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0 95 5182-100-09 1981 L
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SUMMARY
The monitoring programs being conducted at the present tima are de-signed to meet the licensing requirements of the regulatory agencies.
I The Federal Energy Regulatory Commission (FERC) requires five years of post operational data for the Fairfield Pumped Storage Facility. To satisfy the FERC requirements, water quality and biological parameters are monitored in the Broad River and in Parr and Monticello Reservoirs.
The monitoring program is also designed to meet the licensing require-aI ments of the Nuclear Regulatory Commission (NRC) and the requirements of the National Pollution Discharge Elimination System (NPDES) permit for the Virgil C. Summer Nuclear Station (VCSNS) issued by the South Carolina Department of Health and Environmental Control (SCDHEC).
These studies will provide for comparison between preoperational base-line conditions and postoperational impacts.
i This report, which is the fifth one for the current monitoring pro-gram, will be submitted to FERC, NRC, and the SCDHEC. The report includes a summary of data for aquatic biology, surface water chem-istry, and terrestrial data collected throughout 1981. The discussion of the data compares information collected during this reporting period with previous data, where applicable. The purpose of the environmental
,I monitoring program is twofold:
- 1) to establish baseline conditions on Monticello Reservoir prior to the operation of the VCSNS, and 2) to determine what impacts, if any, are occurring to the biota in Parr and Monticello Reservoirs as a result of operating the Fairfield Pumped Storage Facility (FPSF). A detailed description of the history of the reservoirs, collecting stations, and other pertinent information were reported in Section 1 of the Environmental Monitoring Report, June through December 1978 (Dames & Moore, 1978).
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The surface water temperatures at all stations during this reporting period were below the 32.2*C maximum temperature standard established by the SCDHEC, with the exception of a single hourly value of 32.4*C recorded during July at Station 11 (Neal Shoals Dam). Water tempera-tures generally followed seasonal trends and wen highest in July and I
lowest in January. At the Broad River and Park Reservoir Stations, no seasonal thermocline occurred; this was due to the shallow depths and the high current velocity.
In Monticello Reservoir, stratification did occur and a thermocline was noted at the deeper stations from April through October.
I The dissolved oxygen (DO) concentrations, along with temperature, i
followed seasonal trends. Higher DO values occurred during the colder months and lower values during the warmer months. At the Parr Reser-
,l voir and Broad River Stations, DO was found throughout the water I
columns in a sufficient concentration to support aquatic life.
In Monticello Reservoir, DO concentrations at the surface and upper levels of the water column were generally greater than the minimal statutory limit (4.0 mg/1) established by the SCDHEC. There were, however, occasional periods during June through September that depressed oxygen levels were recorded at the United States Geological Survey (USGS) monitor at the FPSF intake. At the lower strata of the water column I
and at the bottom of most stations in Monticello Reservoir the DO values were also below the standards established by the SCDHEC. These depressed oxygen concentrations were due to the stratification and incomplete mixing of the water, a situation which was not found during I
the colder months when the reservoir " turned over" and complete mixing of the water occurred.
I The pH, values recorded at the stations in the Broad River and Parr Reservoir were within the range (6.0 to 8.5 units) of the values prescribed by the SCDHEC.
In Monticello Reservoir the pH exceeded the state standard at the surface of certain stations during the spring and summer months, and in the subimpoundment during May.
The high values I
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were attributed to photosynthetic activity and can be expected during 3
the warm months. Below the thermocline in Monticello Reservoir, the pH fell below the state standard during several months of the year; this situation is not considered unusual in reservoirs that are stratified.
In general, the pH followed seasonal trends in the water bodies. The higher values were recorded during the spring and summer months when photosynthesis of phytoplankton was at its peak; the lower (more neutral) values occurred during the colder months.
I The water clarity, as indicated by higher transparency readings, was much better in Monticello Reservoir than in either the Parr Reservoir or the Broad River Stations. This increased transparency was due to j
settling of suspended particles characteristic of reservoirs as com-pared to the more turbid conditions that exist in lotic systems, such i
as the Broad River and Parr Reservoir.
In Parr Reservoir and the Broad River, nitrate values have ranged from 0.1 mg/ liter to 5.7 mg/ liter during 1978 through 1981. The mean value for this 4-year period was 1.85 mg/ liter. The mean values for nitrate have shown very little fluctuation during these studies, ranging from 1.80 to 1.89.
I At the Neal Shoals Dam station, during 1978 through 1981, nitrate j
values have ranged from 0.5 mg/ liter to 4.8 mg/ liter. The mean value during this 4 year period was 1.9 mg/ liter.
In Monticello Reservoir nitrate values ranged from 0.1 mg/ liter to 4.5 mg/ liter during 1978 through 1981. The mean value for this 4 year I
perint was 1.28 mg/ liter. There has been no well defined pattern for nitrate values in Monticello Reservoir during this time. This pattern is not uncommon in new reservoirs that have been recently flooded, I
cince nutrients are being leached from the soil.
In addition the water quality in Monticello Reservoir is influenced by water that is pumped l
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I up from the Broad River. Values of nitrate in the subimpoundment ranged from 0.1 mg/ liter to 2.1 mg/ liter during 1978 through 1981. The I
mean value during the 4 year period was 0.74 mg/ liter. The trend for nitrate in the subimpoundment has been to generally increase; this increase in nitrate may be attributed in part to the addition of fertilizer as part of the management program for this water body.
I Phosphate levels in Parr Reservoir and the Broad River ranged from 0.01 mg/ liter to 0.92 mg/ liter during 1978 through 1981. The mean value for the 4-year period was 0.33 mg/ liter.
The general trend showed a decrease in the mean value during 1981 (0.17 mg/ liter) after a I
high mean value of 0.75 mg/ liter was reached during 1980. At the Neal Shoals Dam station the range of phosphate values was from 0.09 mg/ liter i
to 4.4 mg/ liter; the mean value during the 4 year period was 0.64 I
mg/ liter.
In Monticello Reservoir phosphate values ranged from 0.01 mg/ liter to 4.5 mg/ liter. The mean value during the 1978 through 1981 period was 0.41 mg/ liter. There was a general increase in phosphate from 1978 through 1980, and then the values decreased during 1981.
In the subimpoundment the phosphate values ranged from 0.03 mg/ liter to 2.1 mg/ liter, with a mean phosphate value of 0.31 mg/ liter. The values I
of phosphate in the subimpoundment have fluctuated, due in part to the application of fertilizer during several months of the year.
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l Ammonia values at stations in the Broad River and Parr Reservoir ranged from 0.1 mg/ liter to 1.6 mg/ liter during 1978 through 1981. The mean value for this 4 year period was 0.35 mg/ liter. There was a general increase in ammonia from 1978 through 1980 and then a decrease in 1981.
At the Neal Shoals Dam station the ammonia values ranged from 0.1 l
mg/ liter to 1.1 mg/ liter. The mean value during the period 1978 g
W through 1981 was 0.34 mg/ liter.
In Monticello Reservoir ammonia values ranged from 0.1 mg/ liter to 1.0 mg/ liter. The mean value during the l
period 1978 through 1981 was 0.32 mg/ liter.
In the subimpoundment I
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ammonia values ranged from 0.1 to 2.2 mg/ liter; the mean value for the period 1978 through 1981 was 0.6 mg/ liter.
At all of the water bodies, at least once during the summer, the con-centration of un-ionized ammonia exceeded the criterion recommended by the U.S. Environmental Protection Agency (USEFA) (1976). This condi-I tion occurred during 1980, but only in Monticello Reservoir. The criterion suggested for ammonia is based on the amount of un-ionized ammonia (NH3) present in solution, which is highly dependent on the temperature and pH of the water body being sampled. Although the con-centrations of total ammonia (NH3 + NH4) were within the historical range occurring in the Broad River, the high pH values recorded at the surface resulted in a greater percentage of the total ammonia being in the un-ionized form. The un-ionized ammonia concentration recorded at the collecting stations is not considered unusual because the tempera-ture, pH, and total ammonia values were within the ranges expected under natural conditions.
Concentrations of heavy metals in Parr Reservoir and the Broad River I
were detected in water samples but occurred in concentrations at or below the lower limit of the analytical procedure with the exception of copper, zinc, and iron. Copper exceeded the lower sensitivity limit at Station 5A (Broad River) during July; however, the value (0.03 mg/ liter) was less than the maximum (0.06 mg/1' iter) recommended by the USEPA (1976) for the well being of aquatic species. Concentrations of zine were detected at several stations, several times during the year.
How-ever in only one case (Station 2, October; 0.16 mg/ liter), did the value exceed the maximum criterion (0.05 mg/ liter) established by the USEPA (1976) for the well being of aquatic species. Concentrations of iron at the stations on the Broad River and in Parr Reservoir exceeded the recommended maximum (1.0 mg/ liter) criterion established by the USEPA at least once during the year. These high values were attributed to I
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iron being a prime constituent of the soils in the area and were coincidental with runoff and high suspended solids values.
In the subimpoundment, the concentration of heavy metals was below the level of sensitivity of the analytical procedure.
In Monticello Reser-voir, the concentration of heavy metals throughout the current moni-I tering program, with the exception of iron and zinc, was below the level of sensitivity of the analytical procedure. The values of iron and zine did not exceed recommended levels established by the USEPA.
These metals are soluble constituents of the soil in the area and high values are to be expected in waters receiving runoff from these soils.
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Copper values have ranged from <0.02 - 0.03 mg/ liter at stations in the j
I Broad River and in Parr Reservoir. At Stations 1 and SA, values of f
0.03 mg/ liter were recorded twice during the period, once for each station. All of the other values recorded were between <0.02 or 0.02 mg/ liter. At stations in Monticello Reservoir, values were either
<0.02 or 0.02 mg/ liter. Zine values at statioris in the Broad River and Parr Reservoir have ranged from 0.01 to 0.59 mg/ liter from 1978 through 1981. The trend has been a decrease since 1978. During 1978 and 1979 5
the mean values for stations in the Broad River and Parr Reservoir were 0.02 mg/ liter. During 1980 and 1931 the mean values were 0.01 mg/ liter, with the exception of Stations 1 (1980) and 2 (1981), where the mean values were 0.02 mg/ liter. 'In Monticello Reservoir zine values have ranged from 0.01 to 0.52 mg/ liter. The general trend has been a decrease in zine concentrations from 1978 to the present.
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1978,1979, and 1980 the mean values were generally 0.02 mg/ liter while during 1981 all the stations recorded zine values of 0.01 mg/ liter.
Iron values in Parr Reservoir and the Broad River during the past four years have ranged from 0.22 to 29.0 mg/ liter. Mean values of iron con-centrations have generally declined since 1978. The values recorded for 1978 and 1979 were 2.01 and 1.79 mg/ liter, respectively; during 1980 the mean iron concentration was 2.53 mg/ liter.
It was during 1980 that the largest maximum values were recorded, 13, 20, and 29 mg/ liter.
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The reason (s) for these high values are unknown, but are probably due to rainfall runoff preceding the sampling period.
During 1981 the iron values decreased and the mean concentration was 1.12 mg/ liter. In I
Monticello Reservoir iron values have ranged from 0.02 to 0.86 mg/ liter. The trend has been a slight decrease since 1978; the mean average has ranged from 0.32 mg/ liter in 1978 to 0.28 mg/ liter in 1981.
The vascular hydrophyte community in Parr Reservoir has become abun-dant. Much of the vegetation is located in backwater areas of the I
reservoir. The community of hydrophytes at the Neal Shoals Dam sam-pling station has shown very little change in species composition since 1
1978. Willows continue to be the dominant form of vegetation at this
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communities of hydrophytes, compared to the other sampling locations.
The rich assemblage of flora may be attributed to the fertilization program being carried out ati this location.
In Monticello Reservoir, I
vegetative associations, especially within the coves, are continuing to show development. Communities of cattai'Is, rushes, and willows dominate the coves; in these areas the substrate appears to be high in I
organic content, associated with the development of this vegetation.
The phytoplankton species ccmposition in Parr Reservoir showed definite seasonal patterns during the past'four years. An algal bloom was present during January at all stations in Parr Reservoir. During the three collecting periods (April, July, October) a general decline next in numbers was observed with the October samples showing the lowest gu numbers. Diatoms predominated the collections at all stations during l
every sampling period, with the exception of Station B.
At Station B, phytoplankton samples were comprised primarily of green and blue green algae. At the Neal Shoals Dam station, diatoms were the most abundant phytoplankton group during all the sampling periods, except during July j
when the green algae were the most dominant. The lowest phytoplankton
.I densities occurred during January and reached their peak during July.
At the subimpoundment, phytoplankton densities were highest during vii c
n-October and lowest in January. During January and July diatoms were the most abundant algal group at this station, making up more than half of the co:mnunity. During April, chlorophytes were the most abundant group, comprising nearly two-thirds of the community, and during October the blue geeen algae were the most numerous.
In Monticello Reservoir phytoplankton densities reached their peak at all stations during the July sampling period and then declined to their lowest level during November. During January there was an algal bloom on this reservoir. Diatoms were the most abundant group of organisms collected throughout the year with the exception of August and September; during I
August the green algae were the dominant group and in September diatoms and green algae were codominants.
An analysis of the zooplankton data during 1981 indicated that the species composition was similar to that reported during the 1978, 1979, and 1980 investigations. The distribution of taxa in the water bodies appeared to follow seasonal trends; this distribution also indicated that generally stable zooplankton communities existed, as compared with previous years' data. The rotifers were the dominant group collected throughout the study area. The overall densities and taxonomic diver-sities at the stations appeared to be similar to the historical data.
The larval fish collections made during 1981 revealed that each of the four major areas (Parr and Monticello Reservoirs, Neal Shoals, and the subimpoundment) harbored a distinct larval fish community. The ich-thyofauna collected in Parr Reservoir were the most diverse among the 8
areas sampled; eight taxa were collected here with the clupeids (giz-zard shad) being the dominant species. At the Neal Shoals Dam station, six taxa were collected with the gizzard shad and crappie being the most abundant. The dominant ichthyofauna in the subimpoundment were the sunfishes; however, during 1981 the gi::zard shad increased their numbers substantially, indicating that reproducing populations have become established. The subimpoundment also had the highest overall 8
larval fish density of the collecting areas.
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the perciethids (temperate basses) are becoming more abundant indicat-ing that reproducing populations of these species are occurring. Col-lections from Monticello Reservoir showed the greatest overall increase I
in larval fish diversity, as compared to previous years. This increase is indicative of a developing fishery.
The benthic macroinvertebrate communities in all of the water bodies sampled illustrated stable conditions with respect to density and diversity of organisms. The only exception to this was at Station B in Parr Reservoir where there was a decline in ecological stability and I
complexity as compared to previous years. This station is in the tail-race canal and is subjected to daily, high current velocities. Thus, the substrate is scoured providing a poor habitat for benthic organ-I isms. The benthic macroinvertebrate community at Neal Shoals Dam and Parr Reservoir was relatively unchanged from the previous studies, with the exception of Transect C in Parr Reservoir. At Transect C, during the past three years there has been a trend of declining numbers and diversity of benthic organisms. The reasons for the decline is due to the fluctuating water levels caused by the FPSF. This trend is still within the limits of natural variation in Parr Reservoir. At the Neal Shoals Dam station, the benthic community shows maintenance of ecologi-cal stability and complexity, compared with previous years.
In the subimpoundment, the benthic community that is established continues to increase while no new organisms are colonizing the area; thus, there is a high density and a low diversity. The benthic community in Monti-cello Reservoir continues to increase in overall mean annual values for density and taxonomic composition, with the exception of the extreme northern area of Monticello Reservoir; this area maintained a benthic community structure in 1981 similar to that reported for 1980. The Asiatic clam continues to colonize new areas of Monticello Reservoir and has now been documented at all of the collecting areas with the exception of the subimpoundment.
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The results of the fish sampling efforts indicated that the fish community of the water bodies in the study area was dominated by two groups:
the clupeids (shad) and centrarchids (bream, bass, and I
crappie).
The clupeid family was represented by une species gizzard shad.
Gizzard shad were collected at least once during the year from every sampling station. The centrarchid family was represented by nine species, of which bluegill was the most common; this species was also collected at every sampling station at least once during the year.
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Parr Reservoir, bluegill was the most numerous species collected and gizzard shad was second in abundance. Overall, the species composition of Parr Reservoir has remained virtually the same throughout the past four years. The groups that have been most abundant, such as the sun-fish, shad, gar, carp, shiners, carpsuckers, and some species of cat-fish, have been found in collections every year, whereas those groups that have a relatively low population occurred sporadically from year to year; these groups included some bullheads, madtoms, yellow perch, and darters. Of special interest is the white bass that occurred in Parr Reservoir for the first time during 1981. This species is occur-ring in larger numbers in Monticello Reservoir and apparently was transported into Parr Reservoir through the FPSF. Age and growth atudies indicated that five year classes of both gizzard shad and blue-gill were found in Parr Reservoir. Growth of both species was somewhat slower than populations from similar habitats in the southeastern United States.
Standing crop estimates from Parr Reservoir decreased from the previous year, which may have been attributed, in part, to the p
d fluctuating water levels and the extremely low water conditions that prevailed during much of 1981. The most abundant species collected was the gizzard shad. At the Neal Shoals Dam sampling station, the.least number of fish species (12) was collected during 1981 compared to previous years, when 19,14, and 16 species were collected during 1978, 1979, and 1980, respectively. The species that were most common during 1981 included the sunfish and gizzard shad.
The groups that have a small population do not appear in the collections every year and X
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include some of the suckers, catfish, including the bullheads, and I
perch. Age and growth studies indicated that five year classes of gizzard shad and four year classes of bluegill were found. Growth of both species was somewhat slower when compared to historical data froa I
similar habitats. Standing crop estimetes from the Neal Shoals Dam area decreased slightly from the previous year. The most abundant species collected was the largemouth bass which comprised more than 63 percent of the collection. In the subimpoundment, the species composi-tion has been identical for the past three years. This consistency in the species composition throughout the years may be attributed to the subimpoundment being a closed system and to the management practices I
being employed by SCE6G. Bluegill was the most abundant species col-1ected and the brown bullhead was next in total numbers collected.
Gizzard shad are becoming more abundant every year in the subimpound-ment.
In addition, those individuals that are collected are much larger than from the other collecting areas. These larger individuals may be af fecting population densities by being capable of producing i
it. ore eggs. The larger size of *.hese shad are attributed to the low population density, with reduced intraspecific competition, and the greater density of algae present in the subimpoundment. Age and growth studies indicated that four year classes of the gizzard shad and five year classes of the brown bullhead occurred. Growth of the brown bull-head was similar in the subimpoundment to that found in other compar-able habitats. Growth of the bluegill in this reservoir was somewhat slower when compared to historical data.
In Monticello Reservoir, the l
fish community was dominated by the sunfishes and gizzard shad, with a total of thirty species being collected during 1981; this is comparable l
to the previous years when 25, 31, and 27 species were collected in 1980, 1979, and 1978, respectively. Nine species of sunfish were iden-tified with bluegill being the most abundant. Gizzard shad was second l
in numerical abundance. The spottail shiner was collected for the l
first time in the study area. This species is common in parts of South l
Carolina, and has been recorded from the Broad River watershed. During 1981 no gar were collected from Monticello Reservoir, although they 1
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I have been collected during previous years; their absence during 1981 indicates that their numbers are decreasing in this reservoir. Age and growth studies determined that four year classes of bluegill and g
gizzard shad were found in the reservoir and that growth of both W.
species was slower than other population 3 in similar habitats.
The results of the avian surveys indicated that the bird populations along the control and test auto survey routes were high in both density and diversity. Although the test route showed approximately the same number of birds for the 1980 and 1981 surveys (1980, 8.9 birds; 1981 I
8.4 birds), the avian density was slightly greater than in most previous years (mean of 8.0 birds). The game birds, exemplified by bobwhite, were found to be at levels similar to previous years. The i
bobwhite population tends to be more sedentary than mourning doves and thus sampling results are not as influenced by flocks moving into the area during the survey as are the results for the mourning dove count.
The avian surveys also identified two immature bald eagles in 1981:
I eagles have been sighted during the previous three years.
It is possible that these immature birds could form a breeding pair in future years. The wide expanse of water offered by Monticello Reservoir and the abundant fish life present make this an ideal habitat for the eagles.
I The waterfowl survey indicated that Monticello Reservoir is an impor-tant sanctuary for ducks and other aquatic bird species. During the peak of the migrating season (fall and winter), waterfowl were abundant in Parr Reservoir. Mallards, black ducks and blue-winged teal were the I
most common species. During the summer months few resident species were observed. The wood duck is the only resident duck that breeds here regularly, although mallards will occasionally occur in this region. However, wood ducks have not been abundant here since the reservoirs were constructed. They bred in the flooded portions of Monticello Reservoir before it was completely filled, and a pair of I
wood ducks was observed in Parr Reservoir during the summer of 1979.
It appears that the fluctuating water levels in the reservoirs is I
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I disturbing to this species, so that wood ducks have probably moved to more stable areas of the Broad River.
I The interpretation of the 1981 aerial photographs indicated that there was no discernable evidence of decline or change in tree vigor in the site vicinity. The only land use changes noted during 1981 were areas of clear cutting for timber removal on private land.
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TABLE OF CONTENTS I
Section Page I
SUMMARY
i LIST OF TABLES xvi LIST OF FIGURES.
xviii
1.0 INTRODUCTION
1.0-1 2.0 AQUATIC SURVEY.
2.1-1 2.1 SAMPLING LOCATIONS AND FREQUENCY 2.1-1 2.2 WATER QUALITY.
2.2-1 5
2.2.1 Introduction.
2.2-1 2.2.2 Findings and Discussion 2.2-1 1
2.2.3 Summary 2.2-13 2.3 VASCULAR HYDROPHYTES 2.3-1
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2.3.1 Introduction.
2.3-1 2.3.2 Findings 2.3-2 2.3.2.1 Parr Reservoir 2.3-3 5
2.3.2.2 Neal Shoala Dam.
2.3-4 2.3.2.3 Subimpoundment 2.3-4 2.3.2.4 Monticello Reservoir 2.3-5 2.3.3 Discussion.
2.3-5 2.3.4 Summary 2.3-7 2.4 PHYTOPLANKTON.
2.4-1 2.4.1 Introduction.
2.4-1 2.4.2 Findings and Discussions 2.4-1 1
2.4.3 Summary 2.4-9 2.5 ZOOPLANKTON.
2.5-1 2.5.1 ' Introduction.
2.5-1 2.5.2 Findings and Discussion 2.5-1 I
2.5.3 Summary 2.5-7 2.6 ICHTHYOPLANKTON.
2.6-1 I
2.6.1 Introduction.
2.6-1 2.6.2 Findings.
2.6-2 2.6.3 Discussion.
2.6-6 5
2.6.4 Summary 2.6-9 8
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I TABLE OF CONTENTS (Continued) 1 i
Section Page 2.7 BENTH0S.
2.7-1 2.7.1 Introduction.
2.7-1 2.7.2 Findings 2.7-2 I
2.7.3 Discussion.
2.7-8 2.7.4 Summary 2.7-10 2.8 FISH 2.8-1 2.8.1 Introduction.
2.8-1 2.8.2 Findings and Discussion.
2.8-2 2.8.3 Summary 2.8-10 3.0 TERRESTRIAL SURVEY.
3.1-1 3.1 PHOTOGRAMMETRIC ANALYSIS OF THE BROAD RIVER /
f MONTICELLO RESERVOIR STUDY AREA.
3.1-1 3.2 BIRDS.
3.2-1 3.2.1 Avian Auto Survey 3.2-1 I..
3.2.1.1 Introduction 3.2-1 3.2.1.2 Findings and Discussion.
3.2-1 3.2.2 Waterfowl Survey.
3.2-3 3.2.2.1 Introduction 3.2-3 3.2.2.2 Findings and Discussion.
3.2-3 3.2.3 Strip Census.
3.2-5 3.2.3.1 Introduction 3.2-5 3.2.3.2 Findings and Discussion.
3.2-5 3.2.4 Unusual Observations 3.2-7 3.2.5 Summary 3.2-7
4.0 REFERENCES
4.0-1 APPENDIX A A-1 I
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LIST OF TABLES Table Page i
2.2.1 Physical measurements (temperature, dissolved oxygen, pH, conductivity, Secchi disc) made during the month indicated.
Bottom depth and approximate depth of thermocline are also given.
2.2-15 2.2.2 Annual summary of the results of chemical analysis of water samples taken at the station I
indicated during the period of January through December 1981.
2.2-27 I
2.2.3 Summary of data taken from the USGS monitoring station at the Fairfield Pumped Storage Facility intake in Monticello Reservoir for the period i
January through December 1981.
2.2-36
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I 2.3.1 Vascular hydrophytes found during shoreline surveys j
of Parr and Monticello Reservoirs, Neal Shoals Dam, and the subimpoundment, 1981.
2.3-8 2.3.2 Dominant vegetation,' relative fish and wildlife value, expected succession, and probable major I.
limiting factors of the littoral communities of the water bodies in the study area, 1981.
2.3-12 I
2.4.1 Density, blomass, number of taxa, and taxonomic diversity of phytoplankton collected during 1981 at Parr Reservoir, Neal Shoals Dam, Monticello Reservoir, and the subimpoundment.
2.4-12 2.5.1 Zooplankton collected in January, April, July, and October 1981, represented by numbers of organisms I
per major taxonomic category, species diversity, and biomass.
2.5-!
I-3 2.6.1 Mean monthly densities of larval fish (number /100m )
collected in net tows, March through September 1981.
2.6-11 B
2.7.1 Summary of benthic macroinvertebrate data cdiected from twelve stations during the 1981 monitoring program.
2.7-12 8
2.7.2 Summary of mean annual values for benthic macro-invertebrates obtained during the 1981 monitoring program.
2.7-16 xvi t
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LIST OF TABLES (Continued)
Table Page i
2.8.1 Number of fish and their percent abundance (%),
collected by electrofisher and gill nets during the 1981 sampling program.
2.8-12 2.8.2 Fish species collected in 1978, 1979, 1980, and 1981.
2.8-15 2.8.3 Standing crop (kg/ha) estimates of fishes from Parr and Monticello Reservoirs and the Neal Shoals Dam, 1981.
2.8-17 3.2.1 Birds observed during the auto survey - Summer 1981 3.2-10 3.2.2 Birds observed during the auto survey - Winter 1981 3.2-12
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3.2.3 Results of the 1981 waterfowl surveys.
3.2-13 1
3.2.4 Results of avian strip census conducted in different habitats on test sites during winter and summer of 1981.
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3.2.5 Results of avian strip census conducted in different habitats on control sites during winter and summer I
of 1981.
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LIST OF FIGURES Figure Page 2.1.1 Sampling Stations for the Aquatic Monitoring Programs.
2.1-2 2.1.2 Environmental Sampling Program, January through 2.1-3 December 1981.
3.1.1 Land Modification in Study Area from 1980 to 1981.
3.1-2 3.2.1 Terrestrial sampling locations and survey routes.
3.2-16 3.2.2 Average number of birds recorded on summer avian survey routes.
3.2-17 3.2.3 comparison of game bird call counts on avian survey routes.
3.2-18 i
3.2.4 Avian Density in Selected Habitats During Strip Censuses.
3.2-19 f
I 3.2.5 Avian Diversity in Selected Habitats During Strip Censuses.
3.2-20 I
I I
I I
I I
l8 3
xviii 5
I 5
1.0 INTRODUCTION
The present environmental monitoring program commenced in June 1978.
I At that time surface water and aquatic biological data were first col-lected on Monticello Reservoir, the subimpoundment, and at Neal Shoals Dam; aquatic biological and surface water data had been collected on Parr Reservoir for a number of years prior to 1978. Terrestrial bio-logical data had also been collected in the site vicinity prior to 1978.
I This report contains the results of the aquatic and terrestrial data collected for the Environmental Monitoring Program. The results of the surface water quality program include data taken by NUS Corporation; k
the biological data were collected by Dames & Moore. The reporting l
l period for the surface water quality, the aquatic data, and the ter-restrial data presented herein is for the year 1981; the data collected during 1981 are compared with earlier data where applicable. The purpose of the environmental monitoring program is twofold:
- 1) to establish baseline conditions on Monticello Reservoir paior to the operation of the VCSNS, and 2) to determine what impacts, if any, are I
occurring to the biota in Parr and Monticello Reservoir as a result of
(
operating the FPSF. A detailed description of the history of the reservoirs, collecting stations, and other pertinent information may be found in Section 1 of the Environmental Monitoring Report, June through December 1978 (Dames & Moore, 1978).
I I
8 I
l2 1.0-1
I I
2.0 AQUATIC SURVEY I
2.1 SAMPLING LOCATIONS AND FREQUENCY The sampling locations were documented in the 1978 Biologic.1 Monitor-ing Report (Dames & Moore, 1978). The stations sampled during January through December 1981 are identical to those reported in 1978 and are ident'fied on Figure 2.1.1.
The biological and surface water quality information has been collected from four major areas, including: Parr Reservoir, Neal Shoals Dam, the subimpoundment, and Monticello Reser-I During the quarterly sampling programs (January, April, July, voir.
and October), all stations and all components of the aquatic ecosystem were sampled, including:
phytoplankton, vascular hydrophytes, zoo-k plankton, ichthyoplankton, benthic macroinvertebrates, and adult fish.
I In addition, the quarterly scope of work for the surface water quality program was carried out.
During the monthly sampling program (January through December) phytoplankton were sampled at six locations in Mon-ticello Reservoir, the surface water quality program was carried out, and ichthyoplankton were sampled according to the established schedule.
Sampling for adult fish, in addition to the regularly scheduled quar-I terly program, occurred at Stations I and M in Monticello Reservoir, three weeks prior to and three weeks after s.e regularly scheduled spring sampling in April. A summary of biological and surface water collecting activities is shown in Figure 2.1.2.
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Environmental Sampling Program, January Through December 1981.
I
I I
2.2 WATER QUALITY I
2.2.1 Introduction Water quality samples and physical measurements were obtained once a month at a series o'. >. ions in the Broad River, Parr Reservoir, and Monticello Reservoir from January 1981 through December 1981 as part of the Summer /Fairfield Environmental Monitoring Program Water Quality I
study.
The Water Quality study was designed to determine the baseline condi-tions on Monticello Reservoir prior to the operation of the VCSNS and to determine what changes, if any, are occurring in Parr and Monticello Reservoirs as a result of operating the FPSF. These data will also be used to determine if the existing water quality in the river and reser-voirs meets the standards set by the South Carolina Department of Health and Environmental Control (SCDHEC) as well as the criteria sug-gested by the United States Environmental Protection Agency (USEPA).
- I The information may also be usefel in defining the cause of any changes that might occur in the communities of aquatic organisms.
2.2.2 Findings and Discussion 8
A summary of the results of temperature, dissolved oxygen, pH, con-ductivity, and transparency (Secchi disc) measurements are given by I
station and month in Table 2.2.1; bottom depth and approximate location of the thermocline are also indicated in this table. Results of the water quality chemical analyses are shown in Table 2.2.2.
A summary of data (water temperature, pH, dissolved oxygen, and conductivity) recorded on the United States Geological Survey (USGS) continuous water quality monitor located at the FPSF intake on Monticello Reservoir is 8
presented in Table 2.2.3.
t 8
2.2-1
I l
Parr Reservoir and Broad River Physical Measurements - During the 12-month sampling period, water I
temperatures in the Parr Reservoir and the Broad River (Stations 1, 2, 2W, 5A) ranged from 0.6*C at the bottom of Station 1 in January to 31.7'C in July at the surface of Station 1.
Analysis of the data revealed a normal seasonal temperature pattern with the coldest water temperatures occurring during January and February and generally increasing temperatures through July followed by a decline to the low winter values. All temperatures taken at these stations were below the 5
maximum standard of 32.2*C set by the SCDHEC (1977). No seasonal thermocline was observed at any of the stations sampled due to the shallow depths and high current velocity.
I Dissolved oxygen (DO) concentrations also followed the expected seasonal trends, with higher levels generally occurring during the colder months and lower levels occurring during warmer periods. The maximum value was 14.1 mg/ liter, recorded at Station 1 in January. The minimum concentration, recorded at the bottom of Station 2 in August, was 4.6 mg/ liter. Most DO values fell within a range of 6.0 to 11.0 mg/ liter. The SCDHEC standard for dissolved oxygen is 4.0 mg/ liter.
The pH values at Stations 1, 2, 2W, and SA ranged from 6.2 to 8.0 units. The minimum pH value was recorded at Station 2 in June. The maximum value occurred at Station 2W in January and February. All values were within the range of 6.0 to 8.5 units set by the SCDHEC (1977).
Conductivity values ranged from 65 pmhos/cm at Station 5A in July to 160 pmhos/cm at Station 1 in October.
Transparency, as measured with a Secchi disc, was lowest (0.1 m) at Station 1 in June.
This low value resulted from a high concentration 8
of suspended materials present in the water column that was probably caused by heavy rainfall and runoff during the period preceeding sampling. The highest transparency value was 1.9 meters recorded at LB.
2.2-2
I I
Station 2 in November. Transparency values at all Broad River and Parr Reservoir stations were lowest from June through September which is thought to be attributable to the higher precipitation level occurring I
during this period.
In general, physical values recorded between January 1981 through December 1981 at the Parr Reservoir and Broad River Stations are con-sistent with historical data collected under the present environmental monitoring program (Dames & Moore; 1978, 1979, 1979a, 1981). Water temperature and dissolved oxygen values conformed to the expected seasonal regime with low water temperatures and high dissolved oxygen concentrations recorded curing the winter, and maximum water tempera-tures and minimum DO values occurring during the summer months. The pH I
values recorded during 1981 were within the range of historical values (6.2 to 8.5 units). The range of conductivity values was slightly higher during 1981 (65-100 pmhos/cm) than occurred in 1980 (50-100 umhos/cm) and in 1979 (30-100 pmhos/cm). The range of transparency values recorded during this collection period was similar to that occurring in 1980.
5 Chemical Analyses - Ammonia values at Stations 1, 2, and SA averaged 0.3 mg/ liter. A maximum ammonia concentration of 0.6 mg/ liter was observed at Station 1 in June. Mean nitrate concentrations varied from 1.7 mg/ liter at Station SA to 2.2 mg/ liter at Station 1.
The maximum nitrate value recorded was 2.9 mg/ liter at Station 2 in March. Average total phosphate concencrations ranged from 0.11 to 0.27 mg/ liter with a minimum value of less than 0.01 mg/ liter at all three stations in June LW and a maximum of 0.57 mg/ liter at Station 2 in July. Ammonia levels in l
the Broad River and Parr Reservoir are slightly less than those reported during 1980. Average nitrate and phosphate concentrations were similar to values reported in 1980.
I Biochemical and chemical oxygen demands (BOD and COD) were generally B
low at all Broad River and Parr Reservoir stations; the BOD averaged 1.3 mg/ liter at these stations, and the COD ranged from a mean of 2.2-3 1
I I
5.0 mg/ liter at Station 2 to 7.3 mg/ liter at Station 1.
An individual high reading of 21 mg/ liter was recorded at Station 1.
The BOD and COD I
values for 1981 are generally similar to those recorded during 1980'.
The average mean value for total hardness recorded at Stations 1, 2, and SA was 16.8 mg/ liter; this value falls within the 0 to 75 mg/ liter criterion defining sof water (USEPA, 1976). Hardness levels recorded from January through December 1981 are similar to levels which have 5
occurred since June 1978.
Cadmium, chromium, lead, and mercury were detected in water samples collected from Parr Reservoir and the Broad River but occurred in con-centrations at or below the sensitivity of the analytical procedures (i.e., they were present in concentrations too low to be adequately quantified). Copper concentrations of 0.03 mg/ liter were recorded at I
Station SA during July. However, this value is below the criterion (maximum of 0.1 times a 96-hour LC-50 as determined for a sensitive, resident aquatic specie's) recommended by the USEPA (1976). Using this criterion as determined from toxicity data for bluegill in sof t water (Pickering and Henderson, 1966), a maximum permissible value of 0.06 mg/ liter copper would apply.
Concentrations of zine in excess of the analytical limit were recorded at one or more of the river and Parr Reservoir stations during Feb-ruary, June, October, and November. However, in only one case (Station I
2, October: 0.16 mg/ liter zine), did the reported value exceed the 0.05 mg/ liter criterion (maximum of 0.01 times the 96-hour LC-50 for bluegill in soft water, as per Pickering and Henderson, 1966) recom-mended by the USEPA (1976).
The USEPA criterion for tota' iron is 1.0 mg/ liter. The mean concen-I tration of iron exceeded this value at Station 1.
The highest iron value recorded at Station 1 was 9.3 mg/ liter in June.
The concen-tration of iron at Station 1 also exceeded the criterion in August (2.8 mg/ liter), September (1.1 mg/ liter), and December (2.4 mg/ liter).
At Station 2, values exceeded the criterion in July (2.4 mg/ liter) and 2.2-4 S
I I
September (1.2 mg/ liter). At Station 5A, values exceeded the limit in June (1.1 mg/ liter) and August (1.6 mg/ liter).
In several cases, the I
high iron concentrations were coincidental with high suspended solids values. Because iron is a prime constituent of clay soils, such as those found in the study area, it is believed that these values were caused by runoff from heavy rainfall preceeding sampling. The other metals values that exceeded the recommended criteria are also believed to be due to leaching from the soil and are not considered unusual for the study area.
Daily observations were made of surface waters at Station SA for the presence of oil and grease and odor. On May 19, July 5 and 9, and August 31, 1981, " trace" amounts of both oil / grease and odor were reported.
I Neal Shoals Dam Physical Measurements - Because of the shallow water depth (approx-imately 1 meter) at this station (11) temperature records at the surface and bottom generally were similar and no thermocline was observed. Normal seasonal fluctuations in water temperature occurred.
The minimum temperature, (0.6*C) was recorded in January and the max-imum (32.4*C) in July. This value was the only recorded instance during the 1981 sampling period when the maximum permissible water temperature of 32.2*C, set by the SCDHEC (1977), was exceeded.
Dissolved oxygen concentrations varied from 14.2 mg/ liter in January to 4.9 mg/ liter in August. These values are above the minimum value of 4.0 mg/ liter established by the SCDHEC (1977).
Values of pH ranged from 6.7 (August) to 8.2 (July) units. These 5
values are within the SCDHEC (1977) standards of 6.0 to 8.5 units.
Conductivity values ranged between 80 (which was recorded several ti' es m
during the year) and 130 (October) pmhos/cm. Secchi disc readings ranged from 0.1 to 1.1 meters, in September and March. respectively.
2.2-5 1
I I
Chemical Analyses - Mean concentrations of ammonia, nitrate, and total phosphate were 0.3 mg/ liter, 1.8 mg/ liter, and 0.28 mg/ liter, respec-tively. During July the concentration of un-ionized ammonia (0.6 mg/ liter) exceeded the criterion recommended by the USEPA (1976). The criterion suggested for ammonia is based on the amount of un-ionized ammonia (NH3) present in solution, which is highly dependent on the temperature and pH of the water body being sampled. Although the concentrations of total ammonia (NH3 + NH4) were within the range I
normally occurring in the river, the high pH values recorded at the surface resulted in a greater percentage of the total ammonia being in the un-ionized form. The un-ionized ammonia concentration recorded at Neal Shoals is not considered unusual because the temperature, pH, and total ammonia vs. lues were within the ranges expected under natural k
conditions. Mean nutrient values at Neal Shoals have varied only slightly since 1978. The average ammonia concentration during 1981 was slightly less than occurred during 1980. Average ammonia values varied previously at this station from 0.3 to 0.4 mg/ liter, mean nitrate values have varied from 1.8 to 2.2 mg/ liter, and average phosphate I
values have varied from 0.30 to 0.39 mg/ liter (Dames & Moore; 1978, 1979a, 1979b, 1981).
The mean BOD and COD values recorded during 1981 were 1.5 mg/ liter and 8.5 mg/ liter, respectively. The average total hardness level was 17.3 mg/ liter, a value characterizing. soft water (USEPA, 1977). The BOD and I
hardness levels are similar to those reported in the earlier surveys while COD values were somewhat higher than previously re. ported (Dames &
Kaore 1978, 1979a, 1979b, 1981).
Of the metals which occurred in detectable concentrations, only iron occurred in amounts greater than the criterion recommended by the USEPA (1976). The average iron concentration at Neal Shoals Dam was 1.4 I
mg/ liter. The maximum iron value recorded was 4.7 mg/ liter which occurred during June. The maximum iron value was coincidental with a moderately high suspended solids load in the river. The recommended 2.2-6 5
I I
criterion for iron was also exceeded at Station 11 during August (2.0 mg/ liter), September (2.3 mg/ liter), October (1.6 mg/ liter), and Decem-I ber (2.0 mg/ liter). Previous studies have indicated that iron concen-trations in the vicinity of Neal Shoals Dam are often greater than that recommended by the USEPA (Dame = & Moore; 1978, 1979, 1981). As with the other stations located in the river and in Parr Reservoir, the elevated concentrations are believed to have resulted from leaching of iron from che soils in the region.
Subimpoundment Physical Measurements - Water temperatures in the subimpoundment (Station 18) ranged from a low of 5.8'C on the surface in January to 30.3*C in July. The bottom temperature ranged from 5.0*C in January to 24.2*C in July. The results from these surveys indicate that the tem-peratures were within the range expected for the seasons encountered.
The dissolved oxygen (DO) concentrations ranged from a low of 6.7 3
mg/ liter at the surface in June to 13.3 mg/ liter in May. At 'the bottom the DO values ranged from a low of 5.7 mg/ liter in October to 10.0 mg/ liter in January; all of the values were above the prescribed limit established by the SCDHEC.
5 The pH was measured only at the surface at this station. The values I
for pH ranged from 6.3 to 9.5 and these were recorded during November and May, respectively. The pH limits established by the SCDHEC are a low of 6.0 and a high of 8.5.
The high pH value recorded in May may have been caused by an algal bloom; no phytoplankton data are collected at this station in May but fertilization of the subimpoundment occurs during this month and a bloom in plankton could have caused a shift in the pH.
I B
2.2-7 I
I I
Conductivity values recorded at the surface range from 60 umhos/cm in February to 119 pmhos/cm in May.
Measurements made at the bottom ranged from a low of 66 pmhos/cm in January to 116 pmhos/cm in I
October.
The transparency values recorded ranged from 0.9 m in May to 2.1 m in March.
All of the physical measurements made during this reporting period appeared to follow seasonal trends for the area, and, except for the I
high pH value in May, fall within the prescribed limits established by the SCDHEC.
Chemical Analyses - The subimpoundment was sampled on a quarterly basis in January, April, July, and October. Ammonia concentrations from the four sampling periods ranged from 0.2 to 0.6 mg/ liter. During April, because of high pH (8.9) occurring at Station 18, the concentration of ammonia (0.5 mg/ liter) exceeded the criterion, based on the amount of un-ionized ammonia present in solution recommended by the USEPA (1976).
Values for nitrate ranged from below detectable limits to 2.6 mg/ liter I
during 1981. The concentrations of total phosphate varied from 0.05 to 0.11 mg/ liter. The maximum and average ammonia concentrations were lower than occurred during 1980 but were similar to those recorded for other years at this station (Dames & Moore; 1978, 1979a, 1979b, and 1981). Nitrate and phosphate concentrations were similar to those reported for 1980.
r t
(
BOD values during the four sampling periods ranged from less than 1 mg/ liter to 3 mg/ liter. Total hardness values ranged from 26 to 28 mg/ liter and were within the range characteristic of soft water; however, the values were higher than those which occurred at the other sampling stations in Monticello and Parr Reservoirs as well as in the Broad River.
l 3
2.2-8 l
I As with the 1979 and 1980 surveys, all concentrations of metals I
measured during the current reporting period were below the level of sensitivity of the analytical procedures.
I, Monticello Reservoir Physical Measurements - All of the temperatures recorded in the Monticello Reservoir (Stations 12 through 17, and 20) were below the 32.2*C maximum limit for Class B waters set by the SCDHEC (1977). The highest temperatures recorded in the Monticello Reservoir were 29.l*C at the surface of Station 14 in July and 29.3*C at Station 17 in August. The lowest temperatures recorded were 5.4*C at the bottom of Station 12 in January, and 5.5 at Stations 13, 14, and 15 in February.
I The water temperatures taken above the thermocline followed the typical seasonal patt.arn.
Water temperatures were generally highest in July and August and lowest in January and February. During the time that a thermocline was present, the water temperatures below the thermocline were from about 5 to 14*C cooler than those in the epilimnion.
A thermocline was obsersed at Station 20 from July through October.
5 In July, it was located at depths between 26 and 29 meters, in August at depths between 27 and 29 meters, in September between 26 and 30 meters, and in October between 29 and 31 meters. The temperatures across the thermocline decreased by between 7.5*C and 11.0*C.
The I
location of the thermocline during 1981 is generally consistent with those recorded at this station during previous surveys (Dames & Moore; i
1978, 1979a, 1979b, 1981). During April at Station 20, thermal strati-t fication was evident between the depths of 9 and 10 meters. Water temperatures decreased from 17.9 to 14.9'C between these depths.
Sta-tion 12 is located in front of the FPSF intake and is approximately 30 meters in depth.
In spite of the depth at this station, April was I
the only month when there was any evidence of water column stratifica-tion when water temperatures decreased from 15.6 to 13.6*C between 9 B
and 10 meters depth. Stratification was also evident during April at t
I 2.2-9
1
\\
R Station 16 between 1 and 2 meters depth where water temperatures de-creased from 16.9 to 14.9.*C.
During January, February, November, and December the difference between I
surface and bottom temperatures at all stations in the reservoir was less than 2*C.
Mean temperature ranges recorded in 1981 by the USGS monitor located at the FPSF intake are generally similar to the temperature ranges measured at other stations in the reservoir during this study. No I
recorded values exceeded the limit set by the SCDHEC (1977).
Dissolved oxygen concentrations recorded at the surface (30 cm) of the Monticello Reservoir ranged between 5.0 mg/ liter and 12.9 mg/ liter.
The maximum surface DO concentration occurred at Station 13 in February. The minimum surface DO level was recorded at Station 13 in August. All surface values were greater than the 4.0 mg/ liter standard set by the SCDHEC (1977).
Dissolved oxygen concentrations near the bottom of Monticello Reservoir I
ranged from 12.9 mg/ liter at Stations 12 and 13 in February to very low values at Station 20 in August (0.2 mg/ liter), September (0.0 mg/ liter),
and October (0.4 mg/ liter). The DO levels near the bottom were below I
the SCDHEC standard at Station 20 during the months of June through November. Values below the standard were also recorded near the bottom at Station 12 in July, at Stations 12, 14, 16, and 17 in August, and at Stations 14, 16, and 17 in September. Low oxygen concentrations are l
l considered typical of waters below the thermocline in deep fresh water ponds or lakes (Knight, 1965). This vertical stratification is believed to be the reason fot the depressed oxygen levels at Station 20 during the warm season.
g.
the USGS Monitor (sampling depth approximately 6 m) the daily mean At DO values during the warm season were below the state standard (minimum 3
2.2-10 Li
of 4 mg/ liter) on three dates: August 5 and 6, and September 11.
Daily mean values ranged from 3.9 to 7.8 mg/ liter during August and from 3.5 to 7.8 mg/ liter during September. A minimum hourly value of 3.0 mg/ liter was recorded in September.
8-The pH standards for Class B waters, as set by the State of South Carolina (SCDHEC, 1977), range from 6.0 to 8.5 units. The pH values recorded in the Monticello Reservoir during 1981 ranged from a minimum I
of 2.8 units at the bottom of Station 20 in July to a maximum of 9.3 units at the surface of Station 20 in April. The pH values also were below the minimum state standard at the bottom of Station 12 in January I
and at the bottom of Station 20 in January, June, July, and September.
Low pH values such as these are not considered unusual near the bottom of reservoirs that are stratified due primarily to the decomposition of l
organic material on the bottom. The maximum permissible pH value was exceeded in the photic zone at Stations 12,16, and 17 in April and at Stations 16 and 17 in June.
These high values are considered to be I
the result of the photosynthetic activity of phytoplankton. Photo-synthesis removes carbon dioxide during daylight periods, shifting the system away from the production of carbonic acid and, consequently, to a less acidic state. This is especially true of soft water areas with low buffering capacity (such as Monticello Reservoir) where wide flue-tuations in seasonal and daily pH values may be expected (Knight, 1965).
I The daily, mean pH values recorded at the USGS Monitor in Monticello Reservoir ranged from 6.5 units in July to 7.8 units in April and May.
The minimum hourly value recorded was 6.3 units and the maximum was 9.0 units. These values appear to be consistent with those recorded during the Water Quality Monitoring Study.
1 Conductivity values in Monticello Reservoir ranged from 60 umhos/cm at I
Station 16 in August to 200 pmhos/cm at Station 20 in April. Most conductivity values recorded were between 80 and 100 pmhos/cm. Daily 8
2.2-11 I
n
,-n
_g
mean conductivity values recorded at the USGS monitoring station in I
Monticello Reservoir ranged from 60 pmhos/cm in February to 95 pmhos/cm in September.
Water transparency measurements in the Monticello Reservoir ranged from a minimum of 0.4 m at Station 13 in June to a maximum of 2.0 m recorded at Station 17 in March.
Physical measurements taken in the Monticello Reservoir since June 1978 reveal seasonal patterns that are typical of deep freshwater lakes and ponds. Vertical temperature stratification occurs during the summer I
months while the reservoir is essentially isothermal in the winter.
Dissolved oxygen levels have been generally highest during the winter months and lowest in the summer. The depressed DO values that have occurred in water below the thermocline are considered normal for water bodies of this type. High pH values can be expected in the photic zone
. luring periods of high phytoplankton activity. Specific conductance I
has remained at a relatively low level throughout the study.
Chemical Analyses - Average ammonia values in the Monticello Reservoir ranged from 0.28 mg/ liter at Station 15 to 0.32 mg/ liter at Station 16.
A maximum ammonia concentration of 0.50 mg/ liter was recorded at Stations 12 (April, May, June), 14 (April), and 16 (January, April).
Mean nitrate and total phosphate levels were within the narrow ranges l
of 1.1 to 1.4 mg/ liter and 0.09 to 0.13 mg/ liter, respectively, at the LT' sampling stations in the reservoir. Ammonia and r.itrate concentrations were lower during 1981 than occurred during 1980. Total phosphate g8 concentrations were slightly higher than occurred in 1980 (Dames &
Moore, 1981).
In April, because of high pH values also occurring at Stations 12, 14, and 16, the concentrations of ammonia exceeded the criterion (based on the amount of un-ionized ammonia present in solu-tion) recommended by the USEPA (1976).
In July, because of high pH and iw water temperature values, the relatively low concentration of ammonia i
(0.20 mg/ liter) at Station 14 also resulted in un-ionized NH3 values 2.2-12
I that exceeded the criterion. Although the concentrations of total I
ammonia (NH3 + NH4) were within the range normally occurring in the reservoir, the high pH values recorded at the surface resulted in a greater percentage of the total ammonia being in the un-ionized form.
I The un-ionized ammonia concentrations recorded from the reservoir are not considered unusual because the pH, water temperature, and total ammonia values were within the ranges expected in the reservoir under natural conditions.
I Biochemical and chemical oxygen demands were low, as they were during the 1978, 1979, and 1980 study periods (Dames & Moore; 1978, 1979a, I
1979b, 1981). BOD values averaged between 1.2 and 1.3 mg/ liter. The range of mean COD levels was between 5.5 and 6.2 mg/ liter. Total hardness values ranged from a maximum of 21 mg/ liter to a minimum of 10 mg/ liter; these values are characteristic of soft water.
Of the metals measured during 1981 in Monticello Reservoir, only iron and zine occurred in detectable concentrations. However, concentra-I tions of these metals did not exceed USEPA recommended criteria. Mean total iron values ranged from 0.20 to 0.36 mg/ liter with a maximum con-centration recorded of 0.56 mg/ liter at Station 14 in March. Zine values averaged 0.01 mg/ liter at all of the reservoir stations with a maximum concentration of 0.04 mg/ liter occurring at Station 14 in January.
Iron and zinc are natural constituents of the clay soils in
!g l
the area; therefore, periodic increases in their concentrations are not LW considered unusual. All of the other metals have remained at low l
l levels throughout the 1978-1981 studies.
2.2.3 Summary With one exception, water temperatures recorded during the 1981 water i
quality monitoring program were below the 32.2*C standard set by the W
SCDHEC (1977). The single occurrence of water temperature exceeding the standard was at the shallow (1 m) Neal Shoals station during July.
2.2-13 3
I Dissolved oxygen concentrations in the Parr Reservoir and the Broad i
I River exceeded the minimum state standard. However, in Monticello Reservoir the DO was somewhat reduced from June to September with concentrations below the standard of 4.0 mg/ liter occurring near the bottom of several sampling stations. The USGS monitor in the FPSF intake indicated that, on rare occasions during this period, the daily mean DO level was below the minimum standard.
I The maximum state standard of 8.5 for pH was exceeded in the photic zone of the Monticello Reservoir during the spring and summer months.
These high values are attributed to natural photosynthetic activity and I
are expected during the warmer seasons.
In several instances, pH values in bottom waters of the reservoir were below the standard.
i Because these values were recorded near the bottom, they are not con-sidered unusual. Transparencies in Monticello Reservoir were generally I
higher than in Parr Reservoir or in the Broad River; the reduced tur-bidity is thought to be due to the greater depth and lentic character-istic of the Monticello Reservoir. Biochemical and chemical oxygen I
demands were low at all stations throughout the reporting period.
Total hardness values at all stations conformed to the 0 to 75 mg/ liter criterion for soft water set by the USEPA (1976). Hardness values in the subimpoundment were higher than those recorded from the other water quality sampling stations. Mean nitrate concentrations were slightly greater in Parr Reservoir and the Broad River than in Monticello 3_
Reservoir. Average total phosphate values were higher at the Broad River stations than in the Parr or Monticello Reservoirs. Ammonia concentrations were similar at all stations. Zinc and iron were the only metals that occasionally exceeded the criteria suggested by the USEPA (1976). These metals are typical constituents of soils in the I
watershed and, therefore, the concentrations observed are not considered unusual.
I 3
1 2.2-14
EeMMM M
mM M
mmmammaeem T ble 2.2.1 Physical measurements (temperature, dissolved oxygen, pit, conductivity, Secchi disc) made during the month indicated. Bottom depth and approximate depth of thermocline are also given.
Page 1 of 12 January 1981 Temperature (*C)
Dissolved Oxygen pil Conductivity Approximate (mg/ liter)
(umhos /cm)
Thermocline Bottom Secchi Station Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 0.7 0.6 14.1
-a 7.6 7.3 70 70 NP 3.5 1.4 2
6.2 6.2 12.0
-a 7.8 7.5 90 90 NP 5
1.3 2W 4.4 4.4 12.8
-a 8.0 8.0 100 100 NP 5
0.9
-b 70
--b b
NP
<1 0.6 13.0
--b 7.7 5A 5.8 11 0.6 0.6 14.2 13.8 7.3 7.6 110 110 NP 1
1.0 12 5.8 5.4 12.3 12.2 7.5 3.4 70 80 NP 28 1.1 p
13 6.0 5.7 12.2 12.0 7.7 6.9 80 80 HP 12 1.2
{
14 6.2 6.0 11.8 11.7 7.6 6.6 70 70 NP 18 1.4 15 6.2 6.2 11.9 11.8 7.7 7.5 80 80 NP 3
1.4 16 6.5 6.4 12.0 11.9 7.6 7.0 70 80 NP 9.5 1.6 17 6.4 6.3 12.0 11.6 8.0 7.3 70 70 NP 11 1.2
-d 65 66
-d 11 1.6 18e 5.8 5.0 10.6 10.0 6.9 20 6.0 5.9 12.0 10.0 -
7.6 5.6 80 80 NP 31 1.2 NP - Not Present.
8 - Instrument malfunction b - Water depth less than Im; only surface measurements made.
c - Data collected by Dcmes & Moore during the aquatic biology sampling, d - Heasurement not required.
m EM E
e M
m e
M M
M M
mee
^
Tcble 2.2.1 (Continued)
Page 2 of 12 February 1981 Temperature (*C)
Dissolved Oxygen pH Conductivity Approximate (mg/ liter)
(pmhos/cm)
Thermocline Bottom Secchi Station Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 4.4 4.3 13.7 13.7 7.6 7.6 100 100 NP 2
1.3 2
5.5 5.5 12.5 12.5 7.6 7.7 90 90 NP 4.5 1.7 2W 5.3 5.4 12.7 12.9 8.0 6.9 100 100 NP 3
1.0 SA 6.2
-a 12.7
-a 6.7
-a 100
__a NP
<0.7 (btm) 0.7 11 4.8 4.8 12.7 12.7 7.8 7.8 100 100 NP 1
(btm) 1.0 12 5.5 5.6 12.7 12.9 7.6 7.5 90 100 NP 31 1.8
{
13 5.7 5.5 12.9 12.9 7.6 7.6 90 90 NP 13 1.0 h
14 5.8 5.5 12.8 12.8 7.6 7.6 90 90 NP 18 1.9 15 5.5 5.5 12.8 12.8 7.6 7.6 90 90 NP 4
1.9 16 5.7 5.7 12.7 12.7 7.5 7.6 80 80 NP 11 1.9 17 5.9 6.0 12.5 12.6 7.4 7.4 SO 80 NP 12 1.1 18b 8.0
-c 10,7
__c 6.7
-c 60
-c
__c 11 1.5 l
20 5.9 5.6 12.7 12.7 7.6 7.5 80 80 NP 30 1.8 l
i NP - Not Present.
a - Water depth less than Im; only surface measurements made.
l
- Data collected by Dames & Moore during the aquatic biology sampling.
b I
c - Heasurement not required, l
l
M' MMMM M
MM m
M M
MMM M
M M
~
Tchle 2.2.1 (Continued)
Page 3 of 12 March 1981 Temperature (*C)
Dissolved Oxygen pH Conductivity Approximate (mg/ liter)
(pmhos/cm)
Thermocline Bottom Secchi Stction Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 9.6 9.6 10.8 10.8 7.4 7.4 90 90 NP 2.5 1.2 2
10.0 8.9 11.2 11.2 7.4 7.2 80 90 NP 5
1.1 2W 11.2 11.0 10.6 10.6 7.5 7.5 90 90 NP 4
0.5 5A 11.1 a
11,1
_a 7.6
-a 90
__a NP 1
(btm) 1.0 11 9.7 9.6 10.8 10.7 7.4 7.4 80 80 HP 1.1 (btm) 1.1 12 10.3 6.6 11.2 10.3 7.6 7.1 90 90 NP 28 1.4 13 10.3 9.6 11.2 10.7 7.6 7.4 90 90 NP 12 1.2 q
14 10.4 9.2 11.2 10.4 7.7 7.4 90 90 NP 16 1.2 15 10.4 9.8 11.2 11.2 7.7 7.6 90 90 HP 3.5 1.5 16 10.4 8.4 11.1 10.0 7.7 7.4 90 90 NP 12 1.8 j
17 10.3 8.3 11.2 9.9 7.6 7.4 90 90 HP 12 2.0 l
18b 12.0
-c 10.9 c
7.2
-c 66
-c
__c 11 2.1 20 10.2 6.4 11.6 9.4 7.8 7.0 80 80 NP 31 1.4
~
NP - Not Present.
8 - Water depth less than im; only surface measurements made, b - Data collected by Dames & Moore during the aquatic biology sampling.
c - Measurement not required.
E EE M
E m
~
M M
M M
M M
M
~
~
T:ble 2.2.1 (Continued)
Page 4 of 12 April 1981 Temperature (*C)
Dissolved Oxygen pil Conductivity Approximate (mg/ liter)
(pmhos/cm)
'lhermocline Bottom Secchi Stction Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 20.9 20.9 8.0 8.0 7.2 7.2 90 90 NP 2
1.4 2
15.4 15.3 10.8 11.3 7.7 7.5 90 90 NP 5
1.0 2W 17.8 17.5 10.2 10.2 7.1 7.1 90 90 NP 3
0.8 5A 18.3
-a 10.2 a
7.8
-a 80
-a NP
<1 0.7 11 20.7 20.6 8.0 8.0 7.2 7.7 80 80 NP 1
0.9 12 17.7 11.0b 10.8 8.8b 9.2 7.2b 80 90b 9-10 28 1.4
,L 13 17.4 16.2 9.2 8.8 7.7 7.6 80 80 HP 12 0.9 14 16.3 15.9 10.3 9.9 8.3 8.0 80 80 NP 11 1.4 15 15.8 15.4 9.7 9.4 7.9 7.8 80 80 NP 5
1.4 16 17.2 13.2 9.7 8.7 8.6 7.2 80 80 1-2 15 1.3 l
l 17 15.2 13.7 9.2 7.8 7.4 7.1 80 80 NP 12 1.4 18c 20.0 17.5 10.9 9.5 8.9
-d 84 80 d
i1 g,$
20 18.2 9.3 10.7 6.0 9.3 6.2 90 200 9-10 32 1.6 NP - Not Present.
8 - Water depth less than Im; only surface measurements made.
b - Bottom measurements believed to be af fected by disturbed substrate; f
reported value made I m above bottom.
c - Data collected by Dames & Moore during the aquatic biology sampling.
d - Measurement not required.
E MM M
M M
M M
M m
m m
m m
a m
m im m
Tchle 2.2.1 (Continued)
Page 5 of 12 May 1981 Temperature (*C)
Dissolved Oxygen pil Conductivity Approximate (mg/ liter)
(u mhos /cm)
Thermocline Bottom Secch i Stetion Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 19.0 18.8 8.2 8.6 7.4 7.4 100 100 NP 2
1.2 1
2 20.1 18.3 7.6 7.5 7.0 7.0 90 90 HP 4.5 0.9 2W 18.8 18.4 7.8 7.7 7.2 7.2 90 90 NP 4
0.5 5A 20.0
-a 8.2 a
7.6 a
90
-a NP
<1 0.5 11 19.3 19.3 8.4 8.5 7.2 7.2 80 90 NP 1
0.7 12 19.4 15.3 9.4 6.6 7.6 7.0 90 90 NP 29 1.9 u
13 18.9 18.6 8.0 7.8 7.3 7.2 90 90 NP 13 1.1
- g g
14 19.6 18.0 9.1 7.6 7.5 7.2 90 90 NP 14 1.9 15 19.1 18.7 8.9 8.6 7.6 7.5 90 90 NP 5
1.3 16 19.4 18.4 9.3 7.5 7.8 7.3 90 90 NP 12 1.6 17 19.3 18.2 9.0 7.2 7.6 7.3 80 80 NP 11 1.1 18b 22.8
-c 13.3
-c 9.5
-c 119
-c
__c 11 0.9 20 19.3 10.3 9.6 4.6 7.6 6.2 90 90 HP 31 1.5 NP - Not Present.
8 - Water depth less than Im; only surface measurements made.
b - Data collected by Dames & Moore during the aquatic biology sampling.
c - Measurement not required.
M MMMM M
M MM M
M M
M M
M M
M M
Tchle 2.2.1 (Continued)
Page 6 of 12 June 1981 Temperature ('C)
Dissolved Oxygen pil_
Conductivity Approximate (mg/ liter)
(umhos/cm)
Thermocline Botton Secchi Station Surface * -tottom Surface Botton Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 25.3 25.4 6.8 7.3 7.1 7.2
, 90 90 NP 3
0.1 2
21.4 21.2 6.4 6.4 7.0 6.2 100 100 NP 4
0.6 2W 24.4 23.4 6.4 6.1 7.0 7.0 90 90 NP 2.5 0.2 SA 25.4 a
7.4 a
7,1
_a 100
__a NP
<1 0.4 11 25.1 24.7 6.1 6.1 7.0 7.0 00 90 NP 0.5 0.2 12 23.3 18.9 7.0 5.4 7.0 6.8 100 100 NP 29 0.5 13 23.0 22.6 6.5 6.2 7.0 7.0 100 100 NP 13 0.4 Yg 14 24.6 21.3 8.2 6.0 7.2 7.0 100 100 NP 18 0.9 15 25.7 25.7 8.5 8.5 8.1 8.0 100 100 NP 4
1.2 16 26.3 21.8 8.7 5.4 8.6,
6.9 100 100 5-7
.11 1.3 17 27.4 22.1 8.8 6.0 9.0 7.4 100 100 5-7 11
~
1.0 18b 29.0 c
6.7 c
8.0 C
102
-C c
g3 g,o 20 24.6 10.7 8.2 1.6 7.2 5.2 95 110 NP 32 0.9 NP - Not Present.
8 - Water depth less than Im; only surface measurements made, b - Date collected by Dames & Moore during the aquatic biology sampling.
C - Heasurement not required.
~ ~..
m
MEWW mmmmmm eee a
e m
e' m e
s Tchte 2.2.1 (Continued)
Page 7 of 12 July 1981 Temperature ('C)
Dissolved Oxygen pil Conductivity Approximate (mg/ liter)
(umhos/cm)
Thermocline Botton Secchi Stction Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (a)
Depth (m)
Disc (m) 1 31.7 30.8 7.1 6.7 7.2 7.3 90 80 NP 2
0.7 i
2 28.5 28.7 5.6 5.7 2.8 6.8 80 80 NP 3
0.4 2W 28.9 29.0 5.6 5.3 6.6 6.6 80 80 NP 2
0.3 5A 29.7
-a 5.2 a
7.3 a
65
-a NP
<1 0.6 11 32.4 31.3 10.2 7.2 8.2 7.4 80 80 NP 1
0.6 12 27.8 24.6 7.0 2.3 7.1 7.0 80 80 NP 29 1.0 13 27.5 26.6 6.1 4.8 6.9 6.9 80 90 HP 11 0.7 h
14 29.1 26.5 8.4 5.2 8.4 6.7 80 80 NP 15 1.5 15 28.0 26.9 7.6 5.4 7.2 7.0 80 80 NP 5
1.2 16 28.0 26.4 7.8 4.8 7.3 6.8 80 80 NP 11 1.4 17 28.2 26.4 8.2 5.4 7.8 7.0 70 80 NP 10 1.4 18b 30.3 24.2 8.0 5.8 7.8 c
106 101 c
11 1.6 20 27.9 12.0 7.4 1.3 7.2 2.8 90 70 26-29 31 1.3 NP - Not Present.
U - Water depth less than Im; only surface measurements made.
b - Data collected by Dames & Moore during the aquatic biology sampling.
c - Measurement not required.
~-
a
M M
M M
M M
M M
M M
M
'M M
M M
& -Q M
i T:ble 2.2.1 (Continued)
Page 8 of 12 August 1981 Temperature ('C)
Dissolved Oxygen pil Conductivity Approximate (mg/ liter)
(pmhos/cm)
Thermocline Bottom Secchi Stction Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 28.6 27.6 6.2 6.7 7.0 6.9 120 110 NP 2
0.3 2
26.8 26.8 4.8 4.6 6.7 6.6 110 100 NP 3
0.8 2W 27.8 27.5 5.0 4.9 6.4 6.3 85 85 NP 2
0.5 5A 27.8
-a 5.4
-a 7.0
-a 80
-a NP
<1 0.5 11 28.6 28.1 5.0 4.9 6.7 6.7 120 120 NP 1
0.3 12 27.0 25.7 5.7 3.0 6.6 6,
80 90 NP 28 1.0 w
13 27.0 27.0 5.0 4.9 6.4 6.3 80 75 NP 15 0.7 N
14 27.7 26.6 8.0 3.5 7.2 6.3 80 50 NP 17 1.1 15 28.6 27.7 8.4 5.8 7.8 6.8 75 65 HP 4
1.5 16 28.5 26.7 8.0 2.5 7.6 6.4 60 65 NP 10 1.7 17 29.3 26.6 8.2 2.2 8.0 6.4 70 65 NP 12 1.4 18b 26.8
-c 8.4
-c 6.9
-c 94
-c
-c 11 1.1 20 27.3 15.9 6.8 0.2 6.8 6.5 80 100 27-29 29 1.1 HP - Not Present.
8 - Water depth less than Im; only surface measurements made, b - Data collected by Dames & Hoore during the aquatic biology sampling.
c - Measurement not required.
~ ~. - -
M M
im M M M M
M M
mW mmW mWmM M
Table 2.2.1 (Continued)
Page 9 of 12 September 1981 Temperature ("C)
Dissolved Oxygen pil Conductivity Approximate (mg/ liter)
(pmhos/cm)
Thermocline Bottom Secchi Station Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 24.8 24.8 7.4 7.3 7.2 7.2 105 100 NP 2.5 0.5 2
26.0 25.4 6.4 5.8 6.8 6.8 100 100 NP 5
0.5 2W 25.8 25.8 5.2 5.0 6.6 6.6 90 90 NP 3.5 0.4 5A 26.9
-a 6.9
-a 7.4
-a 93
__a NP
<1 0.8 11 24.6 24.4 7.0 6.8 7.0 7.0 80 80 HP 1
0.1 12 25.6 25.2 5.2 4.3 6.8 6.6 100 105 NP 31.5 0.9 13 25.6 25.5 5.3 5.2 6.8 6.8 90 90 NP 12.5 0.5
{
h 14 26.0 25.5 6.0 3.9 6.8 6.4 100 110 NP 18 1.3 15 26.2 26.0 7.0 6.8 7.1 7.0 90 90 NP 4
1.3 16 26.6 25.9 7.4 2.9 7.2 6.6 90 90 NP 12 1.4 17 27.3 25.3 8.2 2.1 7.9 6.8 90 90 NP 12 1.4 18b 28.0
-c 10.0
-c 7.8
-c 101
__c
__c 1g 1,3 20 25.7 13.0 4.7 0
6.8 4.6 100 120 26-30 31 1.2 NP - Not Present.
i 0 - Water depth less than Im; only surface measurements made.
b - Data collected by Dames & Moore during the aquatic biology sampling.
c - Measurement not required, n..
M M
M M
M M
M M
M M
M M
M W
M W W M
M i
Tcble 2.2.1 (Continued)
Page 10 of 12 October 1981 Temperature (*C)
Dissolved Oxygen pH conductivity Approximate (mg/ liter)
(umhos/cm)
Thermocline Bottom Secchi Stction Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 16.5 16.4 8.9 8.8 7.6 7.5 160 160 NP 2
0.8 2
20.2 20.1 7.8 7.7 7.2 7.4 120 120 NP 5
1.2 2W 18.5 18.4 7.2 7.3 7.0 6.9 120 130 NP 4
0.6 SA 19.1
-a 7.8
-a 7.6
--a 125
--a NP
<1 1.0 11 16.3 16.3 7.9 7.8 7.1 7.0 130 120 NP 1
0.2 12 21.1 20.5 6.4 6.4 7.0 6.7 100 100 NP 27.5 1.2 13 20.9 20.9 6.4 6.3 7.0 6.8 95 100 NP 8.5 1.3 ft 14 21.1 21.1 6.2 6.1 6.8 6.5 95 95 NP 13 1.2 15 21.1 21.1 6.2 6.1 6.8 6.7 100 100 NP 5
1.3 16 20.9 20.7 5.8 5.8 6.8 6.6 90 90 NP 14 1.5 17 20.8 20.7 5.S 5.7 6.8 6.8 85 80 NP 9.5 1.2 IS 19.2 16.0 7.6 5.7 6.6
--c 83 116
--c 11 1.0 b
20 21.1 13.0 6.2 0.4 7.0 6.3 100 120 29-31 31 1.5 NP - Not Present.
e - Water depth less than Im; only surface measurements made.
b - Data collected by Dames & Moore during the aquatic biology sampling.
c - Measurement not required.
w.-
mMMM M
M M
M M
M M
M M
M M
W W
M M
Tchle 2.2.1 (Continued)
Page 11 of 12 November 1981 Temperature (*C)
Dissolved Oxygen pH Conductivity Approximate (mg/ liter)
(umhos/cm)
Thermocline Botton Secchi Station Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (m) 1 12.4 12.3 9.1 9.0 7.3 7.0 100 100 NP 2
0.9 2
17.2 17.2 7.4 7.4 7.2 7.2 100 100 NP 5
1.9 2W 15.5 15.5 7.2 7.1 7.1 7.0 100 100 NP 4
1.0 5A 16.0
-a 8.8
-a 7.2
-a 100
-a NP 1
(bta) 1.0 11 11.8 11.8 8.8 8.6 7.1 7.1 100 95 NP 1
0.6 12 17.0 16.7 8.4 7.8 7.1 6.6 100 100 NP 30.5 1.7
,ny 13 16.9 16.8 8.3 8.3 7.1 6.9 85 90 NP 7
1.7 U
14 17.1 17.0 8.4 8.3 7.0 6.8 100 100 NP 13 1.7 15 17.0 16.9 8.4 8.3 7.2 7.0 100 100 HP 5
1.7 16 17.2 16.9 8.1 8.0 7.1 6.6 100 100 NP 14.5 1.8 17 17.2 16.9 8.0 7.8 7.0 6.8 90 90 NP 11.5 1.3 18 16.0
-c 7,g
__c 6.3
-C 79
-c
__c 11 1.2 b
20 17.1 16.1 8.3 2.4 7.2 6.5 100 100 NP 31.5 1.7 NP - Not Present.
8 - Water depth less than Im; only surface measurements made.
b - Data collected by Dames & Moore during the aquatic biology sampling, c - Measurement not required.
M Mmmam m
e e
e a
e e
g g
g me Table 2.2.1 (Continued)
Page 12 of 12 December 1981 Temperature (*C)
Dissolved Oxygen pH Conductivity Approximate (mg/ liter)
{ mhos/cm)
Thuinocline Botton Secchi Stction Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m)
Depth (m)
Disc (a) 1 4.3 4.2 13.7 12.6 7.7 7.4 110 100 NP 3
0.2 2
10.5 10.5 10.7 10.6 7.1 7.1 100 100 NP 5
1.5 2W 9.2 7.4 11.0 11.1 7.4 7.5 100 105 NP 4
0.7 5A 8.9
-a 10,7
_a
__b
__a 105 a
NP
<1 0.8 11 4.3 4.3 13.1 13.4 b
__b 100 100 NP 1
0.3 12 10.2 8.7 10.8 b
6.5c
_b 100 100 NP 28 1.5 13 10.1 8.8 10.4 9.9 6.Sc
-b 100 100 NP 12.5 1.2
- y 14 10.5 10.3 10.4 10.4 6.5 b
100 100 NP 14 1.9 5
15 10.8 10.4 9.4 9.2 6.6c b
100 100 NP 4
1.9 16 10.9 10.5 9.6 9.8
-b
__b 100 100 NP 13 1.7 17 10.8 10.3 10.1 10.1 6.5c
_b 100 100 NP 11.5 1.3 18d 20 10.4 9.2 10.7 b
6.5c
__b 100 100 NP 31.5 1.5 l
NP - Not Present.
O - Water depth less than Im; only surface measurements made.
b - Instrument malfunction.
c. Data collected by Dames & Moore during the aquatic biology sampling, d - Measurements not taken due to inclement weather.
~..... -
I Table 2.2.2 Annual sunusary of the results of chemical analysis of water samples taken at the station indicated during the period ef: January 1981 through December 1981.
Page 1 of 9 STATION 1 DEPTH = SURF DETERMINATION-UNITS!
MIN. !
MAX. !
RANOE ! FREQ.!
MEAN 'D ! STANDARD!
8
! DEV.
I SODIUM MG/L!
6.30 !
18.00 !
11.70 !
12 10.69 !
2.31 !
CALCIUM 2.40 !
4.90 !
2.40 !
12 3.83 !
.e4 !
MAGNESIUM 1.70 !
3.20 !
1.50 !
12 2.27 !
.54 !
CHLORIDE 5.00 !
13.00 !
8.00 !
12 7.83 !
2.21 !
I SULFATE (SO 4) 4.00 !
21.00 !
17.00 !
12 10.08 !
4.91 !
TOTAL DISSOLVED 61.00 !
120.00 !
59.00 !
12 77.42 !
13.07 !j SOLIDS I g TOTAL SUSPENDED 2.00 !
130.00 !
128.00 !
12 24.50 !
36.63 !
g SOLIDS l
MO - ALK 14.00 !
30.00 !
16.00 !
1"
- 42 !
4.25 !
l P - ALK (CACO 3) 0.00 !
0.00 !
0.00 !
12 0.00 !
0.00 !
l AMMONIA (NH 3)
.10 !
.60 !
.50 !
12
.23 !
.16 !
p BIOCHEMICAL OXY 1.00 !
2.00 !
1.00 !
12 1.25 !
.45 !
GEN DEMAND CADMIUM
.01
.01 !
0.00 !
12
.01 !
0.00 !
I 4.00 !
21.00 !
17.00 !
12 7.33 !
4.94 !
CHEMICAL OXYGEN DEMAND TOTAL CHROMIUM
.03 !<
.03 !
0.00 !
12
.03 !
0.00 !
.02 ! <
.02 !
0.00 !
12
.02 !
0.00 !
I TOTAL HARDNESS 17.00 !
24.00 !
7.00 !
12 13.92 !
1.93 !
l (CACO 3)
TOTAL IRON
.48 !
9.30 !
8.82 !
12 1.70 !
2.52 !
I, LEAD
. 05 ! <
.05 !
0.00 !
12
.05 !
0.00 !
MERCURY MICRO-GM/L!<
.20 ! <
.20 !
0.00 !
12
.20 !
0.00 !
NITRATE (N0 3)
MG/L!
.60 !
2.30 !
2.20 !
12 2.17 !
.63 !
ORTHO-PHOSPHATE
.01 !
.44 !
.43 !
12
.19 !
.12 !
TOTAL PHOSPHATE
.01 !
.51 !
.50 !
12
.27 !
.15 !
SILICA (SIO 2) 13.00 !
21.00 !
8.00 !
12 15.42 !
2.11 !
TURBIDITY NTU !
5.40 !
150.u0 !
144.60 !
12 27.63 !
42.52 !
ZINC MG/L!<
.01 !
.02 !
.01 !
12
.01 !
.00 !
l-2.00 !
24.00 !
22.00 !
12 8.25 !
5.69 !
CARBON DIOXIDE c
KJELDAHL N NR NR NR NR !
NR NR l
.10 ! <
.10 !
0.00 !
4
.10 !
0.00 !
I i
- In those cases where analyses showed concentrations to be below the detection limit of the analytical procedure, the value of the detection limit itself was used i
to calculate means.
I 1
bValues presented in the text have been rounded to the sensitivity of the analytical procedures.
- Measurement not required.
2.2-27 I-
i I
Table 2.2.2 (Continued)
Page 2 of 9 STATION 2 DEPTH = SURF i
DETERMINATION-UNITS!
MIN. !
MAX. !
RANGE ! FREQ.!
MEAN"'
!' STANDARD!
l I
! DEV.
SODIUM MG/L!
7.60 !
13.00 !
5.40 !
12 9.60 !
1.47 !
I 1.60 !
4.40 !
2.80 !
12 2.90 !
.90 !
3.60 !
2.20 !
12 2.09 !
.61 !
CHLORIDE 4.00 !
9.00 !
5.00 !
12 6.33 !
1.40 !
CULFATE (30 4) 3.00 !
12.00 !
9.00 !
12 7.53 !
3.20 !
TOTAL DISSOLVED 44.00 !
80.00 !
36.00 !
12 67.03 !
10.23 !
SOLIDS TOTAL SUSPENDED 1.00 !
69.00 !
63.00 !
12 12.42 !
18.32\\!
I SOLIDS MO - ALK 17.00 !
22.00 !
5.00 !
12 19.92 !
1.56 !
P - ALK (CACO 3)
O.00 !
0.00 !
0.00 !
12 0.00 !
O.00 /!
AMMONIA (NH 3)
.10 !
.50 !
.40 !
12
.32 !
.13 !
I BIOCHEMICAL OXY-1.00 !
2.00 !
1.00 !
12 1.25 !
.45 !
CEN DEMAND CADMIUM
.01
.01 !
0.00 !
12
.01 !
0.00 ?
CHEMICAL OXYGEN 4.00 !
8.00 !
4.00 !
12 5.00 !
1.31 !
I DEMAND TOTAL CHROMIUM
. 03 ! <
.03 !
0.00 !
12
.03 !
0.00 !
.02 !<
.02 !
0.00 !
12
.02 !
0.00 !
.0TAL HARDNESS 12.00 !
25.00 !
13.00 !
12 15.92 !
4.03 !
(CACO 3)
TOTAL IRON
.22 !
2.40 !
2.13 !
12
.66 !
.61 !
. 05 ! <
.05 !
0.00 !
12
.05 !
0.00 !
I MERCURY MICRO-GM/L!<
.20 !
.20 !
0.00 !
12
.20 !
0.00 !
NITRATE (No 3)
MG/L!
1.20 !
2.90 !
1.70 !
12 - !
1.77 !
.59 !
ORTHO-PHOSPHATE
.01 !
.19 !
.19 !
12
.07 !
.06 !
TOTAL PHOSPHATE
.01 !
.57 !
.56 !
12
.14 !
.15 !
I SILICA (SIO 2) 10.00 !
18.00 !
8.00 !
12 12.67 !
2.19 !
TURBIDITY NTU !
2.20 !
37.00 !
34.80 !
12 11.63 !
10.25 !
ZINC N0/L!<
.01 !
.16 !
.25 !
12
.02 !
.04 !
I CARBON DIOXIDE 3.00 !
17.00 !
14,00 !
12 7.33 !
4.36 !
NR c !
NR NR NR !
NR NR KJELDAHL N BORON
.10 ! <
.10 !
0.00 !
4
.10 !
0.00 !
- In those cases where analyses showed concentrations to be below the detection limit of the analytical procedure, the value of the detection limit itself was used to calculate means.
bValues presented in the text have been rounded to the sensitivity of the analytical procedures.
- Measurement not required.
i 2.2-28
I Table 2.2.2 (continued)
Page 3 of 9 STATION 5A DEPTH = SURF I
DETERMINATION-UNITS!
MIN. !
MAX. !
RANGE ! FREQ.!
MEAN"'D ! STANDARD'
! DEV.
I SODIUM MG/L!
7.70 !
15.00 !
7.30 !
12 9.54 !
2.03 ?
CALCIUM 1.60 !
4.80 !
3.20 !
12
- 2.97 !
1.03 1.40 !
2.40 !
1.00 !
12 1.93 !
.36 MAGNESIUM 4.00 !
11.00 !
7.00 !
12 7.03 !
1.33 CHLORIDE a
I 4.00 !
14.00 !
10.00 !
12 8.67 !
3.26 SULFATE (SO 4)
TOTAL DISSOLVED 52.00 !
87.00 !
35.00 !
12 67.33 !
10.17 SOLIDS TOTAL SUSPENDED 4.00 !
19.00 !
15.00 !
12 10.83 !
4.63 I
SOLIDS MO - ALK 16.00 !
23.00 !
7.00 !
12 20.08 !
2.64 P - ALK (CACO 3) 0.00 !
0.00 !
0.00 !
12 0.00 !
0.00 I
AMMONIA (NH 3)
.10 !
.50 !
40 !
12
.33 !
.14 BIOCHEMICAL OXY 1.00 !
2.00 !
1.00 !
12 1.25 !
45 GEN DEMAND
.01
.01 !
0.00 !
12
.01 !
O 00 CADMIUM I
4.00 !
10.00 !
6.00 !
12 5.17 !
2.17 CHEMICAL OXYGEN DEMAND TOTAL CHROMIUM
.03 ! <
.03 !
0.00 !
12
.03 !
0.00 CCPPER
.02 !
.03 !
.01 !
12
.02 !
.00 I
TOTAL HARDNEG3 11.00 !
21.00 !
10.00 !
12 15.40 !
3.32 (CACO 3)
TOTAL IRON
.33 !
1.60 !
1.27 !
12
.70 !
.37 I
.05 ! <
.05 !
0.00 !
12
.05 !
0.00 MERCURY MICRO-GM/L!<
.20 ! <
.20 !
0.00 !
12
.20 !
0.00 NITRATE (No 3)
MG/L!
1.10 !
2.70 !
1.60 !
12 1.67 !
.44
.01 !
.11 !
.10 !
12
.06 !
.03 ORTHO-PHOGPHATE I
TOTAL PHOSPHATE
.01 !
.16 !
.15 !
12
.11 !
.05 SILICA (SIO 2) 10.00 !
18.00 !
8.00 !
12 13.33 !.
2.15 TURBIDITY NTU !
5.00 !
23.00 !
23.00 !
12 11.32 !
7.20 ZINC MG/L!<
.01 !
.04 !
.03 !
12
.01 !
.01 I
CARBON DIOXIDE 2.00 !
14.00 !
12.00 !
12 7.33 !
3.96 KJELDAHL N NRc NR NR NR !
NR NR
.10 !
.10 !
0.00 !
4
.10 !
0.00 BORON aIn those cases where analyses showed concentrations to be below the detection limit of the analytical procedure, the value of the detection limit itself was used to calculate means.
bValues presented in the text have been rounded to the sensitivity of the analytical procedures.
i l
l CMeasurement not required.
2.2-29
t Table 2.2.2 (Continued)
Page 4 of 9 STATION 11 DEPTH = SURF DETERMINATION-UNITS!
MIN. !
MAX. !
RANCE ! FREQ.!
MEAN a,b! STANDARD!
l
! DEV.
SODIUM MG/L!
5.80 !
13.00 !
7.20 !
12 9.12 !
1.81 !
CALCIUM 2.40 !
4.80 !
2.40 !
12 3.57 !
.77 !
I MAGNCOIUM 1.20 !
2.40 !
1.20 !
10 2.03 !
42 !
CHLCRIDE 5.00 !
11.00 !
6.00 !
12 7.75 !
1.66 !
SULFATE (SO 4) 3.00 !
21.00 !
13.00 !
12 9.00 !
5.53 !
TOTAL DISSCLVED 51.00 !
95.00 !
44.00 !
12 70.33 I
12.39 !
SOLIDS TOTAL GU3 PENDED 1.00 !
50.00 !
49.00 !
12 13.92 !
15.77 !
OCLIDO i !
I MO - ALK 16.00 !
23.00 !
7.00 !
12 19.17 !
1.75 !
P - ALK (CACO 3) 0.00 !
0.00 !
0.00 !
12 0.00 !
0.00 !
AMMONIA (NH 3)
.10 !
.60 !
.50 !
12
.34 !
.16' !
BICChEMICAL OXY 1.00 !
4.00 !
3.00 !
12 1.50 !
.90 !
I.
GEN DEMAND CADMIUM
.01 ! <
.01 !
0.00 !
12
.01 !
0.00 CHEMICAL OXYOEN 4.00 !
20.00 !
16.00 !
12 8.50 !
4.36
- DEMAND I
TOTAL CHROMIUM
.03 ! <
.0? !
0.00 !
12
.03 !
0.00 COPPER
.02 ! <
.02 !
0.00 !
12
. 02 !
0.00 TOTAL HARDNESS 15.00 !
20.00 !
5.00 !
12 17.33 !
1.72 l
(CACO 3)
TOTAL IRON
.49 !
4.'70 !
4.21 !
12 1.41 !
1.23 LEAD
. 05 ! <
.05 !
0.00 !
12
.05 !
0.00 MERCURY MICRO-GM/L!<
.20 !
.20 !
0.00 !
12
.20 !
0.00 8
NITRATE (No 3)
MG/L!
.90 !
'2.90 !
2.00 !
12 1.83 !
.44 ORTHO-PHOSPHATE
.01 !
.40 !
.39 !
12
.16 !
.12 TOTAL PHOSPHATE
.09 !
.42 !
.33 !
12
.28 !
.10 3
SILICA (SIO 2) 10.00 !
19.00 !
9.00 !
12 14.08 !
2.23 g
TURBIDITY NTU !
5.00 !
100.00 !
95.00 !
12 24.86 !
27.75 ZINC MG/L!<
.01 !
.02 !
.01 !
12
.01 !
.00 CARBON DIOXIDE 0.00 !
15.00 !
15.00 !
12 6.42 !
4.24
=
5 KJELDAHL N NRc NR NR NR !
NR NR BORON
.10 !
.10 !
0.00 !
4
.10 !
0.00 5._
- In those cases where analyses showed concentrations to be below the detection limit of the analytical procedure, the value of the detection limit itself was used to calculate means.
I bValues presented in the text have been rounded to the sensitivity of the analytical procedures.
1
- Measurement not required.
9 2.2-30 I
I Table 2.2.2 (continued)
Page 5 of 9 STATION 12 DEPTH = SURF DETERMINATION-UNITS!
MIN. !
MAX. !
RANGE ! FREQ.!
MEAN,b ! STANDARD!
a
! DEV.
SODIUM MG/L!
7.70 !
12.00 !
4.00 !
12 9.37 !
1.50 !
CALCIUM 1.60 !
4.40 !
2.80 !
12 2.33 !
.91 !
I MAONCOIUM 1.20 !
2.40 !
1.20 !
12 1.96 !
.33 !
CHLORIDE 4.00 !
11.00 !
7.00 !
12 6.96 !
1.36 !
4.00 !
17.00 !
13.00 !
12 S.42 !
3.70 !
OULFATE (30 4)
I TOTAL DISSOLVED 59.00 !
79.00 !
20.00 !
12 65.00 !
6.28 !
SOLIDS TOTAL SUSPENDED 1.00 !
14.00 !
13.00 !
12 6.17 !
4.34,!
SOLIDS
)
I MO - ALK 14.00 !
23.00 !
9.00 !
12 19.33 !
2.53 ?
P - ALK (CACO 3) 0.00 !
0.00 !
O.00 !
12 0.00 !
0.00 l AMMONIA (NH 3)
.10 !
.50 !
.40 !
12
.29 !
.15.!
BIOCHEMICAL OXY 1.00 !
2.00 !
1.00 !
12 1.17 !
.39 !
GEN DEMAND CADMIW
.01 ! <
.01 !
0.00 !
12
.01 !
o,co !
CHEMICAL OXYGEN 4.00 !
10.00 !
6.00 !
12 5.50 '
- 'S !
I DEMAND TOTAL CHROMIUM
.03 ! <
.03 !
0.00 !
12
.03 !
0.00 !
.02 !
.02 !
0.00 !
12
.02 !
0.00 !
TOTAL HARDNESS 12.00 !
20.00 !
3.00 !
12 15.17 !
3.07 !
(CACO 3)
TOTAL IRON
.18 '
"3 !
.35 !
12
. 36 !
.11 !
LCAD
.05 ! <
.05 !
0.00 !
12
.05 !
0.00 !
MERCURY MICRO-GM/L!<
.20 ! <
.20 !
0.00 !
12
.20,!
0.00 !
I NITRATE (NO 3)
MG/L!
.70 !
2.10 !
1.40 !
12 1.44 !
.38 !
ORTHO-PHOSPHATE
.01 !
.12 !
.11 !
12
.04 !
.03 !
TOTAL PHOSPHATE,"
. 01 !
.'45 !
.44 !
12
.11 !
.11 !
I SILICA (SIO 2) 10.00 !
15.00 !
5.00 !
12 12.17 !
1.40 !
TURBIDITY NTU !
2.60 !
17.00 !
14.40 !
12 7.96 !
5.44 !
ZINC MG/L!<
.01 !
.01 !
0.00 !
12
.01 !
0.00 !
CARBON DIOXIDE 0.00 !
18.00 !
18.00 !
12 6.58 !
5.50 !
I KJELDAHL N
.30 !
.50 !
0.20 !
3
.37 !
.12 !
.10 !
.10 !
0.00 !
4
.10 !
0.00 !
BORON 8__
aIn those cases where analyses showed concentrations to be below the detection limit of the analytical procedure, the value of the detection limit itself was used to calculate means.
I bValues presented in th text have been rounded to the sensitivity of the analytical procedures.
1
~
2.2-31
I t
Table 2.2.2 (continued)
Page 6 of 9 STATION 14 DEPTH = SURF DETERMINATION-UNITS!
MIN. !
MAX. !
RANGE ! FREQ.!
MEAN,b a
! STANDARD!
I
! DEV.
!I
__l SCDIUM MG/L!
7.60 !
11.00 !
3.40 !
12 9.20 !
1.29 !
CALCIUM 1.60 !
4.40 !
2.80 !
12 2.77 !
.99 !
MAGNESIUM 1.60 !
2.40 !
.80 !
12 2.05 !
.32 CHLORIDE 4.00 !
11.00 !
7.00 !
12 7.00 !
1.31 !
SULFATE (SO 4) 4.00 !
13.00 !
9.00 !
12 7.50 !
3.15 ?
TOTAL DISSOLVED 45.00 !
79.00 !
34.00 !
12 60.92 !
11.43 ?
I SOLIDS TOTAL SUSPENDED 3.00 !
11.00 !
8.00 !
4 4.00 !
3.83 !
SOLIDS i !
MO - ALK 16.00 !
23.00 !
7.00 !
12 19.33 !
2.42 I
P - ALK (CACO 3) 0.00 !
0.00 !
0.00 !
12 0.00 !
0.0Q AMMONIA (NH 3)
.10 !
.50 !
.40 !
12
.29 !
.14 BIOCHEMICAL OXY 1.00 !
3.00 !
2.00 !
12 1.33 !
.65 I
GEN DEMAND CADMIUM
.01 ! <
.01 !
0.00 !
12
.01 !
0.00 CHEMICAL OXY'EN 4.00 !
12.00 !
8.00 !
12 6.17 !
2.92 DEMAND I
TOTAL CHRCMIUM
.03 ! <
.03 !
O.00 !
12
.03 !
0.00 CCFPCR
.00 ! <
.02 !
0.00 !
12
.00 !
0.00 TCTAL HARDNESS 12.00 !
21.00 !
9.00 !
12 15.53 !
3.23 (CACO 0)
I TOTAL IRON
.10 !
.56 !
.46 !
12
.30 !
.12 LEAD
.05 ! <
.05 !
0.00 !
12
.05 !
0.00 MERCURY MICRO-GM/L!<
.20 ! <
.20 !
0.00 !
12
.20 !
0.00 I
NITRATE (No 3)
MG/L!<
.10 !
1.90 !
1.80 !
12 1.16 !
.43 ORTHO-PHOSPHATE
.01 !
.20 !
.19 !
12
.05 !
.06 TOTAL PHOSPHATE
. 01 !
. 28 !
.27.!
12
.09 !
.07 SILICA (SIO 2) 9.60 !
15.00 !
5.40 !
12 11.97 !
1.59 I1 TURBIDITY NTU !
2.50 !
13.00 !
10.50 !
12 4.92 !
2.76 ZINC MG/L!<
.01 !
.04 !
.03 !
12
.01 !
.01 CARBON DIOXIDE 2.00 !
26.00 !
25.00 !
12 6.5S !
7.42 KJELDAHL N
.30 !
1.00 !
.70 !
4
.53 !
.30 I
.10 !
.10 !
0.00 !
4
.10 !
0.00 l
aIn those cases where analyses showed concentrations to be below the detection limit of the analytical procedure, the value of the detection limit itself was used to calculate means.
bValues presented in the text have been rounded to the sensitivity of the analytical procedures.
~
I 2.2 32 5
I Table 2.2.2 (Continued)
Page 7 of 9 I
STATION 15 DEPTH = SURF a,b ! STANDARD!
DETERMINATION-U.;ITO!
MIN. !
MAX. !
RANGE ! FREQ.!
MEAN
! DEV.
l CCDIUM MG/L!
7.70 !
12.00 !
4.30 !
12 9.32 !
- 1. S3 !
.01 !
4.40 !
4.40 !
12 2.40 !
1.26 !
I CALCIUM MAONESIUM 1.00 !
2.90 !
1.90 !
12 1.96 !
.51 !
3.00 !
10.00 !
7.00 !
12 6.53 !
1.73 !
CHLORIDE SULFATE (30 4) 4.00 !
14.00 !
10.00 !
12 8.17 !
3.27 !
49.00 !
75.00 !
26.00 !
12 60.25 !
3.36 !
I TOTAL DISSOLVED SOLIDS 4.00 !
7.00 !
3.00 !
4 6.00 !
1.41 !
TOTAL SUSPENDED SOLIDS I
15.00 !
22.00 !
7.00 !
12 13.92 !
2.50 !;
MO - ALK P - ALK (CACO 3) 0.00 !
0.00 !
0.00 !
12 0.00 !
0.00
.10 !
.40 !
.30 !
12
.23 !
.12 f AMMONIA (NH 3)
BIOCHEMICAL OXY 1.00 !
2.00 !
1.00 !
12 1.17 !
.39 !
GEN DEMAND CADMIUM
.01 ! <-
.01 !
0.00 !
12
.01 !
O.00 !
O.70 '
4.00 !
12.00 !
8.00 !
12
?
6.00 CHEMICAL OXYGEN I
DCMAND 12
.03 '
o' TOTAL CMRCMIUM
'C
.03 ' <
.00 '
O.00 O 00
.02 CCPPCR
.02 ! <
.02 O.00 12 O.45 15.03 TOTAL HARDNESS 10.00 !
21.00 !
11.00 !
12 5
(CACO 3) r TCTAL IRCN
.10 '
.4^
- ^
. 2/.,
.10 !
l LCAO
.05 ! <
.05 !
O.00 !
12
.05 0.00 ?
I-MCRCURY MICRO-GM/L!<
.00 ! <
.20 !
0.00 !
12
.00 !
0.00 !
NITRATC (NO 3)
MG/L!
.50 !
1.70 !
1.20 !
12 1.13 !
.31 !
.01 !
.23 !
.27 !
12
.07 !
.03 !
CRTHO-PHOSPHATE TOTAL PHOSPHATE
. 01 !
.64 !
.63 !
12
.13 !
.18 !
I-9.20 !
16.00 !
6.80 !-
12 12.02 !
1.93 !
SILICA (SIO 2)
TURBIDITY NTU !
2.60 !
6.50 !
3.90 !
12 4.13 !
1.19 !
ZINC MG/L!<
.01 !
.01 !
0.00 !
12
.01 !
0.00 !
I CARBON DIOXIDE 2.00 !.
16.00 !
14.00 !
12 5.50 !
4.56 !
KJELDAHL N
.30 !
.90 !
.60 !
4
.65 !
.30 !
BCRON NRc NR NR NR !
NR NR 5'
aIn those ceses where analyses showed concentrations to be below the detection l
limit of the analytical procedure, the value of the detection limit itself was used l
to calculate means.
bValues presented in the text have been rounded to the sensitivity cf the l
analytical procedures.
CMeasurement not required.
1 2.2-33
I I
Table 2.2.1 (Continued)
Page 8 of 9 STATION 16 DEPTH = SURF a,b DETERMINATION-UNITS!
MIN. !
MAX. !
RANGE ! FREO.!
MEAN
! STANDARD!
I
! DEV.
SODIUM M0/L!
7.60 !
11.00 !
3.40 !
12
?.20 !
1.44 !
CALCIUM 2.00 !
4.00 !
2.00 !
12 2.77 !
.77 !
I MACNCSIUM 1.20 !
2.40 !
1.20 !
12 1.03 !
42 !
CHLORIDE 4.00 !
11.00 !
7.00 !
12 6.67 !
1.37 !
OULFATE (30 4) 3.00 !
14.00 !
11.00 !
12 7.83 !
3.74 !
TOTAL DISSOLVED 40.00 !
79.00 !
39.00 !
12 61.03 !
10.53 !
I SOLIDS TOTAL SUSFENDED 3.00 !
10.00 !
7.00 !
4 8.00 !
3.37 !
SOLIDS I
15.00 1 24.00 !
9.00 !
12
?
19.58 !
2.57 1 MO - ALK 1
P - ALK (CACO 3) 0.00 !
0.00 !
0.00 !
12 0.00 !
0.00 !;
AMMONIA (NH 3)
.10 !
.50 !
.40 !
12
.32 !
.13 !!
BIOCHEMICAL OXY 1.00 !
2.00 !
1.00 !
12 1.33 !
.49 !
I GEN DEMAND
?
.01 ! <
.01 !
0.00 !
12
.01 !
0.00 !
CHEMICAL OXYGEN 4.00 !
12.00 !
8.00 !
12 5.75 !
2.63 !
DEMAND I
TOTAL CHROMIUM
.03 ! <
.03 !
0.00 !
12
.03 !
0.00 !
CCPPER
.02 ! <
.02 !
0.00 !
12
.02 !
0.00 !
TOTAL HARDNESS 11.00 !
20.00 !
9.00 !
12 14.75 !
3.19 !
5 (CACO 3)
TOTAL IRON
.10 !
.23 !
.1S !
1*
^0 !
.07 !
.05 ! <
.05 !
0.00 !
12
.05 !
0.00 !
MCRCURY MICRC-GM/L!<
.20 ! <
.20 !
0.00 !
12
.00 !
0.00 !
NITRATE (NO 3)
MG/L!
.60 !
1.70 !
1.10 !
12 1.07 !
.31 !
CRTHO-PHOSPHATE
.01 !
.12 !
.11 !
12
.03 !
.03 !
. 01 !
.30 t
.29 !
12
.10 !
.09 !
TOTAL PHOSPHATE SILICA (SIO 2) 7.60 !
15.00 !
7.40 !
12 12.03 !
2.20 !
I TURBIDITY NTU !
2.00 !
4.40 !
2.40 !
12 3.23 !
.73 !
ZINC M0/L!<
.01 !
.02 !
.01 !
12
.01 !
.00 !
CARBON DIOXIDE 2.00 !
16.00 !
14.00 !
12 4.75 !
4.05 !
I KJLLDAHL N
.30 !
.70 !
.40 !
4
.43 !
.17 !
.10 ! <
.10 !
0.00 !
4
.10 !
0.00 !
8 aIn those cases where analyses showed concentrations to be below the detection limit of the analytical procedure, the value of the detection limit itself was used to calculate means.
h alues presented in the text have been rounded to the sensitivity of the analytical procedures.
I 2.2-34
I Table 2.2.2 (Continued)
Page 9 of 9 STATION 18 DEPTH = SURF DCTERMINATION-UNITS!
MIN. !
MAX. !
RANGE ! FREO.!
MEAN"' ! STANDARD!
I
! DEV.
OODIUM NG/L!
NRc NR NR NR !
NR NR I
CALCIUM NRc NR NR NR !
NR NR MAGNESIUM NRc NR NR NR !
NR NR CHLORIDE NRc NR NR NR !
NR NR SULFATE (SO 4)
NRc NR NR NR !
NR NR I
TOTAL DISSOLVED 37.00 !
79.00 !
42.00 !
4 53.75 !
17.21 !
SOLIDS TOTAL SUSPENDED 2.00 !
6.00 !
4.00 !
4 4.25 !
1.71 t
!k OCLIDC I
MO - AL:t 2G.00 !
30.00 !
2.00 !
4
- .50 1.00 ';
P - ALK (CACO 3) 0.00 !
4.00 !
4.00 !
4 1.00 !
2.00 I AMMONIA (NH 3)
.20 !
.60 !
.40 !
4
.35 !
.19 I
4 1.50 !
1.00 DIOCilEMICAL OXY 1.00 !
3.00 !
2.00 CCN DEMAND O.00 CAOMIUM
.01 ! <
.01 !
O.00 !
4
.01 CHEMICAL OXYCEN NRc NR NR NR !
NR NR I
DEMAND TOTAL CHROMIUM
.03 ! <
.03 !
0.00 !
4
! ~<
.03 !
0.00 COPPER
.02 ! <
.00 !
0.00 !
4
.02 !
0.00 TOTAL HARDNESS 26.00 !
23.00 !
2.00 !
4 26.75 !
.96 i
(CACO 3)
TOTAL IRCN NR NR NR NR !
NR NR C
!C
.05 ! <
.05 !
0.00 !
4
.05 !
0.00 I
MERCURY MICRO-GM/L!<
.20 ! <
.20 !
0.00 !
4
.20 !
0.00 NITRATE (NO 3)
MG/L!<
.10 !
2.60 !
2.50 !
4 1.00 !
1.33 ORTHO-PHOSPHATE
.01 !
.09 !
.03 1 4
.05 !
.03 05 !
.11 !
.06 !
4
.03 !
.03 TOTAL PHOSPHATE I
NR NR NR NR !
NR NR C
OILICA (OIO 2)
TURDIDITY NTU !
1.60 !
4.00 !
2.40 !
4 2.40 !
1.10 ZINC MG/L!
NRc NR NR NR !
NR NR I
NRc NR NR NR !
NR NR CARDON DIOXIDE KJELDAHL N NRC NR lR NR !
NR NR
.10 ! <
.10 !
0.00 !
4
.10 !
0.00 l
BORON 8'
"In those cases where analyses showed concentrations to De Delow the detection limit of the analytical procedure, the value of the detection limit itself was used to calculate means.
byalues presented in the text have been rounded to the sensitivity of the analytical procedures, cMeasurement not required.
I 2. 2-=
3
MMMEMM E E
M M
M M
M M
M Y M M
M Table 2.2.3 Summary of data taken from the USGS monitoring station at the Fairfield Pumped Storage Facility intake in Monticello Reservoir for the period January through December 1981.
Temperature ('C)
Dissolved Oxygen pH Conductivity (mg/ liter)
(Unhos/cm)
Range Daily Mean Range Daily Mean Range Daily Hean Range Daily Mean Min.
Max.
Min.
Max.
Min.
Max.
Min.
Max.
Min.
Mar..
Min.
Max.
Min. Max.
Min. Max.
January 2.6*
10.3*
5.2*
9.5*
10.1 13.5 11.1 13.2 7.4 7.8 7.4 7.6 66 72 66 71 February 4.3 12.9 6.4 11.0 5.2*
12.5" 8.l* 12.3*
6.8 7.6 7.1 7.5 56 68 60 66 8
8 8
8 8
8 March 8.9 13.8*
9.6*
11.7*
7.7*
12.3 7.9 11.9 7.1*
7.9*
7.l*
7.4*
59" 75" 63 68
- [,g April 11.4 21.0 12.8 18.2 8.2 13.4 9.2 11.7 6.9 9.0 7.0 7.8 57 84 62 72 May 17.9 24.7 18.4 21.9 6.9 11.7 7.8 10.4 6.8 8.8 6.9 7.8 66 84 72 77 June 20.8 30.2 22.0 27.7 5.0 10.5 5.6 8.0 6.6 8.5 6.7 7.4 64 91 69 81 July 24.8*
31.1* 25.6*
29.2*
3.8*
9.1*
4.3*
7.0" 6.5*
8.6*
6.5*
7.2*
74* 110*
77* 91*
August 23.8 30.1" 25.8*
28.1*
3.2*
9.2*
3.9 7.8*
6.5 8.3 6.6*
7.1*
76* 107*
79* 92*
8 8
8 8
September 23.0*
29.8* 24.3*
28.2*
3.0*
9.4*
3.5" 7.8*
6.3*
7.3*
6.6*
6.9*
77* 110" 86* 95*
October 15.6*
24.6* 18.6*
24.3*
6.4 9.9*
6.9*
9.2*
6.7 7.1*
6.7*
7.0" 82* 116*
87* 94*
8 November 10.9*
20.2* 13.5*
18.6*
8.3*
IC.9*
8.4*
9.4*
6.8*
8.3" 6.9*
7.0" 82* 105*
84* 92*
December 4.3 14.1 8.7 14.0 9.0 12.6 9.1 11.8 6.6 7.1 6.8 7.0 51 88 67 86
- Data incomplete for the month.
1 2.3 VASCULAR HYDROPHYTES 2.3.1 Introduction The vascular hydrophytes described in this study included those higher plants with specialized conductive or vascular tissue requiring a hydric I
habitat. Vegetation occupying xeric or mesic habitats was considered terrestrial. Hence, vegetation occurring near the shoreline was in-cluded as aquatic if it was an integral part of the littoral zone. The four major " forms" of hydrophytes included in this study, as defined by Sculthorpe (1967), are:
I 1.
Emergents - These are rooted to the soil and are close to or i
)
below the water level for much of the year, but their leaves and reproductive organs are aerial.
2.
Floating-leaved - These are rooted in' submerged soils, with many of their leaves floating or completely aerial.
I 3.
Free-floating - These are not normally attached but are often entangled in other plants. They may be either completely sub-merged, at the surface, or emergent from the surface.
4.
Submergent - These are attached to submerged materials or sur-
~
faces by roots, rhizoids, or by the whole thallus. Their leaves and reproductive organs remain submerged throughout i
much of the year.
Use of these " forms" was considered both in the categorization of the I
plant as well as in describing the habitat to which it,was confined.
The object of this study was to examine the vascular hydrophyte popula-tion in the study area and qualitatively assess its abundance and species distribution. A list of vascular hydrophytes found in this I
2.3-1
I I
study is presented in Table 2.3.1 along with growth form, location, relative abundance, and relative density.
2.3.2 Findings A total of 57 hydrophyte species was found growing in the study area during 1981 (Table 2.3.1). Numbers of species in each reservoir varied.
Monticello Reservoir had 18 species observed; Neal Shoals Dam, 10; I
Monticello Reservoir subimpoundment, 33; and Parr Reservoir had 44 (including adjacent inundated habitats).
Stand densities, referred to as abundant, moderately abundant, and sparse in Table 2.3.1 were determined by the growth habit of the spe-j cies. For example, cactails (Typha latifolia) and softrush (Juncus effusus) occasienally grew in large monotypic stands described as
/
" abundant," while many forbs such as beggar ticks (Bidens frondosa) and eclipta (Eclipta alba) generally occurred as small populations or as individuals, described as " sparse." The largest monotypic stands I
occurred either submerged or in standing water and are the result of rapid vegetative (asexual) reproduction. The most prominent of these species throughout the study area were the cattails, softrush, and black willow (Salix nigra).
B The dominant vegetation throughout.the littoral zone of the study area l
was emergent (Table 2.3.1).
This vegetation form occurred consistently in areas with shallow water and gently sloping and non-shaded banks.
The most extensive hydrophyte communities occurred in Parr Reserioir, either in backwater areas or on the islands. At the Neal Shoals Dam station, however, where the overhead canopy was very dense and the banks very steep, littoral vegetation was sparse; this lack of vegetation was expected due to the absence of sunlight and unsuitable substrate.
l l
Monticello is a young reservoir which, unlike the subimpoundment, i -
receives little nutrient subsidy (i.e., fertilizer). The development of i
I 2 2-l 3
I the littoral zone of this reservoir may depend on how well the vegetation can withstand wind and wave action. The vegetation of each reservoir is discussed in detail in the following subsections.
2.3.2.1 Parr Reservoir I
Parr Reservoir continued to support an abundant hydrophyte assemblage.
Much of the vegetation was located in backwater areas, resulting from overflow of the banks. These areas are rich in species and support dense populations of composites, grasses, and pickerel weed (Pontederia cordata). The heterogeneous substrate, along with the frequently fluctuating water levels, appeared to promote the growth of a diverse
\\
I flora throughout much of Parr Reservoir. However, the sampling stations 1
(littoral zone) were very rocky and steep and thus supported little or no vegetation. The shallow backwater area parallel to the railroad and I
perpendicular (going north) to thb tailrace canal supported numerous aquatic species, including pondweed (Potamogeton diversifolius), which was not found growing elsewhere in the reservoir. A large, artificial marsh which #s periodically flooded (north of railroad, Figure 2.1.1),
I also supported abundant hydrophytic vegetation and appeared to support numerous water fowl. The numerous islands in the rese" cir are domi-nated by either black willow or grasses (principally Echinocloa spp.).
The Cannons Creek area supported a' rich littoral zone, especially along the north side, where the confluence of a small tributary stream with the reservoir has resulted in a very densely vegetated, marsh-like I
habitat. Dominant species in this area were aneilema (Aneilema keisak) and Arthraxon hispidus var. cyptatherus.
The sampling station at Cannons Creek supported the most abundant vege-tation of any of the sampling stations visited. Dominant species at this station included boltonia (Boltonia asteroides), spike rush (Eleo-charis obtusa), and marsh-fleabane (Pluchea camphorata).
2.3-3 i
L_
I I
Mich of the peripheral area around the Cannons Creek Station had an aspect dominance of bulrush, although other sedges were also numerous.
Although some areas near the landing were periodically moved, the Cannons Creek area supported a relatively stable and productive littoral I
community. A few cypress (Taxodium distichum) saplings have also been planted in this area.
2.3.2.2 Neal Shoals Dam The Neal Shoals Dam area has shown very little change in species compo-sition since the beginning of the monitoring period. The willow islands I
which occur in the cove where the central station is located have been occasionally sprayed with herbicides, but they continued to show some
{
second growth. Most of the dead willows have been densely colonized by l
bryophytes and lichens. No hydrophytic vegetation occurred at the littoral zone sampling station.
I 2.3.2.3 Subimpoundment The subimpoundment contained a very diverse and abundant commanity of vascular hydrophytes. This area has been frequently fertilized as a management practice, resulting in nutrient enrichment and accelerated eutrophication. This was manifested by a rapid development of the lit-total zone. The coves were abundantly populated by softrush, cattail, and willow. Alder (Alnus serrulata) was gecasionally associated with these species in moderate abundance, l
Though extremely abundant in previous years, pondweed (Potamogeton diversifolius) was less dominant; it was only occasionally observed in moderately abundant stands in the subimpoundment.
Instead, an unidenti-fied filamentous alga appeared to dominate. The sampling station, though slightly exposed to wave action, appeared to maintain a rela-tively well-developed littoral community. Softrush was dominant here, although it occurred in small clumps rather than extensive stands.
t l
e
- I
E I
2.3.2.4 Monticello Reservoir Monticello Reservoir continued to show development of vegetative asso-ciations, particularly within the coves. Here, associations of cat-tails, sof trush, bulrush, and willows typically dominated the ends of the coves. Spike rush (Eleocharis obtusa) was occasionally distributed as moderately abundant mats along the shores and in deeper water in these coves.
I The substrate in the coves of Monticello Reservoir appeared to be high in organic content, whereas the banks outside the coves which were exposed to wave action, supported very little vegetation. The exposed shorelines were often very steep and had a clay, hardpan substrate, i
hindering colonization by hydrophyter.. This condition persisted throughout the year and vegetation (kudzu) colonized only the upper i
I edges of the eroded areas.
1 Individual sampling stations in the littoral zone of Monticello Reser-voir were generally very sparsely populated. Most of the stations were located on exposed shorelines and therefore exhibited negligible vege-tative development. Because of the relative instability of these areas, it is likely that this condition will persist.
2.3.3 Discussion l
Vascular hydrophytes perform several important functions in aquatic eco-(
systems. As primary producers, they contribute to the supply of oxygen in the water, by photosynthesis, when submerged.
In lentic (lake) ecosystems, hydrophytes are important contributors of organic matter to the detrital food chain. These plants also provide habitat, cover, and j
food for many species of animals, such as insect larvae, fish, birds, and mammals. Crowth along reservoir edges can also protect the banks I
from erosion caused by wave action. This latter function is important in stabilizing the littoral zone and its associated faunal components.
2.3-5 5
I t
The effects of lack of vegetation are particularly evident in Monticello Reservoir where gulleys d2 void of vegetation are becoming eroded and could present problems in maintenance of a healthy aquatic community in the future.
The abundance of hydrophytes in restricted areas such as coves or back-waters is attributable to shallow water and the protection from wave action. Cattails and softrush, the dominant vegetative types in Monti-cello Reservoir and the subimpoundment, are capable of rapid vegetative reproduction in suitable habitats (i.e., the coves). Thus, these spe-I cies are important in stabilization of shoreline substrates and in facilitating development of a littoral community. Organic sediment was abundant in these stands as a result of increased siltation, stressing k
I their role in successional development. This type of succession is f
/
common in shallow areas of lakes (Sculthorpe, 1967).
Other significant factors limiting development of littoral zones, besides water depth and wave action, are steep banks and a dense overhead canopy. The results of these factors are particularly evident I.
at the Neal Shoals Dam station, where a dense overstory of willows, cottonwoods, and red maple, along with steep banks, severely limit herbaceous vegetation along the shoreline. Fluctuating water levels, along with high turbidity, have probably also been contributing factors limiting the distribution and abundance of vascular hydrophytes in the study area.
8_
Morphological adaptations of vascular hydrophytes frequently provide compensating mechanisms to enable establishment of aquatic vegetation.
These adaptations include a high degree of phenotypic plasticity of leaves such as in pondweed and arrowhead (Sagittaria latifolia); rapid lateral growth by underground stems (rhizomes); and the production of spongy tissues (aerenchyma) which facilitate oxygen metabolism in relatively anaerobic conditions. Thus, many of those species colonizing the shorelines throughout the study area are preadapted to a stressful environment, l
2.3-6 8
I I
Most of the species found in the study area are emergent hydrophytes (Table 2.3.1) and, therefore, are less affected by the water-related limiting factors such as depth, turbidity, and fluctuations of water level.
Submerged hydrophytes are more likely to be influenes i by increases in I
turbidity than emergent hydrophytes, not only because of reduced light penetration but also as a result of abrasive effects which can damage the leaves.
The cause of the decline in abundance of pondweed in the subimpoundment is uncertain, but competition from stress-tolerant algae, along with
\\
occasional oxygen depletion (based on field measurements) associated i
l' with eutrophication, may be contributing factors.
/
Table 2.3.2 presents dominant vegetation communities, relative fish and wildlife value, probable successional changes, and factors most evident in limiting the hydrophytes in each reservoir.
I 2.3.4 Summary A total of 57 species of vascular hydrophytes were found growing in the study area. No significant increases in diversity were noted over previous surveys, although the abutidance of several species continued to increase.
Species which increased in abundance included softrush, cat-tail, grasses (Echinocloa spp.), and willows (in Monticello Reservoir I
only). The subimpoundment continues to show eutrophic conditions, although the pondweed population has decreased in abundance. The major factors limiting growth of the littoral vegetation along all banks appeared to be shading by canopy vegetation and steep banks which did l
not provide a suitable area for colonization. Other significant factors affecting plant development were turbidity, deep water, fluctuating water levels, and wave action.
!R 2.3-7 l5
I I
Table 2.3.1.
Vascular hydrophytee found during shorellne surveys of Parr and Monticello Reservoirs, Neal Shoals Dam, and the subispoundment,1981.
Page 1 of 4 Form
- Stand 5
D C
d Scientific Name Common Name (Hebltet) Location Densities Distribution Allsma subcordatum Water-plantain E
P S
R S
S R
Alnus serrulata Alder E
S MA 0
NS S
R I
Amania coccinea Ammonia E
S S
R M
S R
Anellema kelsak Anellema E,S P
A 0
I*
CC A
0 Arthreren hispidus var.
Grass E
CC MA R
cryptatnerus i
\\
I Aster sp.
Aster E
P MA C
j CC(St.C) MA C
}'
NS S
R M
S R
/
I m
0 Bacopa mannelrl Water-hyssop E
M S
R Bldens frondosa Beggar ticks E
M S
0 I'
0 F
S O
CC S
O Boltonia asteroldes Boltonia E
P m
O I
CC(St.C) MA R
Carex turlda Caric sedge E
S(St.H) m 0
I Cephalanthus occidentails Buttenbush E
CC( St.C) S 0
P S
0 l
l Chasmantium latifollun inland seaoats E
S S
R NS S
R I
P S
R Cicuta maculata Water hemlock E
P S
R CC S
R Cyperus erythrorhlros Flat-top sedge E
S(St.H)
MA 0
Cyperus Irla Flat-top sedge E
P S
R CC(St.C) MA 0
l M(St.K)
S R
Cyperus virens Flat-top sedge E
P S
0 Olodls virginiana Buttonwood E, S P
S 0
I 1
2.3-8
I I
Table 2.3.1 (Continued)
Page 2 of 4 I
8 Form Stand D
C Scientific Name Common Name (Habitnt) location Dens it ies Distributiond I
Echinocios colonum Barnyard-m!Ilet E
S(St.H) m o
P A
C CC m
C Echinocios crusgall!
Bernyard-millet E
M S
0 I
S S
C P
A C
CC m
0 Eclipta alba Eclipta E
M S
R 5
P S
R Eleocharts obtusa Spike rush E.S P
S R
S m
0 I
CC(St.C) m 0
M m
0 Eleccharls quandrangulata Spikerush E
S m
R
\\
I Erlanthus alcanteus Sugarcane E
M m
C plumegrass S
m C
i P
S O
/
CC S
0 I
Fuerina squarrosa Umbrella-grass E
$(St.H)
S R
l M C
S R
Hibiscus moscheutos Hibiscus E
S S
0 I
NS S
R P
S R
CC S
0 Hydrolea quadrivalvis Hydrolee E
P S
0 Hypericum mutitum St. John's wort E
M S
R P
S R
I Juncus acuminatus Bog-rush E
S S
R P
S 0
CC S
O Luncus dichotomus Bog-rush E
S(St.H) m 0
I Juncus effusus Sof t rush E
M m
0 S
A C
CC m
0 Juncus polyceohalu_s Bog-rush E
S S
R Leersta oryzoldes Cut grass E
S m
R I.
Falso pimpernel E
P S
R Lindernia duble NS S
R Leawlala alternifolla False-loosestri f e E,5 S
S 0
Ludwigle alterniflora False-looses tri f e E
S(St.H)
S O
Ludwigle glandulosa Falso loosestrife E
CC(St.C) S 0
l Ludwigla palustris False-loosestrife E,5 M
S R
S S
R s-2.3-9
'8
I I
Table 7.3.1 (Cont inued)
Page 3 of 4 a
Form Stand b
c d
Scientific Name Comen Name (Habitat) Location Densities Distributton I
Mimulus ringens e nkey-flower E
M S
R S
S O
P S
O N iluco victicillata Carpet-weed E
P(St.8)
S R
Paspalum notatum Pas pal um E
S(St.H)
S O
P S
O Penthorum todoldes Oltch stone crop E
P S
R Pluchea camphorata Marsh-floablano E
M(St.M)
S R
CC S
O NS S
R I
P S
O CC(St.C) m O
M(St.0) m O
i i
Polynonum hydropiperoldes Smartweed E
5 C
{
I NS R
CC m
O l
P m
O
/
I Polyqonum lapathlfolium Pale smartweed E
NS S
R P
S R
Polygonum saqlttatum Tearthumb E
P m
O CC m
O Pontederla cordata Pickereiweed E
S S
O P
S 0
CC m
C I
Potamogeton diversifolius Pondweed 5,FL S
S 0
P m
R Pfllimnium capillaceum-Mack Bishop's CC(St.C) M R
l weed Rhynchospora corniculata erned rush-E CC(St.C) S O
P S
R Rotala ram slor Tooth-cup E,5 NS S
F.
l S
m O
Sagitterla latifolla Arrowhead E
CC S
O Salix nlara Black willow E
P A
0 CC.,
~ A C
M O
N3 w M
NA O
3 m
C Saururus cernuus Lizard's tall E
P S
R
.CC(St.C) S R
i I
Scirpus cypeelnus Woolgrass bulrush E
S
- A C
- m C
P-M R
l MtSt.l.K) MA 0
5 2.3-10 8
I I
Table 2.3.1 (Continued)
Page 4 of 4 I
a Form Stand Selentific Name Common Name (Habitat) location Densitlesc D
d Dlstribution Scirpus valldus Softn tem bulrush E
S HA 0
P S
R Taxodlum distichum Bald cypress E
CC S
0 M(St.1)
S R
S S
R 5
Tyoha latifolla Cattall E
M(St.M)
MA 0
A C
CC MA 0
P S
0 a Symbols for form (or habitat) of plants are as follows:
I E = Emergent S = Submerged FL = Floating leaved 4
b Symtnis for locations of populations are as follows:
I M = Monticello Reservoir P = Parr Reservoir li Su Subimpoundment I
CC = Cannons Creek NS = Neal Shoals Reservoir St.~ = Individual station corresponding to neerest littoral benthic macroinvertebrate sampling location.
c Symbols for stand densities are as follows:
A = Abundant (a great umber of Individuals / stand)
MA = Moderately abundant I
S = Sparse (one or tm Individuals / stand) d Symbols for distribution are as follows:
C = Common 3
0 = Occasional R = Rare l
l l 8 l 5 5
lg
g 2.3-11 5
M MM M
M M
M M
M M
W W
W W
W W W W
W 4,
Table 2.3.2.
Dominant vegetation, fish and wildlife value, expected succession, and probable major limiting factors of the littoral communities of the water bodies in the study area, 1981.
Dominant Fish and Expected Probable Major Location Vegetation Wildlife Value Succession Limiting Factors Cannons Creek Diverse; cattails, soft Moderate to high No significanL change Steep banks; deep, rush, boltonia, and in the marshy
- likely, turbid water,
- sedges, areas.
fluctuating water,,
levels.
Subimpoundment Diverse; cattails and liigh Trend is toward eutro-Fertilizer accelerating soft rush; pondweed in phication, growth; lir.ited by styep C
bwks and sbgding. '
- coves, Parr Reservoir Abundant willow stands, High Uncertain; succession Fluctuating water level, y
amartweed, and grasses, appears attenuated by shading, steep banks, and 4
especially on islands and limiting factors.
turbid water, w
backwater areas.
Monticello Reservoir Cattails and soft rush in Moderate Continued development of Steep, clay banks, wave coves.
littoral zone in areas action.
where erosien is not significant.'
Neal Shoals Primarily willows, very-Low to moderate. Little succession expected Steep banks, deep water, little herbaceous growth in near future.
heavy shading from canopy.
along littoral zone.
e-
%,emM
I~
Is 2.4 PHYTOPI.ANKTON 2.4.1 Introduction Phytoplankton are microscopic, free-floating plants which make up an important component of the aquatic ecosystem. They occupy the lowest I
trophic level in the food web within the aquatic environment and are consumed by many types of higher life forms, including invertebrates, e
fish, and occasionally, vertebrates such as waterfowl. Thus, the general. health and physical well-being of these consumers are directly or indirectly dependent on phytoplankton.
In addition to the biotic relationships of phytoplankton, there are i
numerous abiotic factors which are also of importance. Knowledge of f
/
phytoplankton species composition is useful in interpreting water quality and predicting potential problees concerning nuisance algal growths.
Nuisance. algae can cause water taste and odor problems, and bio-fouling in filters, screens, pumps, and other types of water handling equipment.
I 2.4.2 Findings and Discussion Parr Reservoir Stations in Parr Reservoir (Statisns B, C, and D) were sampled during January, April, July, and October. The complex phytoplankton assem-I blage showed definitive quarterly (temporal) patterns. These patterns were exemplified by evaluating mean total densities, collectively, from Stations B, C, and D.
These density data are provided in Tabi.e 2.4.1.
Mean total densities in Parr Reservoir ranged from 3,712/ml in October to 72,988/ml in January. An algal bloom was evident at all of the Parr Reservoir stations during January, with densities ranging from 115,481 I
cells /ml at Station B to 18,581 cells /ml at Station D.
Phytoplankton populations exhibited a general decline in numbers through the next 2.4-1
.5
I three sampling efforts, with October densities ranging between 4 and 35 times lower than those found in January.
Except at Station B in April, diatoms (Baci11ariophyta) were the pre-dominant algal group at all of the Parr Reservoir stations for every sampling effort. This group of organisms comprised between 97 and 54 I
percent of the phytoplankton community throughout the year at all of the stations, except at Station B; diatoms represented only 41 percent of the total community there in April. Green algae (Chlorophyta) were present in samples from each of the sampling stations during all of the months surveyed. Fifty-six and twenty-seven percent, respectively, of the algal population sampled at Stations B and D in April (9,088 l
i.
I cells /ml and 4,179 cells /ml, respectively) were chlorophytes; green j
algae represented between about 18 and 24 percent of the phytoplankters
/
collected at Stations C and D in April and July as well as at Station C in October. Blue green algae (Cyanophyta) were also well represented at the Parr Reservoir stations in October, with 25 percent of the community at Stations B and C and 12 percent at Station D.
' E
""8 the C ur8e f the quarter y 88mP in8, alga Sr ups other than l
W the diatoms, green, and blue green algae were generally uncommon.
Other algal groups, made up less than 7 percent of the densities during I
the four surveys.
The species diversity and number of taxa reported during the quarterly surveys fluctuated independently of the total densities. Collections 8
in July yielded the greatest number of taxa (12.3).
The number of taxa collected during the other three quarterly surveys ranged from an average 11.3 (April) to 8.7 (J.inuary). The average species diversity 5
(a measure of the distribution of taxa among the number of individuals per taxon) was highest during April through October when average di-versity values were between 2.15 and 2.61, and lowest during January (0.96).
5 P
E 2.4-2
I During each sampling period, the predominant species were quite similar in Parr Reservoir.
In January, Melosira was, by far, the dominant I
organism, comprising from 53 percent of the phytoplankton community at Station D to 89 and 93 percent of the communities, respectively, at Stations C and B.
The diatom, Cyclotella, and a blue-green, Anabaena, were also important components of the phytoplankton community at these stations in January.
During April, Melosira and Cyclotella were again among the predominant I
species at the Parr Reservoir stations, with the green alga Chlamy-domonas also beccming a very important part of the phytoplankton community. Cyclotella was the most abundant organism at Stations C and D, comprising 33 percent and 40 percent, respectively, of the com-j munity there; Chlamydomonas was the most prevalent species at Station B, comprising more than 37 percent of the organisms collected there, f
' ll of the Parr Reser-Synedra, a diatom, was the. predominant alga at a
voir stations in July, representing from 71 percent (Station B) to almost 43 percent (Station D) of the phytoplankton communities in July.
Synedra was also a very important component of the algal community in October, when it comprised from 48 percent of the community at Station B to 20 percent at Station D.
Cyclotella and Melosira were also I
abundant at Station D, while Lyngbya (a blue green alga) was the second l
most prevalent species at Station B.
Total phytoplankton biomass in Parr Reservoir during 1981 cannot be correlated with total phytoplankton densities. When the average I
biomass was highest during April (11.7 mg/ liter), the phytoplankton density was much lower than during January (when the average densities j
were much higher).
Zhe lack of correlation between t'hese data may be caused by suspended solids in the water column, which affects both turbidity and biomass. Turbidity affects phytoplankton production by restricting light penetration into the water and, therefore, reducing primary productivity by.'.owering rates of cell growth and reproduction.
i I 3
I I
In addition, solids in the water will add non phytoplankton biomass to I
samples, resulting in apparent biomass increases where no appreciable increase occurs in the density of plankton organisms.
Evaluation of the phytoplankton communities observed at the three Parr I
Reservoir stations showed apparent dissimilarities during 1981. The range of values and mean annual phytoplankton density were highest at Station B'and lowest at Station D.
The inverse of these findings was observed for mean biomass and species diversity. The highest average number of taxa was found at Station C, and the lowest at Station D.
These data suggest that, although Stations B, C, and D are all within the boundaries of Parr Reservoir, each undergoes independent ecological i
I succession.
i
/
In past studies (Dames & Moore; 1978, 1979, 1979a), Station B con-sistently accounted for the lowest phytoplankton density, taxonomic cichness, biomass, and species diversity. Station C, located in the Cannons Creek embayment area, was consistent in producing the highest phytoplankton density, species diversity, and number of taxa.
Station I
D was ranked between these two stations in the above characteristics, except for biomass. This latter station generally showed higher bio-mass levels than at the other stations. During 1981, only the station I
trend for biomass levels did not change with regard to previous trends.
Neal Shoals Dam I
The phytoplankton density increased to a high of 29,961 cells /ml in July from a January low of 5,583 cells /ml, and then declined to 12,901 cells /ml in October, l
B As at the Parr Reservoir stations, in January, April, and October diatoms were most abundant; these organisms made up approximately 44, u
2.4-4
I 93, and 63 percent of the total density, during the respective months.
During July, the green algae were predominant (58 percent), but diatoms (37 percent) were also abundant. Green algae were also numerous during January (25 percent) and October (22 percent).
During January, 63 percent of the phytoplankton population at Station P I
was evenly distributed among the following genera: Spirogyra (a green alga), Navicula (a diatom), and Anabaena (a blue-green alga).
In April, Synedra comprised 31 percent of the population but, as in Parr Reservoir, Cyclotella and Melosira were also abundant. The July sampling effort yielded Dispora (a green alga) as the most abundant species (40 percent), followed by Synedra (25 percent), which was also j
I abundant in Parr Reservoir. Synedra remained at a level of 25 percent I
of the population in October, but was rivaled in abundance by
/
Chlamydomonas and Cyclotella (both almost 20 percent).
The species diversity indices at Station P were very similar throughout the entire year; the values recorded ranged from a low of 2.77 in October to a high of 3.07 in January, and the mean for the four sam-I pling periods was 2.87.
The biomass data reflected the phytoplankton densities throughout the year; the highest biomass (16.8 mg/ liter) occurred in July, and the lowest (5.2 mg/ liter), in January, I
i l
Subimpoundment Phytoplankton densities in the subimpoundment were highest in October (24,737 cells /ml) and lowest in January (9,387 cells /ml), but the trend 1
was not toward greater density over the year since April populations were highe6 than those reported for July.
I.
During January and July, diatoms were the most abundant algal group at Station H, representing 57 and 52 percent of the population, respec-l tively. The blue green algae were also important during the
.g I
2.'+-5 i
l
I January (27 percent) and July (26 percent) periods, with green algae also forming a large portion of the phytoplankton community in July (22 percent). During April, the chlorophytes were the most abundar.t group (64 percent) and, in October, the blue greens were most numerous (52 percent).
In both April and October, diatoms remained an important component of the community, representing 32 and 36 percent of the I
community during those respective months.
A total of 15 taxa was collected from Station H from April through October, while 12 taxa were collected in January.
Species diversity ranged between 3.13 (July) and 2.14 (Janaary), averaging 2.66 for the year.
In January, Melosira (51 percent) and Anabaena (26 percent) were I
the most abundant species. Chlamydomonas accounted for 43 percent of the community, but another green alga, Chlorococcales (13 percent), and
,1 the diatom Asterionella (13 percent) were also important during April.
During the summer period, the blue green Oscillatoria formed the most abundant couponent (25 percent) of the algal community, but Synedra (19 percent), Melosira (15 percent), and Chlamydomonas (12 percent) were present in relatively high concentrations also.. Lyngbya, a species not found in the July samples, bloomed to 41 percent of the October population, with Synedra remaining at a level (22 percent) similar to that seen in July, and Cymbella increasing to 12 percent of 8
the community.
Monticello Reservoir Phytoplankton densities generally showed characteristic trends during every season except summer.
In the winter, mean densities at all stations increased from 3,537 cells /ml during November to 41,567 I_
cells /ml in January. A decline of 30,562 eells/ml occurred in February from January's winter high, but mean densities increased during the spring from March (15,960 cells /ml to May (38,918 celle/ml). June phytoplankton densities decreased to an average of 22,470 cells /ml for the Monticello Reservoir stations. This decrease in the mean phyto-2.4-6 1
I plankton density was followed in July by an increase to the highest mean level recorded for 1981, 47,791 cells /ml. From late summer I
(August) to October, densities decreased from 11,746 cells /mi to 3,284 cells /ml.
Mean densities for phytoplankton at all of the Monticello Reservoir stations indicated that diatoms were the most numerous group, forming 94 (January) to 53 (April) percent of the community, during every month I
except August and September.
In August, the diatoms were second in abundance (38 percent) to the green algae (58 percent); diatoms and green algae were almost equally abundant, as an average, with 38 per-cent and 36 percent of the community, respectively, during September.
Green algae were also important components of the algal community in i
Monticello Reservoir during March (46 percent) and April (51 percent).
Station J was the only station where diatoms dominated the phytoplank-
/
5 ton community year-around, but the chlorophytes were very important (43 percent) at this station during April. At the other Monticello Reservoir stations, green algae were dominant or co-dominant with the I
diatoms from one time (Station I in August., Station M in September) to four times (Stations N and 0 in March, August, September, and December) times during the year.
Melosira was the most abundant organism at all stations during January and February. Although still an.important component of the phyto-l l
plankton community in March, Cyclotella, Chlorococcales, and y
Chlamydomonas were also abundant at all of the stations sampled. By April, Melosira and Chlamydomonas remained important at all stations, and Fragillaria showed a strong increase at Station I.
A Fragillaria bloom was evident at all stations during May and June, but by July this diatom had almost disappeared from the community, being replaced by a Synedra bloom at all stations.
In August, dominance was spread among
' 5 g'-}s, different genera at each station, but in September, Lyngbya was the dominant at Station I and Chlamydomonas was dominant at all other sta-egya
~w tions.
In October, Melosira reappeared as the dominant genus at four i
2.4-7 E
I stations, with Synedra dominant at Stations J and L and Fragillaria most abundant at Station K.
Melosira continued to be a very important component of the Monticello Reservoir phytoplankton community in E'
" " * * " ' ' "i'"
"*d'" " ' ***"* "'""d""' "' "'i " ' ""d R
being most numerous at Station M.
In December, Cyclotella was most abundant at Stations I through N, but was codominant with Melosira at Stations K and M and codominant with an unidentified chlorophyte at Station N.
The unidentified chlorophyte was the predominant species at Station O in December.
Mean species diversity at the Monticello Reservoir stations was lowest I
(0.61) in January but increased during the next two months until it reached 2.75 in March. The diversity then decreased to its second
{
lowest value (1.17) in May before rising to it, highest level (3.03) in f
August. By the end of the three following mor.chs, the diversity had declined tp 1.82.
It remained relati ely constant (1.95) in December before dropping to the January low.
I The highest mean number of taxa (10.7 to 14.7) occurred between February and September. The lowest number of taxa (6.5) was recorded in December, but November and January showed a similarly low number, (6.7) for each month.
Mean total phytoplankton biomass.from the samples collected in Monti-I cello Reservoir was highest between April (12.0 ng/ liter) and July (11.6 mg/ liter), with the highest biomass recorded in June (22.6 mg/ liter). Af ter this peak period, the mean biomass declined from 5
1 8.0 mg/ liter in August to 6.2 mg/ liter in December. During eight of l
the sampling periods, density and biomass increased and decreased l
synchronously. However, in February, when densities had decreased to one-fourth of January levels, the biomass showed a slight increase.
In March, the biomass declined by 1.9 mg/ liter from February while the density increased 1.5 times over February collectio.ts.
In June, i
1 although the mean phytoplankton density had decreased significantly 5
2.4-8 1
I I
from the May levels, the biomass increased by 9.0 mg/ liter. July also showed an inverse correlation between biomass and density. Discrepan-cies in biomass-density relationships may be due to contamination from non planktonic biomass during periods of high turbidity.
I Although the monitoring results sometimes differed noticeably among the Monticello Reservoir stations for the monthly sampling efforts, none of the stations appeared to exhibit a continual, monthly pattern of higher or lower biomass, density, diversity, or taxa number levels than any of the other stations. However, in general, the southern Monticello Res-I crvoir stations (L, M, N) appeared to have lower mean densities than the other stations.
Such a trend was not evident for the other param-eters measured. Station J showed the greatest range in density mea-surements. Station I had the highet.r mean annu.1 gecies diversity (2.35), and Stations J (1.73) and N (1.80), the
!..est.
I In addition, although the dominant genera anc' presentative genera I
sometimes differed among sampling stat.inr.
..tdividual sampling ar ef fort s, there was an over-all similarity.
e phytoplankton composition among stations. For exampic.
. ugh Chlamydomonas was I
the most abundant phytoplankter at all. cati.m during September, with the exception of Station I (where it
<ed in numbers by Lyngbya and Cymbella), this genus still.:oc.
.ed an important part of the community at Station I (almost 11 r arcen -
In addition, during the same sampling period Cymbella formed an impor' ant part of the phytoplankton community at Stations M, N, and te (;I to 13 percent), and Lyngbya was relatively numerous (13 to 22 percen ) at Fea,lors K, M, I
and O.
2.4.3 Summary
-[
During previous studies (James & Moore, 1978, 1979a, 1979b, 1980),
g g.y -
parameters measured for the phytoplankton communities in Parr Reservoir In;;
were observed to be similar to those found at the Neal Shoals Dam sampling site; additionally, the subimpoundment was found to nhibit 2.4-9 l
.. v.
I I
phytoplankton community characteristics similar ca thcae. recorded for Monticello Reservoir. With the exception of species composition, during 1931, the phytoplankton sampling results from Parr Reservoir I
shewed little similarity to those from the Neal Shoals Dam station.
The same dissimilarities, again with the exception of generic composi-tion, were evident between the Monticello Reservoir and subimpoundment I
stations.
During the quarterly surveys in Parr Reservoir, biomass generally fluc-tuated inversely to phytoplankton biomass while a positive biomass-density relationship occurred in Monticello Reservoir during eight of the twelve samplings. These relationships have been observed during 4
previous studies of phytoplankton in the two reservoirs. The opposing
\\
I oatterns seem to be largely caused by the influence of relatively high f
turbidity in Parr Reservoir and generally lower values in Monticello Reservoir.
In Parr Reservoir, the high biomass values are not con-sidered to be accurate indicators of biomass due to non planktonic contamination.
5 The monthly fertilization program being carried out from March through August in the subimpoundment appears to have prolonged the period of highest phytoplankton production during 1981. Although Monticello Reservoir experienced a phytoplankton bloom in January and was char-acterized by decreasing phytoplankton numbers from August through October, the subimpoundment populations were at their lowest recorded level in January before initiation of the fertilization program and peaked in October following termination of the program.
In spite of I
l the artificial nutrient input into the subimpoundment, however, phytoplankton densities at Station H were, except in October, lower I.
than the mean densities in Monticello Reservoir. However, fertiliza-tion appears to have shifted the generic composition since green and blue green algal comprised a greater proportion of the phytoplankton comnunity in the subimpoundment than in Monticello Reservoir. A shift l
2.4-10 l
I..:'
W in species abundance as a result of inorganic fertilization has been documentad in the literature (Bennett, 1970).
As in '.he 1980 study (Dames & Moore, 1980), a high degree of similarity in the. phytoplankton community was observed among the Monticello Reser-I voir stations. The ecological variables measured in the phytoplankton commanities were generally quite uniform throughout Monticello Reser-voir, although mean densities seemed to be, on the average, somewhat lower at stations in the lower reservoir. The generally higher
. variation in range of phytoplankton densities near the FPSF noted during the 1980 effort was not evident during 1981.
1
/
I I
I I
I I
E I
3 2.4-11 3
1
S
& 'S S M M
S S
S S
S M
Table 2.4.1 Density, biomass, rumber of taxa, and ta>onomic diversity of phytoplankton colle<:ted during 1981 at Parr Reservoir, Neal Shoals Dam, Ibnticello Reservoir, and the subimpoundment.
Page 1 of 7 Area Parr Reservoir Neal Shoals Dam Stat ion u
c o
e Density (cells /ml)
J A
JL 0
J A
JL 0
J A
JL 0
J A
JL 0
Chlorophyta 1212 9088 506 85 376 5229 7470 513 364 4179 823 172 1396 1185 17511 2783 Euglenophyta 369 0
0 0
0 0
14 1 0
0 0
0 0
Cryptophyta Pyrrophyta Chrysophyta 0
0 0
0 94 0 215d 0
0 0
16 5 0
225 0
1245 1012 Bacillarlophyta 111952 6648 12930 3248 80855 20506 21746 1281 16395 11264 3462 3612 2131 14525 11205 8094 9
- s.
Cyanophyta 2317 422 1111 3577 0
598 1822 0
516 1531 0
1012 Total 115481 16105 13858 4444 84902 25735 31374 2392 18581 15584 4450 4300 5583 15710 29961 12901 Biomass (mg/l) 7.1 9.6 9.0 8.1 7.4 13.0 13.1 10.7 7.6 12.6 10.8 15.1 5.2 14.6 16.8 12.6 Species
.55 2.54 1.50 2.16
.74 2.73 2.15 2.45 1.58 2.55 2.79 2.96 3.07 2.84 2.78 2.77 Diversity Index No. of Taxa 11 10 10 10 13 14 14 7
6 10 13 9
12 13 17 9
a Shannon-Wiener species diversity Index (Plelou, 1966).
- m...
M
h M
M E
M IE E
N N
ME M E j
l l
l Table 2.4.1 (Continued)
Page 2 of 7 Area Subimpoundment Monticello Reservof-Station H
l Taxa J
A JL 0
J F
A M
JU JL A
S O
N D
l Chlorophyta 1186 10969 2352 2863 90 284 5639 7081 2756 1092 7128 10772 2248 343 340 2992 0
0 0
0 Euglenophyta 0
84 95 160 Cryptophyta Pyrrophyta Chrysophyta 305 740 0
0 3783 0
0 0
0 0
427 86 0
p Bacillarlophyta 5354 5517 5628 8980 43421 4563 8102 8205 47842 19238 46052 8466 5709 5728 2890 7952 C
Cyanophyta 2542 0
0 0
171 4846 683 0
0 2856 12799 0
2854 Total 9387 17226 10920 24737 47294 7701 13741 15446 50598 20330 53760 19836 12889 6752 3230 10944 Blomass (mg/l) 8.3 10.0 7.6 6.7 8.6 9.9 7.0 10.6 10.1 20.3 13.0 7.5 8.1 7.8 5.4 6.6 Species Diversity Index 2.14 2.76 3.13 2.62 0.63 2.45 3.01 2.16 1.05 1.63 1.77 3.16 2.75 2.89 4.16 2.56 a
No. of Taxa 12 15 15 15 5
14 14 8
11 12 13 19 15 12 10 11
- Shannon-Wiener species diversity index (Plelou,1966).
I M
M M M 'W sm W
'M
' M M
~M MMMM Table 2.4.1 (Continued)
Page 3 of 7 Area kbnticello Reservoir Station J
K Taxa J
A JL 0
J F
M A
M JU JL A
S O
N D
Chlorophyta 505 14174 7311 170 477 1451 6761 15083 14024 9309 2142 6241 4869 04 680 259 Euglenophyta 412 0
0 587 0
85 885 0
Cryptophyta Pyrrophyta Chrysophyta 0
0 510 0
0 70 0
65 115 659 85 530 0
Bacillarlophyta 44155 18166 92160 2820 42617 12501 11154 15477 34481 38511 6185 7097 3010 2365 5271 6057 Cyanophyta 0
0 256 0
25 0
0 0
85 2657 84 85 0
I" s~
Total 44660 32752 99811 3246 43094 14057 17915 22130 48505 47935 8986 13593 11951 2533 6036 6316 Blomass (mg/l) 7.6 10.4 9.0 6.6 8.1 8.4 7.2 10.7 12.8 24.0 8.2 6.4 10.7 6.6 6.8 4.6 Species a
Diversity index 0.62 2.27 1.54 2.48 0.51 1.08 2.93 2.44 1.63 2.14 2.73 3.30 2.95 2.33 1.94 1.29 No. of Taxa 8
13 12 9
7 13 14 17 11 16 14 19 14 8
11 4
ll l
a Shannon-Wiener species diversity index (Plelou, 1966).
i i
$M
& & & '& W M
M
&M S
S
'M S
Table 2.4.1 (Continued)
Pajo 4 of 7 Area Monticello Reservoir Station L
Taxa J
F M
A M
JU JL A
S O
ft D
Chlorophyta 404 566 1681 15486 576 16 6 4753 830 2052 252 65 860 Euglenophyta 303 164 0
170 0
Cryptophyta Pyrrophyta Chrysophyta 0
0 0
0 0
655 83 0
0 Bacillarlophyta 38763 10269 7112 12369 25981 2739 52959 3154 1965 1008 1403 2925 Cyanophyta 202 496 0
0 0
0 0
0 0
0 i
G Total 39369 11331 8793 28158 26557 2905 58531 4067 4187 2160 1438 3785 Blomass (mg/l) 7.9 8.7 6.1 12.9 13.3 18.5 13.7 8.1 9.6 5.2 7.4 7.3 Species a
Diversity Index 0.59 1.86 2.77 2.64 0.97 0.99 1.64 2.72 3.01 2.28 0.63 2.07 No. of Tax-8 12 13 17 10 4
17 11 12 7
3 7
a Shannon-Wiener species diversity Index (Plelou,1966).
1
e W
M M
EW "M
W M
'M M
M M
M M
M F
E Table 2.4.1 (Continued)
Pogu 5 of 7 i
Area Monticello Reservoir Stat ion M
i Taxa J
F M
A M
JU JL A
S O
N D
i Chlorophyta 95 320 5845 5152 327 412 2324 854 870 510 64 170 Eug lenophyta 0
0 0
0 0
Cryptophyta
)
Pyrrophyta Chrysophyta 0
71 0
0 0
415 0
0 255 t
N l
Bacillarlophyta 28351 10807 7540 9425 15404 9485 20085 1965 957 1785 588 2210 i
4 j
g Cyanophyta 0
535 572 82 0
598 261 170 0
1190 f
Total 28466 11733 13385 14577 16303 9979 22824 3417 2088 2720
<>72 3570 Blomass (mg/l) 12.6 12.7 9.6 13.1 14.6 27.4 13.1 7.1 6.6 6.4 7.3 6.4 Species a
Diversity index 0.42 1.73 2.79 2.24 1.72 1.60 2.08 2.90 2.47 2.50 1.88 2.07 No. of Taxa 6
15 14 9
11 9
16 10 7
7 5
5
- Shannon-Wiener species diversity index (Plelou,1966).
M h
Y O
M M
M M
S M
- M M
l l
l I
i Table 2.4.1 (Continued)
Paje 6 of 7 Area H>nticello fleservoir Station N
Taxa J
F M
A N
JU '
JL A
S O
H D
Chlorophyta 81 418 16720 14529 1384 14359 2180 11424 4153 85 340 1360 Euglenophyta 279 0
0 86 0
Cryptophyta Pyrrophyta Chrysophyta 0
0 0
69 0
323 0
86 0
c Bacillarlophyta 39351 8378 12097 7609 29328 26305 17888 3696 2681 2805
% 51 1445 Cyanophyta 0
34 0
0 0
420 778 0
0 0
Total 39432 8830 28817 22486 30712 40664 20391 15540 7784 2090 6291 2035 Blomass (mg/l) 9.2 8.1 6.7 14.0 18.4 22.9 10.8 9.9 7.9 3.3 6.5 5.5 Speci es a
Diversity Index 0.49 1.20 2.42 1.78 0.83 2.54 1.43 3.28 3.18 1.47 1.32 1.76 No. of Taxa 6
9 12 11 10 18 13 16 15 4
6 6
a Shannon-Wiener species diversity index (Plelou,1966).
M M
'M M M Is "M
MM MMM M M M M Table 2.4.1 (Continued)
Paga 7 of 7 Area Monticello Reservoir Stat ion O
Taxa J
F M
A M
JU JL A
S O
N D
Chlorophyta 61 790 7035 54s4 3196 6t1 6678 10817 3613 513 171 1275 Euglenophyta 347 0
338 516 0
Cryptophyta Pyrrophyta Chrysophyta 0
68 0
0 85 814 338 172 85 l
Bacillarlophyta 35942 9804 6073 8876 57555 12242 62740 2535 4042 2821 3335 1105 i
E Cyanophyta C
1720 0
0 0
0 1635 170 0
0 Total 48674 12382 13108 14677 60832 13007 70232 14028 9978 3589 3506 2380 Blomass (mg/l) 8.3 8.6 8.4 12.0 12.4 22.7 13.3 9.2 6.0 7.5 5.8 6.9 Species a
Diversity inden 1.06 2.26 2.63 2.65 0.84 1.49 1.22 2.86 3.04 2.76 0.99 1.92 No. of Taxa 7
16 10 13 11 11 13 13 15 10 5
6
- Shannon-Wiener species diversity index (Pietou, 1966).
I 2.5 ZOOPLANKTON 2.5.1 Introduction Zooplankton form the animal constituent of the plankton community.
These organisms are primary consumers which feed directly on the pu phytoplankton and form a portion of the food chain base for the higher organisms.
Replicate samples of zooplankton were collected in January, April, July, and October 1981 at the aquatic biology stations indicated in Figure 2.1.1, Organisms were identified to the lowest practicable I,
taxon and enumerated for each replicate. The findings were averaged for each station and collection period and summarized in Table 2.5.1.
l In presenting these findings, quantitative comparisons were made
,I between stations for number of taxa, densities, distribution of the taxa within the four major sampling areas, and species diversity. Taxa comprising 10 percent or more of the collection were considered codom-1 inants in the community. The species enumerated from the samples were 1
l referenced to two crustacean orders, Cladocera and Copepoda, and the phylum, Rotatoria (rotifers). Unidentified eggs and other immature l
stages of zooplankton, excluding copepod, naupliar, and copepodite
)
forms, were omitted from these analyses.
1 2.5.2 Findings and Discussion Parr Reservoir The biological survey conducted in Parr Reservoir included the collec-( y tion of zooplankton at three stations (Figure 2.1.1).
The average density for total zooplankton, obtained from the mean densities of all three sampling locations, ranged from 5.03/ liter in January to 31.78/
liter in April. The largest mean density occurred at Station C during l
each of' the four sampling periods. Highest total numbers at Station C
- 3 i
2.5-1
E I
during April (37.74/ liter) were concurrent with the greatest densities (31.36/ liter) for members of the phylum Rotatoria observed from Parr Reservoir samples.
I Community composition was generally similar for the four sampling periods. The rotifers were the most abundant organisms identified and I
enumerated from samples collected at the three stations. These zooplankters accounted for an average of 80 percent of the total zooplankton community for the four collecting periods. During 1980, rotifers also predominated in the January, April, July, and October collections, comprising an overall average of 74 percent of the total zooplankton community (Dames & Moore, 1980). According to Chengalath, I
al. (1971), the rotifers are perhaps the most common animals found et in standing waters, and, in many cases, constitute the numerically l
dominant fauna in zooplankton.
The mean relative abundance for copepods and cladocerans represented approximately 15 and 5 percent of the total zooplankton community, respectively. The highest number for copepods, 4.60/ liter, was l
l recorded during April at Station C.
Cladoceran densities were generally low and ranged from 0.10/ liter at Station D during January l
to 1.78/ liter at Station C in April.
l.I For the four sampling periods, the overall codominant zooplankton l
species recorded from Parr Reservoir samples were the rotifers Polyarthra sp., Synchaeta sp., and Keratella cochlearis and the copepod l
nauplii. These taxa were also the most numerous zooplankters collected I
at all three sampling locations in January, April, and October 1980 (Dames & Moore, 1980). Additional codominant species of the present B
study were: Asplanchna sp. at Station C during April and Bosmina l
longirostris at Station D during July.
Several other species, although less abundant, occurred at all three stations. The mean number of taxa collected was 15 in January, 11 in I
2.5-2 i
t I
April, 20 in July, and 15 in October; the range was from 10 in April to 23 in July at Stations B and D, respectively. Similarly, the Shannon-Wiener diversity values ranged from 2.21 in April to 3.27 in July, at Stations B and D, respectively.
I Zooplankton biomass was determined for all sampling periods, with values averaging 0.028 mg/ liter for January, 0.004 mg/ liter for April, 0.004 mg/ liter for July and 0.005 mg/ liter for October samples. The greatest biomass was measured at Station D (0.031 mg/ liter) during January.
E Neal Shoals I
Zooplankton samples were collected from one station (Figure 2.1-1) in the Neal Shoals Dam area. N e mean density for total zooplankton in-creased from low levels in January (0.47/ liter) and April (1.81/ liter) to 241.00/ liter in July before declining to 60.72/ liter in October.
The high densities observed during July were the largeat recorded for j
the 12 stations sampled during the 1981 survey.
I The rotifers were the most abundant organisms observed, accounting for 93 percent of the total zooplankton community for the four collecting I
periods. These zooplankters also precominated in the samples collected l
during 1980, comprising an average of 82 percent of the total zooplank-ton coc:munity (Dames & Moore, 1980).
Species of Cladocera and Copepoda were observed in all samples during the collecting periods, except in January when cladocerans were not i
present in the samples. Their densities, however, were generally low l
W and comprised approximately 1 and 6 percent, respectively, of the l
zooplankton community for the 1981 survey. Copopods were highest in densities during October (14.38/ liter) and accounted for almost 24 per-cent of the collection for that month.
I I
2.5-3 I
I I
Codominant taxa recorded from samples collected at the station were the rotifers: Synchaeta sp., Keratella cochlearis, and Polyarthra sp.
during January; Polyarthra sp. and Synchaeta sp. during April; I
Brachionus angularis, Asplanchna sp., and Filinia longiseta during July; and Synchaeta sp., Conochilus unicornis, and Polyarthra sp.
during October. During an earlier study conducted in 1980, these I
rotifers (with the exception of B_. angularis) were also observed as codominants (Dames & Moore, 1980). Although B_. angularis was recorded only from the July collections of the present study, the mean density of this rotifer was the highest reported for any taxa for the 12 stations sampled during the survey.
In addition, the copepod nauplii were codominant in January, April, and October.
The number of ta_xa collected during January, April, July, and October were 12, 13, 16, and 11, respectively. During the previous year, collections yielded 22,18, 20, and 13 taxa from the four sampling '
periods.
I During the 1981 study, zooplankton species diversity ranged from 2.11 l
l during April to 2.76 in January. Diversity values recorded during 1980 l
W ranged from 2.24 in October to 3.06 in July. Diversity values reported i
l in July (2.52) and October (2.40) during 1979 were the lowest reported for the entire study. area (Dames & Moore, 1979 ).
l l
Zooplankton biomass for 1981 was 0.005 mg/ liter in January, 0.006 mg/ liter in April, 0.G37 mg/ liter in July, and 0.016 mg/ liter in October. The values recorded at this station were comparable to those t
recorded in Parr Reservoir during April, but were much higher during July and October; they were somewhat lower during January (Dames &
B Moore, 1981).
E 5
l l
I 2.5-4
I Subimpoundment The average density for total zooplankton collected ranged from 3.55/ liter in July to 111.31/ liter during April. Mean densities for the rotifers and copepods accounted for approximately 83 and 14 per-I respectively, of the total zooplankton community for the four
- cent, sampling periods. Mean densities for the cladocerans ranged from 0.01/ liter during July to 5.26/ liter in April. The densities obtained for the cladocerans never represented more than 5 percent of the total zooplankton community for each sampling period.
I Codominant taxa observed in samples collected from the subimpoundment I
were the rotifers:
Polyarthra sp., Keratella cochlearis, and Kel-licottia bostoniensis during January; K_. cochlearis and Conochilus unicornis during April; Brachionus angularis, and Synchaeta sp. during i
July; and Polyarthra sp., Synchaeta sp., and C_. unicornis during l
October.
' I During previous investigations conducted in 1980, K_. cochlearis and the l
copepod nauplii were the codominant taxa for the four sampling periods (Dames & Moore, 1980).
K. cochlearis alone comprised 50 percent of the I
zooplankton recorded from samples collected in July 1979 (Dames &
3 Moore, 1979a). In the present study, K,. cochlearis accounted for 60 percent of the April collection. According to Stemberger (1979)
Keratella is perhaps the most common limnetic rotifer in fresh water.
l The number of taxa collected during January, April, July, and October was 17, 15, 12, and 13, respectively.
Zooplankton species diversity was highest in January (2.75).
The l
lowest diversity in the subimpoundment occurred in July (1.42); this was also the lowest value reported for the entire study area for all four sampling periods.
3
.g 2.5-5
~
i t
I Biomass was determined for all sampling periods and was highest in April (0.016 mg/ liter). The high volume coincides with phytoplankton productivity associated with fertilization of the subimpoundme.st.
Monticello Reservoir I
Zooplankton samples were collected from Monticello Reservoir at seven stations (Figure 2.2.1) during the four sampling periods. The average density for total zooplankton, obtained from the mean densities of all seven sampling locations ranged from 1.84/ liter during October to 32.94/ liter in April. Mean densities for individual sampling stations ranged from a low of 1.24/ liter at Station L in October to a high of I
60.25/ liter at Station N during April. The cunulative average densities of major taxa among the seven stations sampled were highest l
for the rocifers, cladocerans, and copepods during April.
The rotifers were the most numerous zooplankters in samples collected during January, April, and July. The greatest density observed for l
these individuals, 49.36/ liter, was recorded at Station N in April.
l Overall, the occurrences of the rotifers represented an average of 65 percent of the total zooplankton community for the four sampling periods.
I Average densities for the two crustacean orders, Copepoda and Cladocera, accounted for 26 and 10 percent, respectively, of the total zooplankton identified from the Monticello Reservoir samples. During July and October, however, the copepods comprised 42 and 59 percent, respectively, of the total zooplankton population.
l l
The codominant taxon which was observed in all sampling periods was the copepod nauplii. This taxon alone accounted for' 38 and 43 percent of the total zooplankton community during July and October, respectively.
Additional codominant taxa for individual sampling periods were:
Synchaeta sp. and Keratella cochlearis during January; Polyarthra sp.,
2.5-6 g
I I
Synchaeta sp., Asplanchna sp., and B_. longirostris during April; K_.
I cochlearis and Polyarthra sp.
during July; and B_. longirostris during October.
In addition to these codominants, several species were frequently observed throughout the samples collected in the Monticello Reservoir, although in lower overall densities. The number of zooplankton taxa enumerated at the sampling stations ranged from:
9 to 17 during January; 11 to 15 during April; 17 to 22 during July; and 13 to 17 during October.
I Zooplankton species diversity ranged from 2.19 during July to 3.11 in October, both extremes occurring at Station 1.
Overall, however, the average species diversity was slightly higher in April (2.62) than in January (2.50), July (2.49), and October (2.56).
Values for biomass were higher during January, averaged 0.023 mg/ liter I
and ranged from 0.013 mg/ liter at Station 0 to 0.037 mg/ liter at Station K.
l 2.5.3 Summary The zooplankton communities observed during January, April, July, and October 1981 did not indicate any unusual trends. Based on assessments t
of taxonomic composition, de..sities, distribution among the stations, I
and species diversity, these zooplankton populations appeared to be l
l progressing through normal seasonal changes. The species composition i
of zooplankton at the twelve stations in the study area was similar to that reported during the 1978, 1979, and 1980 investigations. The rotifers were, overall, the dominant organisms collected during this I
study these organisms are characteristic of limnetic habitats such as l
that found throughout the study area. 'The distribution of taxa indicated that generally stable zooplankton communities exist. The frequency of zooplankter occurrence at the various stations indicated 2.5-7 e
e.:.a e
,e E
W
- s..s that few dif ferences seemed to occur within each major study area, particularly Parr and Montic'ello Reservoirs. Overall densities and taxonomic diversities at the stations for all areas did not appear to
.}
change significantly from previous years.
I I
I I
l l
4 l3
.\\
.I
.~
+.
n l m I g 1
- g
\\
k 2.5-8 L
M' M
M M
M M
M M
M M
M M
M W
W M
E t
i
/
r 9
Zooplanktor collected in January, Aprli, July, an[0ctober 196'!, represented by numbers of organisms per major taxonomic category Table 2.5.1 a
3 b
species divarsity, and blomass.c e
~
Page 1 of 2
\\_
a e
7 E of Neal.
Sub-I or Area Parr Reservoir 0-0 Shoals f.+o un dmen t h *icello Reservoir 1-0 Stat ion B C
0 P
H
~
~
I J
K L
M N
O January
~
O~
Hota toria 3.34 5.13
- 3. 7.1 4.07 3.36 -
II.05 4.05
- 2. 89 4.70 1.42 2.89 2.20 1.68 2.78 Cladocera 0.27 0.12 0.10 0.16 A.00 x
0.37 0.81 0.44 0.09 0.08 0.08 0.14 0.10 0.25 Copepoda 0.85 0.69 0.88 0.80 0.09
'?. 38 0.62 0.30 0.88 0.25 0.59 0.45 0.31 0.49 Total Density 8 :.'3 5.93 4.70 5.03 0.47 19.80
,5.48 3.23 5.67 I.75 3.56 2.78 2.10 3.51 Total Taxa 13 13 19 15 12 17 12 14 9
15 15 13 17 14 Seecles Diversity 32.65 2.47 2.65 2.59 2.76 2.75 2.27 2.23 2.39 2.64 2.52 2.67 2.81 2.50
^
, 140 mass t.029 0.024 0.031 0.028 0.005 0.006 0.025 0.028 0.037 0.015 0.023 0.022 0.013 0.023
- u April ne Rotatoria 28.32 ' 31.36 19.06 26.25 0.99 94.09 6.F 14.03 38.16 14.9 5 22.76 49.36 14.07 22.76 Cladocera 1.74,
1.78 1.02 1.15 0.04 5.26 5.
5.81 1.99 2.34 1.89 5.01 2.45 3.59 Copepoda 3.96 4.60 3.51 4.02 0.78 11.95
- 7. t.
13.95 4.82 4.48 3.77 5.88 5.5B 6.59 Total Donsity 34.02 31.74 4L60 31.78 1.81 111.31 19.32 33.79 44.97 21.76 28.41 60.25 22.10 32.94 Total laxa 10 13 11 11 13 15 15 15 11 14 13 13 13 13
~
Species Diversity 2.21 2.50 2.24 2.32 2.11 2.06 2.67 2.90 2.38 2.73 2.54 2.42 2.69 2.62 biomas s 0.002 0.007 0.004 0.004 0.006 0.016 0.011 0.013 0.011 0.005 0.005 0.011 0.005 0.009 i
I
m M
M M
M M
m e
e e
e m
e me e
m s.
Tablo f. 5.1 (Continuedl Poju 2 of 2 i of Neal Sub-E of Area Parr Reservoir B-0 Shoals impoundment
- Monticello Reservoir j --L Station B C
D P
H I
J K
L H
N O
~
hly
~
~
~
~
~
~
~
~
~
~
Rotatoria 2.66 17.24 0.71 6.87 235.73 3.51 13.54 6.65 II.18 1.97 1.91 2.38 1.54' 5.60 Cladocora 0.80 0.86 0.23 0.63 3.44 0.01 0.37 0.35 0.47 0.72 0.55 0.81 0.48 0.49 Copopoda 3.32 2.12 0.44 1.96 1.84 0.03 8.73 7.31
- 2. 56 3.16 1.95 4.46 2.91 4.41 Total Density 6.79 20.21 1.39 9.46 241.00 3.55 22.64 14.32 13.72 5.58 4.41 7.65 4.94 10.50 Total Taxa 20 16 23 20 16 12 17 22 19 18 18 19 20 19 Species Diversity 2.81 3.23 3.27 3.10 2.40 1.42 2.19 2.38 2.55 2.54 2.62 2.58 2.57 2.49 Blomass 0.007 0.005 0.001 0.004 0.037 0.009 0.004 0.004 0.005 0.002 0.003 0.006 0.001 0.004
,N October Y Rotatoria 1.18 30.16 4.50 11.95 46.04 20.12 0.67 0.33 0.36 0.26 0.36 0.42
.0.24 0.38 b
Cladocera 0.21 0.67 0.55 0.47 0.30 0.07 0.29 0.31 0.40 0.21 0.64 0.35 0.48 0.38 Copepoda 0.83 4.22 2.17 2.41 14.38 0.72 0.87 0.66 1.59 0.76 1.51 1.09 1.11 I.08 Total Density 2.22 35.05 7.21 14.83 60.72 20.91 1.82 1.30 2.35 1.24 2.51 1.87 1.83 1.84 Total Taxa 15 16 15 15 11 13 17 17 13 14 14 15 15 15 Spocles Diversity 2.72 2.33 2.62 2.56 2.60 1.97 3.11 2.79 2.38 2.52 2.20 2.45 2.45 1.%
Blomass 0.003 0.003 0.008 0.005 0.016 0.002 0.001 C.001 0.001 0.0004 0.001 0.001 0.001 0.0009 a Counts are in numbers of organisms per liter.
b Shannon-Wienor spectos divorsity index (Plelou 19661.
c Blomass is in ag/lltor of ash-froo, dry wolght.
I 2.6 ICHTHYOPLANKTON t
2.6.1 Introduction i
Ichthyoplankton, comprised of the egg and larval component of the ichthyofauna, are of fundamental importance in assessing fishery I
success for two reasons:
1.
Ichthyoplankton are the products of a species' reproductive efforts; therefore, ichthyoplankton abundance and survival bear directly on the reproductive success o' a species.
I Ichthyoplankton, particularly of forage species such as giz-2.
zard shad, provide a valuable food resource to a number of desirable fish species.
In temperate a.eas, most spawning takes place in spring and summer; therefore, ichthyoplankton are collected most abundantly in these seasons. The presence of early life history stages of fish often indicates that a water body is being used as a nursery and/or nursery i
1 l
area by adult fish.
l Because of their limited mobility, eggs and larvae are particularly i
susceptible to being affected by the operation of power generating sta-tions. These effects, which are dependent on specific engineering variables, include impingement upon water intake structures, entrain-ment through condenser cooling systems, and entrainment in the heated l
effluents discharged during power generation (Battelle, 1974). Thermal stress can kill organisms (Marcy, 1971; 1973), weaken them and thus I
make them more vulnerable to predation (Schubel et al., 1978), or, in the case of eggs, cause abnormal development of the embryo which often results in death soon after hatching (Koo and Johnston, 1978). Mechan-ical stress can also weaken or kill exposed organisms (Marcy, 1973).
I 2.6-1 2
I I
Ichthyoplankton samples were collected throughout 1981 at eleven sca-tions:
two stations in Parr Reservoir (Stations B and C), one control station in the Broad River upstream from Neal Shoals Dam (Station P),
one station in the subimpoundment of Monticello Reservoir (Station H),
and seven stations in Monticello Reservoir (Stations I, J, K, L, M, N, and 0).
Collections were made at the surface and at mid-depth at all I
stations except C (Parr Reservoir) and P (Neal Shoals). At these two stations, only surface samples were taken because of the she.llow water.
Data provided by these sampling efforts are described below for each of the four study areas (Sectior _.a.2) and then related to the present and developing fisheries in these areas (Section 2.6.3).
The following I
characteristics are dese: bed by these data:
- 1) species composition,
- 2) relative abundance, 3) spatial distribution and frequency, and
- 4) temporal distribution.
2.6.2 Findings Mean monthly ichthyoplankton densities are presented in Table 2.6.1 for March through Sepcember 1981. No ichthyoplankton were found in samples collected in January, February, October, November, or December of 1981.
Parr Reservoir Two distinctly different habitats were sampled in Parr Reservoir.
l N
Station B is located in the tailrace canal for the FPSF and is subject to high velocity and scouring currents. Most ichthyoplankton found at I
Station B were probably derived from Monticello Reservoir via the FPSF.
In contrast, Station C is in a cove formed by the mouth of Cannons Creek. This protected area harbors a resident larval fauna.
il i,
2.6-2
I At Station B, patterns of increase and decline followed those of Monticello Reservoir. This is to be expected because most larvae collected at Station B probably come from Monticello Reservoir via the FPSF. Clupeids were the most abundant larvae collected; second in abundance were sunf'ishes. Clupeid densities reached 67.6/100 m, and 3
3 total sunfish abundance did not exceed 2.4/100 m. Densities for I
these predominant organisms were highest in May and showed a declining trend in June, July, and August. Other taxa collected at Station B included minnows (Cyprinidae), suckers (Catostomidae), white bass, crappie, and darters. Mean monthly densities for each of these taxa 3
never exceeded 1.6/100 m. Larval fish were first collected at Station B in April and included catostominae, Morone spp., and I
clupeids.
At Station C, the highest monthly mean densities collected in 1981 3
3 occurred in May (150.3 larvae /100 m ) and June (152.2/m ), and consisted mostly of clupeids (144.9 to 146.1/100 t.t3) dbring these respective months.
Other taxa which were collected at Station C during May and June included minnows (Cyprinidae), crappie (Pomoxis spp.), temperate bass i
(Morone spp.), and sunfishes (Lecomis spp.) and an unidentified centrarchid. Moderately high clupeid densities initially occurred at 3
Station C in April (97.4/100 m ),
then peaked in May and June.
In July, clupeid abundance declined to less than 1.3/100 m3 and in August, clupeids failed to appear in the samples. Sunfish (Lepomis spp.) followed the same relative trend April through August; densities peaked in April then declined in May and occurred sporadically in June, l
1 l
July, and August. Lepomis spp densities did not exceed 2.6/100 m.
3
[
Darters (Percidae) were the first larvae obtained from the entire study area, appearing in March.
?I l.
2.6-3 l LI
I I
Neal Shoals Neal Shoals, Station P, is a control station removed from the influence of the FPSF and its attendant fluctuations in water level. Two peaks in larval densities were observed at Neal Shoals in May and July. The first peak was produced as a result of the presence of numerous I
3 clupeids (158.7/100 m ) and the second peak occurred mostly because 3
of the abundance of Lepomis spp. (132.1/100 m ).
Low densities of minnows, crappie, and darters were also present in these samples.
Densities declined sharply in June and August, with only unidentified 3
sunfish occurring in September (0.9/100 m ).
The larval fauna at Station P consisted of low densities, exclusive of clupeids; densities of other taxa were never greater than 4.7/100 m3, and most often were I
less than 1.1/100 m3 The less numerous taxa included darters, minnows, and crappie.
Subimooundment I
Station H is located in a subimpoundment at the northern end of Monti-cello Reservoir. The fertilization program being carried out in the subimpoundment is responsible for maximizing the development of a desirable fishery in this area. Unlike the other areas studied, clupeids were not the numerically predominant larval fish collected from the subimpoundment.
In April, the first taxa collected were crappie and clupeids, both taxa being comprised of similar numbers, 17 l
to approximately 23/100 m3 in surface collections.
In May, very few crappie were taken in collections, but sunfish larvae were present in 3
moderate abundance (maximum 26.9/100 m ) in surface and mid-depth samples. Maximum clupeid density reached 220.2/100 m3 at mid-depth, and clupeids were present in moderate aoundance at the surface (29.1/100 m ). Sunfish abundances increased to even higher levels in 3
3 June (mean at surface was 86.3/100 m ; mean at mid-depth was 6.0/100 3
3 l
m ) while clupeid densities declined to only 1/100 m. Sunfish l
1 -
2.6-4 l
1
4 I~
I abundance in August.
In most months, there was a noticeable trend for sunfish to be more abundant in surface samples.
Monticello Reservoir The seven stations (I, J, K, L, M, N, and 0) sampled in Monticello I
Reservoir were all located in open water, as opposed to protected coves, and were sampled at both surface and mid-depth. For the reservoir as a whole, larval fish first appeared in April with 3
a mean density of approximately 10 organisms /100 m, increased in 3
abundance in May to 50 organisms /100 m, then decreased from June through September from 30 to less than 1 organism /100 m3 From April I
through July, all stations collectively showed higher larval fish densities in surface samples. The frequency of taxa occurring in 84 possible surface and mid-depth samples from April through September ranged from one for Ictaluridae (catfish) to 55 for Clupeidae. The next most frequently occurring taxa were Lepomis spp. (35), Percidae (19), and Cyprinidae (14), and suckers, Morone spp., and crappie (from 6 to 9 occurrences each).
I Densities of larval fish at all stations, except Station L, increased in May and decreased in June with clupeids dominating the collections.
I At Station L, the highest ichthyoplankton density occurred in Jurie, 3
119.0/100 m, with clupeids being the most abundant group. In May, 3
the highest density, 111.3/100 m, was found in i.Jrface samples at 3
Station M; the lowest, 12.2/100 m, was foun t at mid-depth at Station L.
Densities at both surface and mid-depth were atypically low at Station L in May.
Averaged surface and mid-depth densities of clupeids i
were statlar in May and slightly higher at the surface than at mid-I depth during June for all stations. Other taxa collected during May and June generally did not exceed 2.0/100 m3 and included crappie, suckers, darters, cyprinids, and white bass, which were generally more numerous in May than June.
In June, total densities declined, asso-ciated with a decline in clupeid abundance, while a general increase il 2.e-5 1
I I
in sunfish abundance was noted. Percidae frequency and abundance decreased significantly from May to June. Sunfish were generally dis-tributed evenly in both the surface and mid-depth samples.
I In July, densities continued to decline with no station having a mean monthly density higher than 10/100 m3, and most showing densities I
3 less than 3/100 m. Sunfish and clupeids were the most abundant larvae collected at all stations, with average clupeid density being slightly higher. Additional taxa collected in July included minnows and unidentified Centrarchidae.
In August, averaged densities were the lowest recorded during 1981, and only two taxa, sunfish and clupeids, were collected. Sunfish were the most abundant at Stations I, J, K, L, I
and M.
Clupeids occurred only at Stations K and M.
The highest mean larval fish density in August was recorded at Station L, mid-depth 3
3 (6.4/100 m ) and Station M, surface (6.1/100m ).
The only Ictaluridae to be collected in the entire study area were present in the September samples at Monticello Reservoir, Station M, mid-depth, 3
their density was less than 1 organism /100 m,
2.6.3 Discussion A rather typical ser.aonal succession of fish larvae was observed in the y
study area during 1981. The first larvae to appear were the Percidae, then crappie, clupeids, temperate bass, and minnows, followed by.un-fish and suckers and, finally, by ictalurids. This succession is expected, based upon available information on preferred spawning temperatures of the adult fish of these taxa.
Shallow water areas, especially Stations C and P, with morphometric I
features conducive to influencing increased water temperature, were the first to produce relatively high abundances of larval fish.
(This com-parison excludes the artificially enhanced fishery in the subimpound-ment.) The reason for these areas to produce larval fish early in the season was likely due to a rapid but stable increase in water temper-ature in these shallower, protected areas, resulting in the earlier 2.6-6 LI
I I
attainment of preferred spawning temperatures. The earlier occurrence of percid larvae in March, and the higher larval fish densities in samples collected during April, indicated earlier spawning activity in 1981 than in 1980. During the 1981 sampli7g program, overall monthly larval fish densities peaked higher than 1980 densities in Menticello I
Reservoir. This could possibly indicate more favorable environmental conditions for fish and fish spawning and rearing.
Each of the four major study areas (Parr Reservoir, Neal Shoals, the subimpoundment, and Monticello Reservoir) harbored distinct larval fish communities for the sampling periods during 1981.
Parr Reservoir was composed of 8 ichthyoplankton taxa comprised pre-dominantly of Clupeidae, Lepomis spp., and Cyprinidae. The ichthyo-plankton community at the Neal Shoals Dam statica was composed of 6 I
taxa comprised predominantly of Clupeidae, Lepomis spp., and Percidae, while Monticello Reservoir samples were composed of 10 taxa made up mostly of Clupcidae, Morone spp., Lepomis spp., Catostomidae and Percidae. The subimpoundment contained 3 larval fish taxa and, ranked in order of high to low abundance' included Clupeidae, Lepomis spp., and Pomoxis spp. Overall, the number of larval fish taxa collected monthly was lower at Neal Shoals than at Parr Reservoir; was the highest at I
Monticello Reservoir, and the lowest at the subimpoundment. Compara-tively, the subimpoundment had the highest average larval fish density, Neal Shoals was second, Parr Reservoir third, and Monticello Reservoir was fourth. This presently makes the subimpoundment the most produc-tive and, in part, verifies the success of SCWMRD program to establish a recreational fishery here. The moderately high densitier and variety I
of larval fish collected from Parr Reservoir and Neal Shoals reflect their relative mature development. The overall low densities in Mon-ticello Reservoir likely reflect it being a new impoundment and a less developed ecosystem, while that of the subimpoundment has obviously 1
2.6-7 I
I I
been artificially enhanced for high productivity of fish nd other types of aquatic life.
I Further evaluation of larval fish distributed among Monticello Reser-voir stations showed that the greatest number of taxa was collected during 1981 at Stations K, L, and M.
This high diversity may be due in I
part to the relatively shallower, somewhat protected environments at K and M compared to the other stations in the reservoir. The overall favorable larval fish diversity at Station L is likely affected by the FPSF. Thus, larvae from nearby habitats of Parr and Monticello Reser-voirs, may be carried into the sampling area, potentially increasing the number of taxa collected here.
Sunfish populations in Monticello Reservoir during 1981 were relatively low considering the numerically I
abundant adult population. Lower densities of sunfishes may be due to fluctuating water levels in Monticello, caused by the operation of the FPSF, which interferes with reproduccion by nest bt.ilding species such as centrarchids. Snyder (1971) found that only a limiced area was used by nest builders in another pumped storage facility with similar fluc-tuations in water level.
It is also possible that these species are missed because areas where they are likely to occur most abundantly are 8
not sampled, such as the numerous protected and shallow areas of the many coves around the periphery of Monticello Reservoir.
The abundance of clupeid larvae in nearly all areas of'Monticello Reservoir provides a valuable food resource to several recreationally important species (largemouth bass, crappie, and white bass) which, I
both as larvae and adult, prey upon the larvae of forage species such as gizzard shad (Clark and Pearson, 1979). This may be especially true for the recreational fishery in Monticello Reservoir where the greatest potential for increasing fish populations probably exists.
The trends evident in t'.s 1981 data are quite similar to those observed in previous years (Dames & Moore; 1978, 1979, 1979a, 1980). The early peaks in densities at Stations C and P in 1981, although varying in 1
l 2.6-8 i
I I
time by several weeks, were apparently the result of an unusually warm I
period in early spring at favorable environmentally oriented stations.
Clupeid larvae were more abundant throughout the study areas in 1981 than in previous years. Steady increases in most other larval fish diversities and overall abundance are also evident from data from I
Monticello Reservoir. This trend should continue until Monticello Reservoir approaches maturity.
I 2.6.4 Summary A typical succession of larval fish species was observed in the study area in 1981. Percidae were the first taxa to appear in March and clupeids the first to occur in notable abundance. The presence of these taxa was followed by that of crappie and sunfish.
I Except for the subimpoundment, clupeids dominated collections in all areas. The numerical abundance and wide distribution of clupeids in the study alrea make it an important forage fish which provides a valuable food resource to some of the recreationally important fish species present in the area.
In the subimpoundment, sunfish and crappie were proportionally more abundant than in other collections; g
this is presumed to be the result of directed management of this water M
body for recreational fishing. The subimpoundment also had the highest overall larval fish d2nsities. Parr Reservoir and Neal Shoals produced the highest densities of clupeid fish but also maintained a relatively diverse larval fish assemblage among areas sampled. Total larval fish densities were moderatelf high, with the lower densities observed in Monticello Reservoir and highest densities in the subimpoundment.
I Monticello Reservoir showed the greatest overall increase from 1980 in larval fish diversity, alt' ough overall abundance was lowest compared to Parr Reservoir, Neal Shoalc, and the subimpoundment during 1981.
Parr Reservoir and Neal Shoals showed some characteristics typical of a mature fishery whereas Monticello Reservoir was typical of a naturally I
2.6-9 LI
I developing fishery and the subimpoundment of an enhanced or managed I
fishery.
E I
I I
I I
E I
l i
I I
I I
lI ll 2.6-10
N E
N E
'M M
M m
e m
e e
e W
mW W
m m
3 Table 2.6.1 Mean nonthly densities of larval fish (number /100 m ) collected in not tows, Mard through Septenber 1981.
Page 1 of 7 Neal Sub-MARCH 1981 Area Parr Shoals Impoundment Monticello Scientific Name Common Name
~Ca
~pa
~
I
~
~
~
~
~
~
Station B H
J K
L M
N O
Dorosoma spp.
Herring Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Clupeldae, Unid.
Herring Sfc Mid
(-3
(-1
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Cyprinus carplo Carp Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Cyprinidae Minnows Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Catos tominae Suckers Sic Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Catostomidae, Unid.
Suckers Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
to cn Morone spp.
Temperate bass Sic 8
Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Lepomis spp.
Sun f ish Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
P moxis spp.,
Crappl e Sfc o
Mid
(-)
(-)
(-)
(-)
(-1
(-)
(-)
(-)
(-)
(-)
(-)
Centrarchidae, Unid.
Sunfish Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Percidae Darters Sfc 1.0 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Damaged, Unid.
Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Total Sfc 1.0 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Note: Sfc = Surface Samples; Mid = Hid-depth a Only surface samples taken at Stations C and P
W W W M
M M
eeeee ee mee Ttble 2.6.1 (Continued)
Paje 2 of 7 Neal Sub-APRIL 1981 Area Parr Shoals impoundmont Monticello Scla,ntIfIc Name Common Namo
-Ca
~pa
~~
~~
Station B n
g J
K l.
M N
O Dorosoma spp.
Herring Sfc HId
(-)
(-)
(-)
(-)
( -)
( -)
(-)
(-1
(-)
(-)
(-3 Clupoldae, Unid.
Herring Sfc 5.3 97.4 18.7 17.4 3.4 6.1 16.3 12.4 3.2 3.2 Mid (7.8)
(-)
(-)
(20.0)
(0.9)
(6.1)
(13.2)
(1.4)
(15.0)
(4.3)
(1.9)
Cyprinus carpio Carp Sfc 1.1 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Cyprinidae Minnows Sfc 2.0 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
( -)
(-)
Catos tominae Suckers Sfc 0.9 0.9 Mid
(-)
(-)
(-)
(-)
(-)
( -)
(-)
(-)
( -)
(-)
(-)
Catostomidae, Unid.
Suckers Sfc 5.6 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-i
(-)
(-)
Nrone spp.
Temperate bass Sfc 0.9 2.7 1.0 4.1 1.2 HId
(-)
(-)
(-)
(-)
(-3
(-)
(-)
(-)
(-)
(-)
(4.4) m 1
Lepomis spp.
Sunfish Sfc 2.6 N
Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-1 Pomoxis spp.,
Crapple Sfc 1.5 22.8 1.0 Mid
(-)
(-)
(-)
(4.4)
(2.8)
(-)
(-)
(-)
(-)
(-)
(-)
Centrarchidae, Unid.
Sunf ish Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-3
(-)
Percidae Darters Sfc 4.7 1.1 1.2 3.4 0.9 1.6 Mid
(-1
(-)
(-)
(-)
(1.3)
(-)
(-)
(-)
(-)
(-)
(-)
Damaged, Unid.
Sfc 2.4 13.5 2.0 0.9 1.1 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(1.0)
(-)
(1.2) i Total Sfc 7.1 107.5 36.9 40.2 4.5 9.3 33.4 13.6 5.0 7.0 Mid (7.8)
(-)
(-)
(24.4)
(5.0)
(6.1)
(13.2)
(1.41 (18.9)
(4.3)
( 7. 5)
Note: Sic = Surface Samples; Mid = Mid-depth a Only surf ace samples taken at Stations C and P 1
l
M M
M M
M M
M M
M M
W W
Trble 2.6.1 '(Continued)
Page 3 of 7 Neal Sub-MAY 1981 Area Parr Shoals impoundmont Manticello Scientific Name Common Name
~
~C0
~Pa
~
I
~
~
~
~
~
Stat ion B H
J K
L M
N O
Dorosoma spp.
Herring Sic 1.0 Hld
(-)
(-)
( -)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Clupeldae, Unid.
Herring Sfc 63.2 144.9 158.7 29.1 54.0 82.2 25.1 14.8 111.3 13.7 14.3 Mid (67.6)
(-)
( -)
(220.2)
(32.7)
(70.23 (51.0)
(12.2)
(82.33 (43.0)
(29.0)
Cyprinidae, Unid.
Minnows Sfc 1.1 0.8 1.0 1.3 Mid (0.9)
(-)
(-)
(-)
(-)
(-)
(2.5)
(-)
(-)
(-)
(-)
Catostomidae, Unid.
Suckers Sfc 1.2 0.9 0.9 Mid (0.9)
(-)
(-)
(-)
(-)
(-)
(-1
(-)
(0.9)
(-)
(-)
Morone spp.
Temperate bass Sfc 0.9 1.0 Mid (0.9)
(-)
(-)
(-)
(-)
(1.0)
(-)
(-)
(1.1)
(-1
(-)
Lepomis spp.
Sunfish Sfc 2.2 0.8 1.9 25.8 1.0 1.0 3.5 2.5 1.0 2.8 Mid (1.0)
(-)
(-)
(26.9)
(-)
(-)
(-)
(-)
(1.2)
(-)
(-)
,M Pomoxls spp.,
Crapple Sfc 0.9 2.9 1.0 0.9 1.5 1.3 am MId
(-)
(-)
(-)
(1.5)
(-)
(-)
(-)
(0.9)
(1.5)
(-)
(1.1) e C
Centrarchidae, Unid.
Sunfish Sic MId
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Percidae, Unid.
Darters Sfc 1.6 1.0 4.6 0.9 1.0 2.0 1.0 1.1 1.0 Mid
(-)
(-)
(-)
(-)
(1.1)
(1.0)
(1.0)
(-)
(-)
(-)
(-)
Damaged, Unid.
Sfc 2.4 1.4 2.4 1.6 3.0 1.7 2.4 2.4 1.9 Nid
(-)
(-)
(-)
(2.41
(-)
(-)
(1.2)
(-)
(1.9)
(2.4)
(1.3)
Total Sfc 72.6 150.3 165.0 57.3 62.1 88.0 28.8 21.3 119.6 20.8 20.0 Mid (71.3)
(-)
(
-)
(251.0)
(33.8)
(72.2)
(55.7)
(13.1)
(88.9)
(4 5.4 )
(31.4)
Note: Sfc = Surface Samples; Mid = Mid-depth a Only surface samples taken at Stations C and P
M M
m m
m m
a m
Ttble 2.6.1 (Continued)
Page 4 of 7 Neal Sub-JUNE 1981 Area Parr Shoals impoundment Monticello Scientific Name Common Name
-Ca
-pa g
i Station B j
g g,
y y
o Dorosoma spp.
Herring Sfc Mid
(-)
(-)
(-)
( -)
( -)
(-)
(-)
(-)
(-)
(-)
(-1 Clupeldae, Unid.
Herring Sfc 13.3 14 6.1 41.2 1.0 4.8 10.1 20.8 119.0 27.8 42.1 22.8 Mid (15.1)
(-)
( -)
( -)
(9.0)
(15.7)
(33.3)
(15.2)
(11.5)
(27.9)
(36.4)
Cyprinus carpio Carp Sfc Mid
(-)
( -)
(-)
( -)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Cyprin!dae Minnows Sfc 1.1 1.0 1.0 0.9 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(0.9)
(-)
Catos tomi nan Suckers Sfc 0.9 1.0 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
( -)
(-)
(-)
(-)
Catostomidae, Unid.
Suckers Sfc Mid
(-)
(-)
( -)
(-)
(-)
(-)
( -3
(-)
( -)
(-)
(- )
Morone spp.
Temperate bass Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
cn
)
Lepomis spp.
Sunfish Sfc 2.1 1.9 86.3 1.0 1.0 1.5 3.8 1.3 2.1 0.9 ss Mid
(-)
(-)
(-)
(6.0)
(1.1)
(0.9)
(0.9)
(-)
(1.4)
(2.4)
( -)
PomoxIs spp.,
Crapple Sfc 2.5 1.0 Mid
(-)
(-)
(-)
(-)
(-)
(-)
( -)
(-)
(-)
(-)
(-)
Centrarchidae, Unid.
Sunfish Sfc 0.8 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Percidae Darters
$fe 1.0 1.0 1.0 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
( -)
Damaged, Unid.
Sfc 1.0 0.9 1.0 1.6 1.0 Mid
(-)
(-)
(-)
(1.1)
(-)
(-)
(1.3)
(-)
(-)
(0.8)
(-)
Total Sfc 17.5 152.2 42.2 88.9 6.7 12.1 25.3 124.8 29.1 46.2 24.6 Mid (15.1)
(-1
(-)
(7.1)
(10.I)
(16.6)
(35.53 (13.2)
(12.9)
(32.0)
(36.4)
Note: Sic = Surface Samples; Mid = Mid-depth i
a Only surf ace samples taken at Stations C and P I
l
E m
e M
M M
M h
M M
M M
M M
M M
M M
Table 2.6.1 (Continued)
Page 5 of 7 Noal Sub-JULY 1981 Area Parr Shoals ppoundmont Monticello Scientific Namo Comnnn Name
-Ca pa
~
i
~
Station B il J
K L
M N
O
~
[k>rosoma spp.
Herring Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Clupoldau, Unid.
Horring Sfc 1.0 1.3 12.9 1.0 1.2 10.0 1.0 1.1 1.9 Mid (0.9)
(-)
(-)
( -)
(1.2)
(1.4)
(-)
(3.4)
(I.3)
(2.3)
(3.9)
Cyprinus carplo Carp Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
( -)
Cyprinidae Minnows Sfc 1.0 1.1 1.1 1.0 Mid
(-)
(-)
(-)
(-)
( -)
(-)
( -)
(2.3)
(1.3)
(-)
(-)
Catos tominae Suckers Sfc Mid
(-)
(-)
(-)
(-)
( -)
(-)
(-)
(-)
(-)
(-)
(-)
Catostomidae, Unid.
Suckers Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Morone spp.
Temperate bass Sfc Mid
(-)
(-!
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
i Lepomis spp.
Sunfish Sic 132.1 28.0 1.1 2.7 2.1 1.1 2.9 Mid (0.9)
(-)
(-)
(3.5)
(1.0)
(-)
(1.2)
(-)
(1.1)
(-3 (1.1) u PomoxIs spp.,
Crappl e Sfc Mid
(-)
(-)
(-1
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Centrarchidae, Unid.
Sunfish Sfc 1.0 Hid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Percidae Darters Sfc Hid
(-)
(-)
(-)
(-)
( -)
(-)
(-)
(-)
(-)
(-)
(-)
Damaged, Unid.
Sfc 0.8 2.2 0.9 1.1 1.1 1.5 1.0 Mid (0.9)
(-)
(-)
(2.7)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Total Sfc 2.0 2.1 146.1 31.2 2.3 3.6 14.3 4.2 2.6 6.8 Mid (2.7)
(-)
(-)
(6.23 (2.21 (1.43 (1.23 (5.7)
(3.7)
(2.3)
(5.0)
Note: Sfc = Surface Samples; Mid = Mid-dopth
- Only surf ace samples taken at Sta'tlons C and P
m m
m m
h M
M M
m m
m e
Ttble 2.6.1 (Continued)
Page 6 of 7 Heal Suts-AUGUST 1981 Area Parr Shoals impo undmon t Nnticello Station B H
J K
L M
N O
Scientific Name Common Name
~Ca
~pa
~
I
~
~
~
~
~
~
-Dorosoma spp.
Herring Sfc Hid
(-)
(-)
(-)
( -)
( -)
(-)
(-)
(-)
(-)
(-)
(-)
Clupeldae, Unid.
Herring Sic 0.8 Mid (1.1)
(-)
(-)
(5.4)
( -)
(-)
(1.6)
(-)
(1.2)
(-)
(-)
Cyprinus carpio Carp Sfc Mid C-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Cyprinideo Minnows Sfc 1.0 Mid
(-1
(- )
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Catostominae Suckers Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-1
(-)
(-)
(-)
(-)
Catostomidae, Unid.
Suckers Sic Mid
(-)
(- )
(-)
(-)
(-3
(-)
(-)
(-)
(-)
(-)
( -)
f Morone spp.
Temperate bass Sfc (b
Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
5 Lepomis spp.
Sunfish Sfc 1.4 1.9 2.9 5.9 0.9 1.2 2.1 4.7 6.1 Mid (2.4)
(-)
(-)
(7.5)
(-)
(-)
(1.6)
(6.4)
(-)
(-)
(-)
Pomowls spp.,
Crapple Sfc Mid
(-)
(-3
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Centrarch idae, Unid.
Sunfish Sfc Mid
(-)
(-)
(-)
(-)
(- 3
(-)
(-)
(-3
(-)
(-)
(-)
Percidae Darters Sfc Mid (-).
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Damaged, Unid.
Sfc 0.9 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Total Sfc 3.2 1.9 2.9 6.8 0.9 1.2 2.1 4.7 6.1 Mid (3.5)
(-)
(-)
(12.9)
(-)
(-)
(3.2)
(6.4)
(1.2)
(-)
(-)
Note: Sfc = Surface Samples; Mid = Mid-depth a 0.11y surface samples taken at Stations C and P
^**
m'-T '.7 m
m._ -
W M
M M
M M
M i
m Ttble 2.6.1 (Continued)
Page 7 of 7 Neal Sub-SEPTDOER 1981 ArJa Parr Shoals Impoundment Monticello Station B H
J K
L M
N O
Scientific Name Common Name
~
-Ca
-pa I
Dorosoma spp.
Herring Sfc Mid
(-)
(-)
( -)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Clupeldae, Unid.
Herring Sfc HId
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Cyprinus carpio Carp Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Cyprinidae Minnews Sfc i
Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(0.9)
(-)
(-)
Catos tomi nae Suckers Sfc l
Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Catostomidae, Unid.
Suckers Sfc Mld
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
w W>rcne spp.
Temperate bass Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
I y Lepomis spp.
Sunfish Sfc 1.09 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Pomoxls spp.,
Crapple Sfc Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Centrarchidas, unid.
Sunf ish Sic 0.9 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
Percidae Darters Sic MId
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
letaluridae Catfish Sic Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(0.9)
(-)
(-)
Total Sfc 0.9 1.09 Mid
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(-)
(1.8)
(-)
(-)
Note: Sic = Surface Samples; Mid = Mid-depth a Only surface samples taken at Stations C and P
I R
2.7 BENTH0S 2.7.1 Introduction I
Benthic macroinvertebrates are bottom-dwelling organisms which inhabit underwater substrates during part or all of their life cycle. These organisms are large enough to be retained by a 0.595 mm sieve and may be seen by the unaided eye. Many species are important biological indica-tors of the physical and chemical quality of an aquatic ecosystem. The benthic macroinvertebrate community may also provide an indication of important trophic or food chain relationships with higher life forms, especially fish, within the aquatic environment. Certain aspects of these relationships are evaluated using numerical analyses (mean annual values) as described herein.
The resulting numerical relationships, which are emphasized in this section, provide indications of overall ecological congitions and trends that are of ten better than evaluations provided by single indicator species, or single community component (number of taxa, densities, biomass, diversity, or equitability) evaluations (Tables 2.7.1 and l3 2.7.2).
The component of density provides information on the upper and lower limits of the number of organisms per square meter of a particular taxon or complete community.
Biomass data supplements density measure-ments with weight per square meter measurements and also shows upper and lower limits for specific taxa and entire communities. The community components of diversity and equitability provide evaluations of taxonom-ic richness or variety, and evenness or the apportionment of individuals E
t among taxa.
Higher diversity and equitability values generally indicate l
more complex food chains (numerous functional feeding groups present at different trophic levels) and increased community stability (reduced l
oscillations or moderation from extreme variations of density, biomass, and taxonomic makeup).
1 l
2.7-1
.I
I I
Frequently, subtle changes reflected in the benthic macroinvertebrate communities cannot be completely assessed with short-term data collec-tion. Under these circumstances it is possible that either natural variation or artificial changes may be the cause. Environmental changes resulting from natural variation are likely to be caused by temporal and/or spatial changes, or influences on the benthic community. For objective evaluations of these types of changes in the aquatic environ-ment, long-term studies may be required to complete an ecological assessment.
The emphasis of this section was to evaluate the benthic data collected quarterly during 1981 and to assess important ecological trends and relationships which have occurred since June 1978. Evaluation and comparison of the benthic macroinvertebrate data were based on variables among the transects sampled and mean annual values calculated from com-posite quarterly survey data.
The numerical relationships (mean annual vslues) depicting general ecological relationships were., calculated for each transect and include density, biomass, number of taxa, diversity, and equitability. Distribution, and frequency of important taxa were considered separately. Mean annual values were calculated from tripli-lg 5
cate samples at each transect, collected quarterly (January, April, July, and October). The data from which mean annual values were calculated for 1981 are presented in Table 2.7.2.
The 1978, 1979, and 1980 data are provided in the respective Environmental Monitoring reports (Dames & Moors; 1978, 1979, 1979a, 1980).
2.7.2 Findings I
Parr Reservoir During 1981, the benthic macroinvertebrate communities in Parr Reservoir showed similar trends to those from previous surveys (Dames & Moore; 1978, 1979, 1979a, 1980). During 1981 mean annual taxonomic diversity g
(3) was 1.31 for Transect B, 1.99 for Transect C, and 3.35 for E
Transect D; equitability was 0.48, 0.58, and 0.83, respectively. The 2.7-2 1
I I
mean annual number of taxa was 6.5,11.5, and 17.0 for Transects B, C, and D, respectively. Mean annual density was 882/m2, 1817/m2, and 1204/m2 for Transects B, C, and D, respectively.
Bicmass was 44.49 I
g/m2 at Transect B, 12.78 g/m2 at Transect C and 26.94 g/m2 at Transect D.
Transect B showed the most significant changes since the 1978 survey.
I Community characteristics, as indicated by the improvement of selected overall mean annual values, showed some moderation from a developing trend toward previously lower extreme values at Transect B.
The moderation experienced at Transect B was from an earlier trend toward lower numbers of taxa, and lower diversity and equitability, but with sigr.ificant increases in density and biomass (1978 through 1980)
I indicating a less stable, less complex benthic community. During the 1981 survey, mean annual density and equitability remained similar and biomass, number of taxa, and diversity increased.
Since incr2ases in the number of taxa and diversity indicate greater stability in aquatic ecosystems, it is considered a slight improvement in the benthic macro-invertebrate community at Transect B.
Further monitoring should help determine the significance of the beneficial changes that occurred I
l during 1981.
I i
Transect C and especially Transect D, showed ranges characteristic of the mean annual values obtained during previous surveys '(Dames & Moore; 1978, 19 79, 19 79a, 1980).
I Although the benthic community at Transect C showed characteristic density and above normal biomass values, as compared to previous data, a
gradual trend toward decreased number of taxa, diversity, and equita-bility were indicated. These changes suggest a slightly decreased community complexity since 1978. Th:s trend was most pronounced in 1981 when fewer benthic macroinvertebrate texa occurred which subsequently reduced the mean annual values for taxonomic diversity and equitability.
The reduction in number of taxa may be caused by repeated drawdown in l.
l l
2.7-3 1
l
I I
Parr Reservoir and, in part, may also result from natural variation.
Studies in 1982 may provide findings which will help define this trend and establish further rationale for the causes.
I The slightly increased taxonomic variability at Transect B suggests a slightly improved benthic community during 1981. The indicator values, I
however, were still considerably below mean values for 1978, indicating that the tailrace area is a physically stressed environment.
Benthic density and biomass continue to increase predominantly due to the presence of the Asiatic clam (Corbicula manilensis) at Transect B and are presently much higher than pre-1979 values.
During 1981, Parr Reservoir showed mean annual benthic macroinvertebrate I
density (1301/m2), and diversity (2.22) to be higher than observations obtained from 1976 through 1981 (Dames & Moore; 1976, 1977, 1978, 1979, 1979a, 1980, and 1981). Mean annual density, from 1976 through 1981, 2
2 ranged from 381/m to 1633/m, and diversity ranged froms1.92 to 2.78.
The mean annual values calculated for the same period were 1197/m2 for density and 2.20 for diversity. The indication is that g
unlike Transects B and C, the benthic community at Transect D has become
'E more diverse. Based on statistical data, this improvement has been of a magnitude to easily differentiate the subtle and possible adverse trend described at Transect C.
Benthic macroinvertebrate biomass at all Parr Reservoir stations was higher than for any previous year. This increased biomass results from the collection of both higher numbers and larger Asiatic clams, depend-ing on the specific sampling area. Overall, benthic density did not Nu increase during this survey year. The data for other benthic organisms indicated that biomass for all except the Asiatic clam has probably stabilized.
I l
Although there has been significant variability in Asiatic clam densi-ties since these studies began in Parr Reservoir in 1978, the overall
<=
trend indicates increased abundance from June 1978 through January 1980; a
- a 2.7-4
I I
decreased densities from April 1980 through July 1981, and a return to higher densities in October 1981. The Asiatic clam abundance continues to show the greatest variation at Transects B and C and the least I
variation at Transect D.
The highest densities for the Asiatic clan in Parr Reservoir for a single benthic sample occurred at Transect B 2
2 (3014/m ) in January 1980, and Transect C (2497/m ) in October 1980.
The highest Asiatic clam density during the 1981 survey also occurred at Trat. sects B and C, with 860/m2 2
and 732/m, respectively.
The most abundant taxa collected from Transects C and D in Parr Reser-voir during 1981 were primarily midges, mayflies, and tubificid worms.
Many of these taxa were also predominant during earlier studies. The predominant organisms, which also are useful indicator species, were I
Hexagenia limbata, Coelotanypus spp., Cryptochironomus spp., Tanytarsus spp., Dicrotendipes spp., Procladius spp., Branchiura sowerbyi, and the Asiatic clam, Corbicula manilensis. These aquatic macroinvertebrates appeared frequently in the benthic samples at Transects Q and D.
e The benthic macroinvertebrate community at Transect B provided further
- ,E
""id*"'"
' """' "''""**'""""d"*"'
E and operation of the FPSF. This alteration was expected and has been discussed in the previous reports (Dames & Moore; 19 78, 19 79, 19 79a,
1980). Dominant benthic species present at Transect B included tubi-ficid and naidid worms, and the Asiatic clam. Although other species of benthic macroinvertebrates were occasionally present, they occurred infrequently. The slight increase in diversity during 1981 was due to increases in the frequency of previously uncommon taxa a: curring in s
I benthic sampics. The Asiatic clam made up from 32.1 to 89.5 percent of the benthic density at Transect B and continues to be the most important biomass component.
JE 2.7-5 LI
I I
Neal Shoals Dam Senthic macroinvertebrate samples have been collected from the Neal Shoals Dam station since 1978; at this location, the benthic community I
has remained stable, based on samples collected through 1981. Mean annual values for densities increased slightly while those for taxonomic composition, biomass, diversity, and equitability decreased slightly during 1981, as compared to previous studies.
I Mean annual diversity (2.61) in 1981 reflected a complex community I
comprised of high numbers of taxa (mean,14.3) and high densities (mean, 2
1786/m ).
These characteristics reflected a mean annual equitability index of 0.69.
The predominant benthic fauna were similar to that observed at Transects C and D in Parr Reservoir. The Asiatic clam was more abundant during 1981 than during previous surveys at Neal Shoals Dam; and during July and October the Asiatic clam densities were highar than at the Parr Resevoir transects.
I 3enthic macroinvertebrate biomass, as expressed by mean annual values (0.89 g/m2), remained consistent during 1981 as compared to previous surveys in 1979 and 1980, but was much less than the 1978 measurement of 2
5.70 g/m,
Subimeoundment The benthic macroinvertebrates communities at Transect H have changed considerably in species, density, biomass, diversity, and equitability from 1978 through 1981. This community has increased its mean annual density by a factor of nearly 24 during that period. Mean annual tr-'nomic composition doubled from 1978 through 1980 and decreased during 1981. Taxonomic diversity increased from 1.9 in 1978 to 2.98 in 1980, and then decreased to 2.15 during 1981. This decrease was due t
primarily to very h.gh densities of Chaoborus sp.
(7003/m2) and 2
[
Chironomus sp. (3171/m ) taxa during 1981. Biomass increased slightly is.
2.7-e il
I I
from 1979 through 1981. These data indicate that the benthic com-I munities achieved a very high growth rate through 1980 and may have reached, at least temporarily, a growth plateau.
Monticello Reservoir Monticello Reservoir benthic communities have shown an overall increase in all parameters surveyed from 1978 through 1981. Densities calculated from the 1981 study were higher than the results from previous years at all transects. Taxonomic diversity was generally stable or had in-creased at most transects. Collectively for all transects, there has I
been an increase in mean annual diversity (from 1978 through 1981) from 1.80 to 2.74 in Monticello Reservoir.
I Benthic macroinvertebrate community characteristics may be assessed using the mean annual values calculated for each transect during 1981.
For example, the highest densities occurred at Transects L and M (2180/m2 2
and 2084/m, respectively), while moderate densities (1460/m2 2
and 1770/m ) occurred at Transects N and K, respectively.
The remaining transects showed benthic densities between 917/m2 (Transect I) and ll82/m2 (Transect J).
Corbicula manilensis, tubi-ficid worms, Hexagenia limbata, Nais sp., and occasionally Dero sp.,
Dicrotendipes spp. and Chironomus sp. were typically found in samples with the highest densities.
The transect with the highest mean nuriber of taxa was K (15.8); Tran-sects J and L had 14.8 and 15.0 taxa, respectively, and Transects M and 0 had 14.5 taxa each. Transects N (13.0) and I (13.8) had the least number of taxa. Taxonomic diversity (3) indicated that the most diverse benthic community occurred at Transects L (2.88) and 0 (2.86),
while slightly less diverse communities occurred at Transects I, J, and B
K (2.79, 2.76, 2.75, respectively). The lowest taxonomic diversities occurred at Transects M and N, 2.58 and 2.61, respectively.
!E 2.7-7 15
I I
Equitability values were between 0.67 and 0.78, with Transect I being highest and Transect M being the lowest.
The most frequent insect taxa occurring in Monticello Reservoir were present at six combinations of the seven transects during each quarterly survey. These included the following insect taxa: _ Hexagenia limbata, I-Dicrotendipes spp., Coelotanypus spp., Procladius spp., Pseudochironomus sp., Cryptochironomus spp., and Chironomus spp.
The following non-insect taxa also occurred: Asiatic clam, tubificid worms (Tubificidae),
Dero spp., and Nais spp.
For the first time since 1978, the Asiatic clam was present at all transects. All of the above taxa increased their frequency of occurrence since 1979 and expanded their distribution throughout most of the reservoir. Overall, the taxonomic component I
within Monticello Reservoir continued to show a greater assortment of benthic organisms than during previous years.
Evaluation of benthic macroinvertebrate biomass data in 1981 indicated substantial increases throughout Monticello Reservoir. This was espe-cially true for Transects J, K, L, and N.
The Asiatic clam continues to I
add substantially to biomass at Transects L cnd M.
Transects M, 0, and I continued to show increases in biomass, but during 1981 these in-creases were not as large as those exhibited by Transects J, K, L, and N.
The Asiatic clam continues to be the predominant biomass contribu-l tor, aiding in the increase in overall mean annual benthic biomass of approximately 23 times in this reservoir from 1980 through 1981.
In-creases of this magnitude in the future will largely depend on the I
distribution, frequency, and potential population size of the Asiatic l
clam; their densities are expected to increase in Monticello Reservoir, however, not at the rate experienced during the 1981 study.
2.7.3 Discussion Several important observations may be made by comparing the data collected during the past four years. These observations reflect the 2.7-8 1
1
I I
overall quality of the aquatic environment mitt which the benthic organisms live.
I Three trends are apparent from a review of the benthic macroinvertebrate data collected from Parr and Monticello Reservoirs, the subispoundr.wnt, and the control station at Neal Shoals. These trends have been Obdarved through objective evaluations of short-and long-term changes in benthic macroinvertebrate coc:munity components. These trends are characterized
- 1) declining ecological stability and complexity at Transect B in as:
Parr Reservoir; 2) maintenance of ecological stability and complexity at I
Neal Shoals Dam, Transects C and D in Parr Reservoir, and Transect I in Monticello Reservoir; and 3) increasing ecological stability and com-plexity in the subimpounument and six transects in Monticello Reservoir.
Each of these observations are discussed below.
Transect B in Parr Reservoir has the only benthic coumunity showing a significant overall trend towards reduced ecological., stability and a more simplified community structure. This trend has been recognized in previous Dames & Moore reports (1978, 1979, 1979a, 1980) and is evidenced by decreasing community diversity, fewer taxa, and a si:npli-fled community structure; the trend moderated somewhat during 1981. On the other hand, specific taxa such as the Asiatic clam are tolerant of these environmental stresses, and are increasing in numbers of organisms and concomitant biomass.
The trend towards maintenance of ecological stability and complexity during 1981 is apparent at Neal Shoals Dam, Parr Reservoir Transects C and D, and for Transect I in Monticello Reservoir. Transect C in Parr Reservoir, showed a slight decline in the overall complexity of the macroinvertebrate community. This slight decline is attributed pri-marily to natural variation and, for this reason, Transect C has been categorized as maintaining ccological stability. This is not intended to disregard the possible adverse affects of drawdown or. this benthic community. The 1982 benthic data should provide more insight towards 2.7-9 im
x definin;; ehis trend and establishing further rationale for potential e
causes? '
h-k"W.e' sir Monticello Reservoir transects that showed increased ecological stability and complexity were J. K, L, M, N, and O.
The variability was I
substantial between stations; however, all shcued improved ecological characteristics..Each of these transects has unique habitat features which probably a count for most variability among the stations. These include both abiotic 'and biotic factors which are reviewed to determine basic limnological characteristics of the sampling areas studied.
I Transect 11, l e.ted in the subimpoundment, has shown the most dramatic I
changes in thi ecological stability and complexity of its benthic macroinvertebrate community over the past three years. Based on the 1981 data and a perspective of previous studies, the benthic community reached at Mast a temporary plateau in which standing crop increased bu: the number of taxa, diversity, and equitability decreased.
I 2.7.4 Summary The benthic macroinvertebrate data obtained from the 1981, and earlier surveys mimicked the somewhat 5Y predictable environmental conditions found in the four major study areas. As expected, in Parr Reservoir, only Transect B has shown a significant decline in ecological stability and couplexity. During 1981 this change was not as apparent as reported for earlier surveys; however, the relative' level of physical stress due to the station's close proximity to the FPSF, was still observed.
The remaining tranaects in Parr Reservoir (C and D) continue to have dB diverse benthic macroinvertebrate communities, illustrative of ecologi-cal stability and complexity. The 1981 data for Transect C, however, continues to show a trend over the past three, years of slightly declin-ing environmental conditions. This trend is believed to te within the limits of natural variation in Parr Reservoir. floweve r, the potential 2.7-10 LB
I adverse affects of repeated drawdown on benthic communities in Parr Reservoir cannot be disregarded at this time.
Further data collection and evaluation will define the significance, if any, of the trend observed at Transect C during the previous three years. The benthic I.
community of Transect P (Neal Shoals Dam) also demonstrated maintenance of ecological stability and complexity.
The macroinvertebrate communities in Monticello Reservoir continue to show increases in mean annual values for density, taxonomic composition and diversity, equitability, and biomass. This increase in biological productivity and community complexity is expected to continue in Monti-I, cello Reservoir, although more variability may occur at those transects located closer to the FPSF. Transect I was the only station in Monti-cello Reservoir which did not show substantive increases in parameters measured and appears to have attained stable community development.
I The benthic community in the subimpoundment continues to show increases I
in decsity and biomass while showing a lower number of taxa and reduced diversity. This trend is expected to continue as long as intensive fertilization continues. The subimpoundment is the only area sampled to date in which the Asiatic clam have not been reported.
5
' 8 I
8 l
I 2.7-11
!I
M M
M M
M M
M M
M M
W M
M M
M M
W W
W l
1 Table 2.7.1 Summary of benthic macroinvertebrate data collected from twelvo stations during the 1981 monitoring projram.
Page 1 of 4 Neal Sub-Area Parr Reservoir Shoals impoundment Bbnticello Reservoir S tat ion -
_K
_L
_M
_N
_O B
C D
P H
I J
Taxonorrje Abundance (Na/m )
Oryozoa 14 Coelenterata 14 Tur bel lari a 29 14 Nomatoda 14 29 29 Ol igochaota 57 1,306 316 330 4,391 28 330 1,263 615 270 431 4 16 w
Hirudinea 14 57
).,
Castropoda 43 14 w
Divalvia 603 488 157 14 143 230 215 1162 459 531 Diptera 14 114 156 1,176 5,926 57 I,231 157 430 517 487 243 Ephemeroptera 158 29 86 43 43 14 57
-732 72 186 Megaloptera 14 i
Odonata 14 i'
Trichoptera 14 14 42 TOTAL 674 1,908 803 1,592 10,445 14 2 1,789 1,735 1,346 2,710 1,449 1,246
m M
M maememmam Table 2.7.1 (Continued)
Pago 2 of 4 Noal Sub-Area Parr Reservoir Shoals impoundment Monticello F4eservoir Station -
..O B
C D
P H
I J
K L
M N
I Taxonom{c Abundanco (No/m )
Coolenterata 14 129 j
Nonu toda 14 14 14 Oligochaeta 689 257 459 387 1,966 86 101 402 1,866 286 531 387 H1rudinea 57 Divalvla 388 746 71 29 29 301 1,134 1,004 244 531
,N Diptera 14 70 660 1,469 4,103 1,061 229 228 144 271 272 456 u
,8 Ephemeroptera 143 14 57 115 29 4 16 29 w
Odonata 14 14 Trichoptera 14 14 14 Hydracarina 14 TOTAL 1,119 1,087 1,333 1,870 6,126 1,305 387 1,045 3,144 1,977 1,047 1,560
EsMMMM M
M M
M M
M M
M M
M 4
W W
l l
l l
l Table 2.7.1 (Continued)
Page 3 of 4
,I f
Neal Sub-Area Parr Reservoir Shoals impoundment Monticello Reservoir Station 0
C D
P H
I J
K L
M N
O JULY
~
~
~
~
~
~
~
~
~
~
~
l
{
Taxonomjc Abundance (No/m )
i Bryozoa 14 f
Coelenterata Nematoda 14 43 14 14 j
Oligochaeta 344 1,234 416 372 301 473 14 789 558 789 144 28 Blvalvia 301 57 100 703 14 86 703 230 861 603 158 Diptera 14 70 285 416 5,257 128 558 300 443 156 300 417 w
Ephemeroptera 43 14 14 Megaloptera 14 14 Trichoptera 29 14 14 28 14 Coleoptera 14 J
TOTAL 687 1,404 887 1,505 3,558 643 672 1,834 1,231 1,820 1,075 617 4
e
m MM M
M M
emamm mammW W
m Table 2.7.1 (Continued)
Page 4 of 4 Neal Sub-Area Parr Reservoir Shoals impoundment Monticello Reservoir Sta t ion -
D C
D P
H I
J K
L M
N O
Tamnomge Abundance (No/m )
Bryozoa 14 Turbellarla 14 Nematoda 14 72 14 14 14 Gastropoda 14 244 Blvalvia 860 631 158 1,378 273 574 847 631 646 1 29 100 N
Oligochaeta 100 387 660 359 718 431 42 759 1,564 574 I,378 43 Y
Hirudinea 14 5
Diptera 57 286 571 387 11,911 371 9 74 601 544 258 489 559 Ephemeroptera 1,535 330 14 43 474 258 158 14 86 14 129 Megaloptera 14 29 Trichoptera 29 14 14 14 14 Hydracarina 14 TOTAL 1,046 2,867 1,761 2,167 12,672 1,563 I,876 2,465 2,997 1,578 2,038 84 5
E N
$N U
E
'M M
M W
mm Tablo 2.7.2 Summary of mean annual values for bunthic macruinvur tubrotus ubtoinud during the 1981 monitoring program.
Hoel Sub-liua Parr Husorm,1,r, Shoals
, i mp2undmins t Monticullo Rusurvoir Station B
C D
P H
I J
K L
M N
O Density No/m2 Jan 674 1908 803 1592 10445 14 2 1789 1735 1346 2710 1449 1246 f
April 1819 1087 1333 1b70 6126 1305 387 1045 3144 1977 1047 1560 July 687 1404 887 1505 3558 643 672 1834 1231 1820 1075 617 Oct 1046 2867 1761 2167 12672 1563 1876 2465 2997 1578 2038 845 Hean Annual b32 1817 1204 1786 8201 917 1182 1770 2180 2084 1460 1115 2
Blomass g/m Jan 0.11 0.98 23.18 0.85 1.93 0.04 0.67 0.74 7.07 50.87 0.35 8.88 April 57.60 19.04 10.59 0.71 1.42 0.71 0.17 0.55 25.08 65.52 0.53 4.10 July 33.62 3.57 20.44 1.69 0.34 0.31 0.16 17.93 12.70 77.02 19.81 4.07 Octobur 86.62 _ 27.52 53.56 0.30 1.34 4.50 16.10 23.44 106.97 81.93 11.06 8.86 Mean Annual 44.49 12.78 26.94 0.89 1.26 1.39 4.43 10.67 37.96 68.84 7.94 6.48 Number Jan 3
7 12 12 22 6
22 13 16 17 15 17 of Taxa April 9
13 I6 20 17 22 12 18 14 15 13 22 July 8
10 16 11 9
11 9
15 14 13 11 7
October 6
16 24 14 13 16 16 17 16 13 13 12 g
(
Mean Annual 6.5 11.5 17.0 14. 3 15.3 13.8 14.8 15.8 15.0 14.5 13.0 14.5 1
a Mean Species Jan 0.57 2.02 2.91 2.73 3.10 2.37 3.00 2.39 3.44 2.55 3.14 3.11 Diversity (3) April 1.78 1.97 3.49 3.39 2.43 3.75 3.38 3.25 2.30 2.63 2.58 3.18 July 1.81 1.76 3.27 2.41 1.23 2.20 1.95 2.49 2.82 2.48 2.21 2.05 October 1.07 2.19 3.71 1.92 _
1.83 2.85 2.70 2.87 2.95 2.67 2.52 3.10 Mean Annual 1.31 1.99 3.35 2.61 2.15 2.79 2.76 2.75 2.88 2.58 2.61 2.86 Equi ta-Jan 0.36 0.72 0.81 0.76 0.69 0.92 0.67 0.65 0.86 0.62 0.80 0.76 bility (e)b April 0.56 0.53 0.87 0.78 0.59 0.84 0.94 0.78 0.60 0.67 0.70 0.71 July 0.60 0.53 0.82 0.70 0.39 0.63 0.61 0.64 0.74 0.67 0.64 0.73 October 0.41 0.55 0.81 0.50 0.50 0.71 0.67 0.70 0.74 0.72 0.68 0.87 Moon Annual 0.48 0.58 0.83 0.69 0.54 0.78 0.72 0.69 0.74 0.67 0.71 0.77 a Index used is Shannon-Wiener (Pielou, 1966).
b index used is presented in USEPA (1973).
I I-2.8 FISH 2.8.1 Introduction I
Fish are important and visible componer s of the aquatic ecosystem.
I Fish rank high as a source of food and 2 creation for man.
Species that are not of special interest for man as a recreational or food source serve as food for other, more valuable fish species. Also, because of I
their sensitivity to changes in their environment many species may be useful indicators of stress in the aquatic ecosystem.
The purpose of this investigation was to identify important character-istics of the fish community in the water bodies of the study area according to: species composition and relative abundance, standing crop, diet, and condition factors and age distribution. The relative I
abundance was expressed as the percent of the total yearly catch for a species from all of the stations in that reservoir.
Mean condition factors and fish lengths at annulus formi;rion were calculated for dominant species (those that comprised five percent or more of the total 1981 catch). The condition factor (K) is a means of comparing the relative well being of fish. The heavier a fish is at a i
given length, the larger the factor and, by implication, the better the 1
" condition" of the fish. The factor is expressed in the form 5 3 K = W x 10 f t where W is the weight of the fish in grams, L is the total length of the fish in mm and 105 is a factor to bring the value of K near unity.
8 For growth determinations the scale (spine) radius and fish length data were fitted by linear regression using raw data and log-transformed (log 10) data.
The particular relationship used for back-calculation 8
was determined by the goodness of fit based on the regression correla-tion coefficient (r); the higher the r value, the better the fit. The Lee Method (Lagler, 1969) of back-calculation was used to estimate
>I 2.8-1
I total body length at each annulus for species in which the higher r value was obtained using raw data. The Monastyrsky Method (Lagler, 1969) was used for species in which the higher r value was obtained using log-transformed data. For the Lee Method fish body lengths were estimated according to the formula L = m S + b, where L represents the I
length of the fish in mm and S represents the scale (spine) radius in =s multiplied by 43 (60), the magnification at which the scale (spine) was viewed; m and b are constants derived from the data. The formula for the back-calculation of lengths using the Monastyrsky Method is L = bS*.
E 2.8.2 Findings and Discussion I
A total of 32 fish species were collected from all the stations during the 1981 sampling periods, utilizing gill nets and a boom electrofisher.
I The most numerous group of fish collected from all impoundment's was the centrarchid family (sunfish), which was represented by several species, particularly bluegill, largemouth bass, and black crappie. The next most abundant group was the clupeid family (shad) represented by one species, gizzard shad, which occurred in all the impoundments.
Icts-lurids (catfish), cyprinids (minnows), and catostomids (suckers) were found in all the impoundments in varying degrees of abundance.
Species composition of 1981 collections was similar to observations in previous years (Dames & Moore, 1978, 1979, 1979a, 1980), with minor exceptions. Exceptions to previous years included the first time col-lection of the spottail shiner, which was captured in Monticello Reser-voir. Other exceptions indicated passage of fish between Monticello and Parr Reservoirs through the penstocks of the Fairfield Pump Storage Facility (FPSF). The tessellated darter, observed in Parr Reservoir in 1978 and 1980, was collected for the first time in Monticello Reservoir 8
in 1981. Whitefin shiner and white bass, previously collected only from Monticello Reservoir, were collected for the first time in Parr Reser-voir.
2.8-2
I I
A detailed description of the fishery investigation follows and is pre-sented by reservoir.
S.ecies composition, relative abundance, condition t
factors, and age distritttions are described for the ccabined 1981 sampling periods.
I Parr Reservoir I
Species Composition and Relative Abundance. A total of 22 species were collected in Parr Reservoir utilizing both gill nets and a boom electro-fisher (Table 2.8.1).
During 1981, the centrarchid (sunfish) family was the dominant group. It represented 66 percent of the total catch and I
was represented by 8 species, of which the bluegill was most numerous.
The next most abundant group was the clupeid (shad) family. This group comprised 34 percent of the total catch and was represented by one species, gizzard shad. The remaining groups of fish obtained in these collections, with the percent of the catch, included:
five members of the catostomid (sucker) family, three percent; three members of the I
ictalurid (catfish) family, three percent; two members of the cyprinid (minnow) family, one percent; and one member of the lepisosteid (gar) family, one percent. Whitefin shiner and white bass were collected in Parr Reservoir for the first time. These species were previously found in Monticello Reservoir (Table 2.8-2) and their occurrence in Parr Reservoir indicated a mcVement through the penstocks of the FPSF.
The fish composition of Parr Reservoir has changed little since 1978 (Table 2.8-2).
Of 32 species collected since 1978, 21 have been col-lected in at least 3 of the 4 collecting years. Species at apparently low population levels, including shorthead redhorse, yellow bullhead, tadpole madtom, and tessellated darter, were infrequently collected.
Four species, creek chubsucker, snail bullhead, flier, and swamp darter, have not been collected since 1978.
I
!I 2.8-3 1
I I
Condition Factor and Age Distribution i
Condition factors and lengths at annulus formations (based on the I
Monastyrsky Method) for gizzard shad, bluegill, and largemouth bass are:
Mean Mean Length (mm) at Condition Annulus Formation Species Factor 1
2 3
4 5
6 7
Gizzard shad 0.960 114 182 228 281 327 Bluegill 1.665 47 88 117 138 158 Largemouth bass 1.422 127 214 287 350 386 411 378 Gizzard shad exhibited slightly slower growth than fish from waterbodies I
in other areas of the southeastern U.S. (Carlander, 1969) and the condition factor was average compared to fish from other bodies of water reported by Jester and Jensen (1971).
In general, growth of bluegill at Parr Reservoir was slower than other bluegill populations from the Southeast (Carlander, 1977). The condition factor was considered average when compared to data for other bluegill populations compiled by Carlander (1977).
I For the average largemouth bass from Parr Reservoir, recruitment into the fishery, at approximately 305 mm (12 in), occurred i
during the fourth year of life, as it did for. most largemouth bass froni the Southeast (Carlander, 1977). However, growth appeared to be slower l
for Parr Reservoir largemouth bass than other populations. The mean condition factor was average in comparison to other largemouth bass
)
populations in the Southeast (Carlander, 1977).
l Standing Crop Estimates. The standing crop is the poundage of fish present in a body of water at a specific point in time.
Standing crop l
estimates at Station C were made by block netting an area of 0.07 ha (hectare). The rcsults are shown in Table 2.8.3.
A total of 5.3 kg/ha, represented by 3 species, occurred at this cove in 1981, as compared l
with 142.8 kg/ha, represented by 17 species, that occurred during 1978; 11.3 kg/ha, represented by foar species in 1979; and 54.9 kg/ha, i ^
l l :
l i 2.8-4 L
I I
represented by 15 species in 1980 (Dames & Moore; 1978, 1979a, 1981).
The most abundant species collected (by weight) during 1981 was gizzard shad. The decreased abundance since 1980 at the cove near Station C may be attributed in part to the fluctuating water levels and the extremely low water conditions that prevailed during 1981.
I Neal Shoals Dam Species Composition and Relative Abundance. A total of 12 fish species was collected from Neal Shoals Dam utilizing the electrofisher during the 1981 collecting periods (Table 2.8.1).
The centrarchid family was numerically the dominant group of fish comprising 78 percent of all fish collected. This family was represented by 7 species, of which bluegill was the most numerous (38 percent of the total catch). The clupeid, represented by gizzard shad, was the second most numerous group (20 I,
percent of the total catch).
s The species composition of fish collections at Neal Shoals Dam have generally been consistent since 1978 (Table 2.8-2).
Of 23 species collected from the reservoir,13 have been collected in at least three of the last four collecting years. Four species, silver redhorse, shorthead redhorse, white catfish, and pumpkinseed, have been coll >cted 5
infrequently. Black bullhead, mosquito fish, redbreast, and yellow perch have not been collected since 1978. Creek chubsucker, common in the subimpoundment.and Monticello Reservoir, was collected for the first time in 1981.
Condition Factor and Age Distribution. Presented below are the condi-tion factors and mean fish lengths at annulus formation for the dominant y
species in the 1981 collections. The Lee Method was used for back-calculation of gizzard shad, bluegill, and redear and the Monastyrsky Method was used for white crappie and black crappie (Lagler, 1969).
3 s
2.8-5 I
)
I Mean Mean Length (mm) at I
Condition Annulus Formation Species Factor 1
2 3
4 5
6 I
Gizzard shad 0.924 127 184 220 257 293 Bluegill 1.700 43 87 119 141 Redear 1.562 98 137 158 192 183 White crappie 1.220 88 140 192 252 301 319 I
Black crappie 1.148 74 115 150 178 215 245 I
Growth of bluegill was slow. Typically, bluegill from the Southest reach a harvestable size of 152 mm (6 in) by the fourth growing season (Carlander, 1977) but the average bluegill from Neal Shoals Das will not I
reach harvestable size until the fifth growing seacon. The growth of gizzard shad was slow compared to other populations in the Southeast (Carlander, 1969).
The condition factor of gizzard shad was *1w and, for bluegill, was average when compared to values reported ey Jester and Jensen (1971) for s
.I
- "'d """' ""'
"""d"' ( ") ' ' ' ""'" -
W black crappie was slightly below average when compared to crappie popu-lations from similar habitats (Carlander,1977) Growth and condition of white crappie and redear was average when compared with other areas of the Southeast (Carlander, 1977).
3 Standing Crop Estimates. The standing crop estimates from the control station was made by block netting an area of 0.07 ha and applying rotenone. A complete kill was assumed and the results are illustrated in Table 2.8.3.
A total of 23.8 kg/ha of fish were collected, represented by 10 species. Largemouth bass and bluegill (15.2 and 5.9 kg/ha, respectively) accounted for the greatest biomass. Other species listed in order of abundance included: warmouth, black crappie, and i
redear sunfish. The standing crop estimates for 1981 were about one l
half of that recorded during the previous year (Danes & Moore,1980).
lN The reason for this decline may be attributed to the low water condi-tions that prevailed during much of 1981. The low water may have caused the fish to migrate out of the area.
l l
l 2.8-6 l
I I
Subimpoundment Species Composition and Relative Abundance. A total of 13 species were collected from the subimpoundment during the 1981 collecting periods utilizing gill nets and a boom electrofisher (Table 2.8.1).
The cen-I trarchid family, which comprised 53 percent of all fish collected, was the dominant group. This family was represented by eight species, of which bluegill was the most numerous (23 percent of all fish collected).
I The ictalurid was the second most numerous group; it was represented by the brown and yellow bullhead, and comprised 36 percent of the fish collected.
I Of 20 species collected in the subimpoundment since 1978, 12 have been collected in three of the past four collecting years.
Silvery minnow and black bullhead have been collected infrequently and are probably at I
low population levels. Black crappie was collected for the first time in the subimpoundment in 1981. Threespecies,redfinhickerel, lake chubsucker, and white catfish, have not been collected since 1978.
Condition Factor and Age Distribution. Presented below are the mean condition factors and mean fish lengths at annulus formation (Monastry-sky Method) for the dominant species in the 1981 collections.
l Mean Condition Mean Length (mm) at Annulus Formation Spacies Factor 1
2 3
4 5
6 Gizzard shad 1.004 191 273 298 332 l
Brown bullhead 1.178 175 242 258 269 272 Warmouth 2.043 62 118 154 167 Bluegill 1.842 32 90 134 149 158 168 Largemouth bass 1.256 135 196 243 263 8
Growth of the gizzard stad was faster than described by Carlander (1969) and Jester and Jensen (1977) for populations in the Southeast. Growth of the brown bullhead was faster than described by Carlander (1969) for 3.
! l l
2.8-7
other brown bullhead populations. Compared to growth data of warnouth I
from North Carolina lakes compiled by Carlander (1977), warmouth from the subimpoundment grew at a faster rate.
Similar to bluegill from Parr Reservoir and other waterbodies from the Southeast, the average bluegill from the subimpoundment reached harvestable size, approximately 152 mm I
(6 in) in their fourth growing season. However, growth appeared to be slower in bluegill from the subimpoundment than in populations from other areas in the Southeast (Carlander, 1977). Mean condition for I
bluegill was higher than bluegill from Parr Reservoir but within the range of values for bluegill from similar habitats (Carlander, 1977).
No largemouth bass older than age four were collected from the subim-I poundment in 1981. On the average, largemouth bass have not yet attained harvestable size by their fourth growing season. Generally the I,
growth rate and condition of largemouth bass from the subimpoundment was lower than for other largemouth bass from similar latitudes (Carlander, 1977).
Monticello Reservoir l
Species Composition, Relative Abundance, and Diversitv. A total of 30 5
fish species were collected from Monticello Reservoir utilizing gill l
nets, boom electrofisher, and a seine in the 1981 collecting periods (Table 2.8.1).
For all stations and collecting periods combined, the centrarchid family was the dominant group of fish; it was represented by nine species and comprised 66 percent of the fish captured.
Bluegill was the most numer-3.
ous species (54 percent of the fish captured). The next most numerous group was the clupeid, comprising 20 percent of all samples, and was represented by one species, gizzard shad. The remaining groups of fish obtained in these collections, with the percent of the total catch, included: seven members of the ictalurid (catfish) family, ten percent; five members of the catostomid (sucker) family, three percent; five
- I i i 2.8-8
I members of the cyprinid (minnow) family, one percent; one member of the percichthyid (temperate bass) family, 0.02 percent.
The fish composition in Monticello Reservoir has changed little since I
1978 (Table 2.8.2).
Of 32 fish species collected since 1978, 26 have been collected in at least three of the last four collecting years.
Green sunfish and lake chubsucker have been collected infrequently and redfin pickerel is the only species that has not been collected from the reservoir since 1978. The tessellated darter was collected for the first time in 1981; this species was previously collected in Parr Reservoir and may represent movement of fish through the penstocks of I
the FPSF.
Condition Factor and Age Distribution. Presented below are the mean condition factors and fish lengths at annulus formation calculated for gizzard shad and bluegill using the Monastyrsky Method and largemouth bass using the Lee Method.
l L
Mean Condition Mean Length (mm) at Annulus Formation Species Factor 1
2 3
4 5
6 7
Gizzard shad 0.888 120 187 228 275 Bluegill 1.628 48 87 115 139 Largemouth bass 1.241 127 199 280 348 410 449 488 These species generally exhibited slower growth than populations in areas of similar habitats (Carlander,1977; Jester and Jensen, 1971).
l However, largemouth bass were recruited into the sportfishing population by their fourth growing season; this is common in the Southeast.
Com-pared to populations in the southeastern United States the condition factor of gizzard shad from Monticello Reservoir was low (Jester and Jensen, 1971) and average for bluegill and for largemouth bass (Car-lander, 1977).
Standing Crop Estimates.
Standing crop estimates from coves near l
Stations I and K were made by block netting an area of 0.07 ha and 2.8-9 1
l '
I i '
' L
I applying roten--
a complete kill was assumed. The results are pre-I sented in Table z 8.3.
A total of 5.9 kg/ha was obtained at the cove near Station I and 1.6 kg/ha was collected at the cove near Station K.
At Station I, gizzard shad was the most abundant species; this was followed by bluegill and largemouth bass. At Station K, bluegill was the most abundant species; it was followed by pumpkinseed and largemouth bass.
The standing crop estimates for the 1981 samples were lower than the previous year. The results from the 1978 study showed that coves near Station I and K produced 83.5 and 84,5 kg/ha, respectively, and during 1979, 6.6 and 5.4 kg/ha, respectively (Dames & Moore; 1978, 1979). The 1980 data suggest that the fish were utilizing the littoral zone as they were during 1978, while the 1981 data indicate that the fish were not I
using the littoral zone as frequently, following the 1979 trend. The fluctuating water levels in the littoral zone increases turbidity and i
may account for this area not being frequented by fish.,
2.8.3 Summary I
The fish populations of Parr Reservoir were comprised primarily of the iI centrarchid gizzard shad species.
Bluegill was the most numerous species collected and gizzard shad was second in numerical abundance.
Five year classes of gizzard shad and five year classes of bluegill were
,I found. Growth of both species, as determined from back-calculated lengths, was slightly slower than other populations in various areas of the southeastern United States.
The fish data from Neal Shoals Dam indicated that centrarchids and gizzard shad numerically dominated the fish fauna. Seven species of centrarchids were collected with bluegill being the most numerous.
8 Gizzard shad was second in numerical abundance.
Four year classes were found for both bluegill and five year classes for gizzard shad. Growth il 2.8-10
I of both species was slightly slower than populations in other areas of the Southeast.
The fish populations of the subimpoundment were numerica.11y dominated by I
centrarchid-ictalurid species. Bluegill was the most numerous of the eight centrarchid species collected and brown bullhead was the most numerous of the two ictalurid species collected. Four year classes of of gizzard shad and five year classes of brown bullhead were found.
Growth of the brown bullhead was similar to fish in other southeastern
~
areas and growth of bluegill was slightly slower.
I The fish populations in Monticello Reservoir were also numerically dom-inated by centrarchid-gizzard shad species. Nine species of centrar-chids were identified and bluegill was the most numerous. Gizzard shad was second in numerical abundance in the collections. Four year classes of bluegill and gizzard shad were found in the reservoir. Growth of both species was slower than populations in other areas of the south-s eastern United States.
5 I
l 8 I
l 8
8 2.8-11 1
r-
-E O
E Y
E E
E E
E O
'O E
E E
Ttble 2.8.1 Numbers of fish, and their percent abundance ($), collected by electrof f sher and gill net during the 1981 sampling program.
Neal Sub-Area Parr Resermir Shoals impoundment mnticello Reservoir Station B C
D P
H i
J K
L M
N O
Common Name Scientific Name Gar Lepisosteldae 4
7 3
Longnose gar Lepisosteus osseus
(%)
(0.9)
(2.6)
(1.1)
Shad Clupeldae Gizzard shad Dorosoma cepedianum 80 62 91 94 65 284 152 16 2 19 262 14 6 19
(%) (18.1) (23.4) (32.4) (19.7)
(9.0)
(27.7)
(45.5)
(46.21 (1.7)
(28.7)
(43.7)
(1.7)
Minnows Cyprinidae Carp CyprInus carpio 8
5 2
1
($)
(3.0)
(1.1)
(0.2)
(0.3)
Silvery minnow Hybognathus nuchalls
($)
(0 2)
(0 2)
(0 3)
(0.1)
(0 8)
(0 6)
(0 2)
Goldsn shiner tbtemigonus crysoleucas
(%)
( 5)
(0 4)
(1 2)
(0 2)
(0 3)
(0 2)
(0 1)
(0.1) thitafin shiner tbtropis niveus
($) (0 2)
(0 4)
( I)
(0.3)
(0 6)
(0 4)
( 6)
N Spottall shiner
- y
~N. hudsonius 1
(%)
(0.1)
^"
Sucker Catos tomidae Quillback carp-Carplodes cyprinus 2
11 5
6 15 30 10 18 11 2
sucker (5)
(0.5)
(4.2) (1.8)
(0.6)
(4.5)
(8.5)
(0.9)
(2.0)
(3.3)
(0.2)
River carpsucker C_. carpi gg) gj 33 (0 1)
Hightin carpsucker C. vellfer (5)
(0.4)
(0 1)
Silver redhorse Nxostoma anisurum
(%) (0 2)
(2 8)
(0 1)
(1 2)
(0.3)
( 2)
(0 I)
Shorthead redhorse
~M. macrolepidotum 1
(%)
(0.4)
Creek chubsucker Erlmyznn oblongus 1
4 1
4 6
(5)
(0.2)
(0.6)
(0.1)
(0.4)
(0,5)
Catfish Ictaluridae thits catfish letalurus catus I
9 93 g 3) g y
Yellow bullhead
- 1. natalls (g)
(0 8)
(0 3)
(0)4)
(0 7) i
f r,-
,,j
,.-,i,, g m,,,
is, liiin lua m Tua u m 1mus les m 1mm g
l Tablo 2.8.1 (Cont inued)
Paje 2 of 3 Noal Sub-Area Parr Reservoir Shoals impoundment Monticello Reservoir Stat ion B C
D P
H I
J K
L M
N O
Common Name EclentIfIc Name Brown bullhead
- 1. nebulosus 2
5 1
4 256 220 3
6 4
16 2
5 (5) (0.5) (1.9) (0.4)
(0.8)
(35.3)
(21.5)
(0.9)
(1.7)
(0.4)
(1.8)
(0.6)
(0.4)
Channel cattish
- 1. punctatus 4
6 5
2 1
3 1
3
(%) (0.9)
(2.13 (0.5)
(0.6)
(0.1)
(0.3)
(0.3)
(0.3)
Flat bullhead I. platycephalus 3
6 4
1 2
i
($)
(0.3)
(1.7)
(0.4)
(0.3)
(0.2)
Snell bulthead
- 1. brunneus 1
43 28 27
(%)
(0.1)
(3.9)
(3.1)
(2.4)
Marginej madtom Noturus insignis 2
F (5)
(0.2)
Y CTemperate bass Percichthyldae i
White bass Morone chrysops 2
I
(%) (0.5)
(0.1)
Sunfish Centrarchidae filer Contrarchus macroptorus 6
1 1
2 5
(%)
(0.8)
(0.3)
(0.3)
(0.2)
(0.5)
Hod ts eas t Lepomis auritus 15 1
e 2
1 2
22 20 32
(%) (3.4)
(0.4)
(0.5)
(0.1)
(0.6)
(2.01 (2.2)
(2.8) ttarmout h L. gulosus 3
3 71 12 3
20 24 2
29 (5) (0.7)
(0.6)
(9.8)
(1.2)
(0.9)
(1.8)
(2.6)
(0.6)
(2.6)
Blusjlli
- 1. macrochirus 125 72 79 179 166 325 83 90 874 385 117 919
(%) (28.23 (27.2) (28.1) (37.6)
(22.9)
(31.9)
(24.9)
(25.6)
( 78. 3.'
(42.21 (35.0)
(81.0) i
E
'E E
O N
E E
E M
E M M M
'E Table 2.8.1 (Continued)
Page 3 of 3 Neal Sub-Area Parr Reservoir Shoals impoundment Nnticello Reservoir Stat ion B
C D
P H
I J
K L
M N
O Common Name Scientific Name Pumpkinseed L. gibbosus 12 19 8
I4 22 8
12 16 7
14 18 (5) (2.7)
(7.2) (2.8)
(1.9)
(2.1)
(2.4)
(3.4)
(1.4)
(0.8)
(4.2)
(1.6)
Redear sunfish L. microlophus 13 22 6
28 l
4 4
2 1
(%)
(2.9)
(8.3) (2.1)
(5.9)
(0.1)
(1.2)
(1.1)
(0.2)
(0.3)
Largemouth bass Micropterus salmoldes 110 20 28 9
122 83 40 24 57 59 13 49 (f) (24.8) (7.5) (10.0)
(1.9)
(16.8)
(8.1)
(12.0)
(6.8)
(5.1)
(6.5)
(3.9)
(4.3)
White crapple Pomoxls annularis 11 3
24 3
(%)
(4.2)
(1.1)
(5.0)
(0.3)
Black crapple P. nigromaculatus o5 3
36 126 3
11 1
4 18 6
(%) (14.7)
(1.1) (12.8) (26.5)
(0.4)
(1.1)
(0.3)
(1.1)
(1.6)
(0.7) 7
's Perch Percidae Yetlow perch Perca flavescens 13 2
(%)
(1.3)
(0.6)
Tesseilated darter Etheostoma olmsted!
1
(%)
(0.1) l Total number captured 443 265 281 476 725 1025 334 351 1116 912 334 1135
IQ
(&
ih
~&
~&
M
'M M
M M
M Y
S
~
Table 2.8.2 Fish species collected in 1978,1979,1980, and 1981.
Page I of 2 Parr
% nticetto Area Reservo ir Neal Shoals Dam Subimpoundment Reservoir Yoar 1978 1979 1980 1981 1978 1979 1980 1981 1978 1979 1980 1981 1978 1979 1980 1981 Common Name Scientific Name Gar Lep t sos teldae longnose gar Lepisosteus osseus x
x x
x x
x x
Shad Clupeldae Gizzard shad Dorosoma copedianum x
x x
x x
x x
x x
x x
x x
x x
x Pickerel Esocidae Redfin pickerel Esox americanus x
x Minnows Cyprinidae Carp Cyprinus carpio x
x x
x x-x x
x x
x x
Silvery minnow Hybognathus nuchalls x
x x
x x
x x
x x
x x
Colden shiner Notemigonus crysoleucas x
x x
x x
x x
x x
x x
x x
x x
x Whitefin shiner Notropis niveus x
x x
Sandbar shiner N. scepticus x
- Carpsucker Catostomidae Qulliback carp-Carplodes cyprinus x
x x
x x
x x
sucker River carpsucker C. carpio x
x x
x x
x x
x x
x Highfin carpsucker C. vellfer x
x x
x x
Silver redhorse Nrostoma anisurum x
x x
x x
x x
x x
Shorthead redhorse M. macrolepidotum x
x
.a x
- x x
Lake chubsucker Erimyzon sucetta x
x x
Creek chubsucker E. oblongus x
x x
x x
x x
x x
Catfish letaluridae Whitu catfish Ictaturus catus
.x x
x x
x x
x x
x x
x Yullow bullhood
- 1. natalls x
x x
x x
x x
x x
x Drown but lhead
- 1. nobulosus x
x x
x x
x x
x x
x x
x x
x x
x Channel catfish I. punctatus x
x x
x x
x x
x x
x x
Flat butthead
- 1. platycephalus x
x X
X X
'M I&
O M
M M
M M
M M
'M M
Y Q
Y M
Table 2.8.2 (Continued)
Page 2 of 2 Parr Monticello Reservoir Neal Shoals Dam Subimpoundment Reservoir 1978 1979 1980 1981 1978 1979 1980 1981 1978 1979 1980 1981 1978 1979 1980 1981 Common Name Scientific Name Snall bullhead 1.brunneus x
x x
x Black bullhead
- 1. melas x
x x
x x
x Mrrgined modtom Noturus insignis x
Tadpole madtom N. gyrinus x
PoecilIdae 1
l Mosqui to fish Gambusa affinis x
Temperate Bass Percichthyldae White bass Dbrone chrysops x
x x
x Sunfish Centrarchidae Filer Centrarchus macropterus x
x x
x x
x x
x x
w Redbreast Lepomis auritus x
x x
x x
x x
x x
x x
x x
?
Wtrmouth L. gulosus x
x x
x x
x x
x x
x x
x x
x x
x
>-4 Bluegill
- 1. macrochirus x
x x
x x
x x
x x
x x
x x
x x
x Pumpkinseed L. gibbosus x
x x
x x
x x
x x
x x
x x
x Rodoar sunfish L. microlophus x
x x
x x
x x
x x
x x
x x
x x
l Longear sunfish L. megalotis x
Green sunfish L. cyanellus x
Hybrid sunfish Lepomis sp.
x x
l Largemouth bass Micropterus salmoldes x
x x
x x
x.*
x x
x x
x x
x x
x x
White crapple Pomoxis annularis x
x x
x x
x x
x x
x x
x Black crapple P. nigromaculatus x
x x
x x
x x
x x
x x
x x
Percidae Yellow perch Perca flavescens x
x x
Swamp darter Etheosoma fusiforme x
Tessellated darter E. olmstedl x
x Total Number of Spocles 28 22 20 22 19 14 16 12 15 13 13 13 27 31 25 30
I I
Table 2.8.3 Standing crop (kg/ha) estimates of fishes from Parr and Monticello Reservoirs and the Neal Shoals Dam, 1981.a Monticello Neal I
Reservoir Parr Reservoir Shoals Stations I
K C
P Common Name Gizzard shad 3.8 4.3 Silvery minnow 0.2 Whitefin shiner 0.04 Channel catfish 0.3 White catfish 0.06 Pumpkinseed 0.2 Warmouth 0.9 I
Bluegill 1.8 0.8 0.8 5.9 Redear sunfish 0.6 Largemouth bass 0.2 0.2 0.2 15.2 White crappie 0.08 Black crappie 0.9 Tessellated darter 0.04 5
Swamp Darter 0.01 Total 5.9 1.6 5.3 23.8
.1 l
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3 l
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2.8-17 3
l 1
I 3,0 TERRESTRIAL SURVEY I
3.1 PHOTOGRAMMETRIC ANALYSIS OF THE BROAD RIVER /MONTICELLO RESERVOIR STUDY AREA An analysis of the false-color infrared aerial photography of the Broad River Study Area indicated that little change has occurred in land use between April 1980 and April 1981.
Seven areas evidenced changes in vegetative cover (Figure 3.1.1).
In all of these areas, the modifica-I tions consisted of clear-cutting for timber removal. This is a common timber management practice in the southeastern United States and results in the creation of relatively large areas of open habitat which, until pine trees again dominate the area, are very good wildlife habitat.
5 The areas cleared in 1981 ranged in size from 9 to 44 acres and totaled 123 acres. Two of the areas (B and C) could erode into Parr and Mon-ticello Reservoirs respectively, but the potential for' this is not high.
A comparison of the 1981 photographs with those taken in earlier years does not indicate any change or loss of vigor.
1 I
1 8
1 1
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Figure 3.1-1.
Land Modification in Study Area from 1980 to 1981.
--r----
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I 3.2 BIRDS I
3.2.1 Avian Auto Survey 3.2.1.1 Introduction I
The Auto Survey was conducted along two separate series of roads during both the winter and summer seasons (Figure 3.2.1).
One series of roads I
was located around the perimeter of Monticello Reservoir, near the j
areas of influence of the generating facilities (Routes ABC), while the other was located away from this area (Route D).
The and use along the two routes is superficially similar with approximately equal amounts of wooded versus open land occurring on the routes. However, Route D is more urbanized than Routes ABC.
Numerous single-family I
houses occur along this route, while houses along Routes ABC are less I
common. The undisturbed habitat present on Route D occurs in smaller patches than on Routes ABC.
The surveys were conducted during both the winter and summer seasons.
The sumner survey was timed to coincide with the U.S. Fish and Wildlife l
Service's Game Bird Call Count. All birds seen or heard at designated l
l stops were counted; a separate count of bobwhite and mourning dove was j
made for the Game Bird Call Count during the summer s,urvey.
l l
3.2.1.2 Findings and Discussion
'~
A list of species obscrved during the summer and winter auto surveys is presented in Tables 3.2.1 and 3.2.2.
The number of birds observed along both the control and the test routes decreased from the levels recorded in 1980 (Figure 3.2.2).
However, as has been noted since 1973, there were more individuals along the test route than along the l
control route (Figure 3.2.2).
A daily average of 8.4 birds pe. stop was observed during the summer survey along the test routes (ABO) while l
the average along the control route was 5.4.
This relationship was
!~
further demonstrated by the results of a X2 test conducted on the 3.2-1
I I.
number of individuals of certain indicator species which occurred on the two routes. The indicator species which were abundant enough on both routes during the summer survey to be included in the analysis I
were the mocking bird, eastern meadowlark, cardinal, rufous-sided towhee, Carolina chickadee, and mourning dove. The X 8enerated was significant at the 95 percent level, indicating that a significant dif-ference did exist in the abundance of these species on the two routes.
For all but the cardinal and chickadee, the numbers of individuals recorded on the test route were higher than on the control.
I A similar relationship between the test and control routes occurred during the winter survey. The test route had an average of 9.5 birds 2
per stop per day, while Route D had only 7.6.
The X calculated for indicator species was not significant. !Iowever, only the cardinal, Carolina chickadee, and rufous-sided towhee were abundant enough to be included in the analysis, resulting in an analysis which was less powerful as the analysis conducted on the summer datas, On the other hand, during the winter survey, both towhees and chickadees were more abundant on the test than on the control route.
I Twenty-five bobwhite were recorded along the test route during the two summer mornings of the Game Bird Call Count.
During the same period, twenty-five bobwhites were also recorded along the control route (Figure 3.2.3).
A comparison of the 1981 data with ddta from previous years indicates that the bobwhite populations along both routes have been fairly stable since 1977.
I Eight mourning doves were recorded along the test route during the Game Bird Call Count while five were recorded along the control route.
Since 1978, the test route has consistently had higher numbers of mourning doves than the control route. This relates to the degree of urbanization along the control route. Although doves occur regularly around houses, larger flocks occur in the less disturbed habitats along Routes ABC, thus accounting for the observed differences.
D 3.2-2 1
I I
3.2.2 Waterfowl Survev 3.2.1.1 Introduction i
Waterfowl surveys were conducted on Monticello Reservoir and on Parr Reservoir anc its tributaries, Frees Creek, and Cannons Creek. Obser-I, vations were.rade of all ducks and other waterfowl, wading birds, and shorebirds wl.ich utilized these areas during the winter, summer, and fall seasons of 1981.
3.2.2.2 Findit.gs and Discussion Waterfowl observed during the 1981 surveys are listed in Table 3.2.3.
I The fall and winter surveys documented the occurrence of migrating species utilizing the aquatic habitats of the study area. The summer survey was performed to document the occurrence of resident waterfowl species.
s I
During the fall survey, ducks were abundant in Parr Reservoir and its tributaries, with mallards, black ducks, and blue-winged teal being the W
most common species seen.
During this survey, the great blue heron was particularly abundant in Parr Reservoir, with 37 individuals observed in the reservoir and its tributaries. A small flock of Canada geese was also seen in Cannons Creek during the fall survej. The fall survey of Monticello Reservoir indicated that mallards were the only common, migrating duck species, although the large, resident flock of Canada I-geese was present. Numerous gulls and great blue herons, as well as three common loons were also seen on Monticello Reservoir.
During the winter survey, a large number of ducks was present in Parr Reservoir and its tributaries. Mallards were abundant in the dredge spoil area south of Frees Creek on the east bank of Parr Reservoir.
Great blue herons and killdeer were also common there. This area is somewhat protected from the boat traffic on the reservoir and offers 1
3.2-3
I i
attractive habitat in the form of open, shallow water broken up by marshy areas vegetated with willows and aquati-plants. A large flock of mallards was found in the slough which runs north from the tailrace I
canal parallel to the Broad River. Gulls also were numerous here as were great blue herons. Gulls occurred in Cannons Creek during this s
survey.
Fewer ducks were observed on Monticello Reservoir than on Parr 3
Reservoir during the winter period. Mallards and scaup were the most There were high winds on the lake during the winter census common.
period, and it appeared that many ducks found the more sheltered habitat of Parr Reservoir more suitable *han the open water of Lake Monticello. The flock of Canada geese transplanted by the South Carolina Wildlife and Marine Resources Department during 1979 seemed to be doing well in Monticello Reservoir.
The summer survey censused resident species that occurred in the area.
The wood duck is the only resident duck that breeds here regularly, although mallards will occasionally occur in this region. Only a single wood duck was seen in Parr Reservoir. Wood ducks have not been abundant here since the reservoirs were constructed. They bred in the I
flooded portions of Monticello Reservoir before it was completely filled, and a pair of wood ducks was observed in Parr Reservoir during the summer of 1979.
It appears that the condition of fluctuating water levels in the reservoirs is not attractive to this species, so that wood ducks have probably moved to more stable areas df the Broad River.
The only other aquatic birds seen in Parr Reservoir during the summer survey were three great blue herons, a common egret, and a woodcock.
Other than the transplanted geese, the only species seen in Monticello Reservoir were the great blue heron and the double-crested errmorant.
!8 1
g i
3.2-4
I I
3.2.3 Strip Census 3.2.3.1 Introduction I
Avian strip censuses were conducted at six sites in the study area
,during the winter and summer of 1981. Three sites were designated as sites and were located within an area of possible influence of the test generating facilities; the other three sites were designated as con-trols, and were located outside of any area of influence. A survey and control site were located in each of the following habitats, test I
which were the major vegetative types in the study area: pine, selectively-cut pine, and deciduous forests.
3.2.3.2 Findings and Discussion Twenty species of birds were observed on the three test sites during the 1981 surveys (lable 3.2.4).
Thirty-two species were recorded on the control sites (Table 3.2.5).
A graphic presentation of avian density (birds per acre) on test and control sites during the periods I
1974 through 1977 and 1979 thru 1981 is provided in Figure 3.2.4.
Avian diversity (number of species per site) is given in Figure 3.2.5.
A comparison of the data from winter 1981 with that from 1979-1980 showed that the pine habitat exhibited an increased density and diver-sity of species in the winter of 1981. The increase in density on the control site (Transect 1) was due to the presence of numerous cardinals and towhees, both of which vere uncommon on the test strip. Differ-1 I
ences between the control and test sites were observed during the I
summer survey. Both the density and diversity of birds on the control site during summer were over twice as great as the density and diver-sity of birds on the test site. The summer bird community on the control site contained numerous summer tanagers, vireos, and warblers, which were rare on the test site.
3.2-5
!il l
I I
The selectively-cut pine sites were altered by harvesting certain sized pines several years ago.
This is a common practice in pine forested areas managed for timber. Initially, this harvesting practice opens I
the habitat to additional sunlight and allows a more diverse plant community to become established on the forest floor.
Species such as bobwhite will move into these areas until the remaining pines grow to a size at which the canopy once again shades out the sunlight, and the area reverts back to a nearly monotypic pine stand. Both of the study sites in this habitat have passed the "open" stage and are now similar to pine-dominated sites.
I The density of birds on both the control and test, selectively-cut pine stands was much lower in the winter of 1981 than during winter 1980.
However, the density recorded in 1980 was heavily influenced by flocks of kinglets which inflated the density estimates. These flocks were not present in 1981, and the densities recorded were similar to the 1979 levels. Diversity was higher on the test site du, ring the winter, I
with nearly twice as many species seen as on the control. Avian density and diversity during the summer surveys was equal on both test and control sites and was similar to the levels recorded in 1980.
I The deciduous control site was located in a heavily wooded stream bottom while the test site was located in an area where a transmission line was constructed directly through a stream bottom; Since the establishment of the transmission line, the species found on the test site have included birds common to bottomland areas as well as those found in fields and hedgerows.
l 1
The winter community observed on the deciduous control site was similar in both density and diversity to the levels recorded during 1980. No t
one species was particularly common, but a fairly large number of species was seen.
However, the winter community on the test site was greatly reduced both in density and diversity from previous surveys, with only two species seen, the hermit thrush and the towhee.
l 3.2-6 I
I I
There is presently no explanation for the reduced numbers of birds on this strip.
Similar results occurred during the summer survey. The populations on the deciduous control site were similar both in density and diversity to populations observed in previous years. However, the populations on I
the test strip were greatly reduced in number and diversity. Again, there is no apparent explanation for this. Currently, the reduction in numbers on the test strip cannot be attributed to the operation of the generating facilities. However, this test area should receive particu-lar attention during future surveys to determine if a trend is apparant 3.2.4 Unusual Observations During the 1981 surveys, two species listed as endangered by the U.S.
Department of the Interior were observed within the study region.
During each of the waterfowl surveys of Parr Reservior, two immature southern bald eagles were seen. Eagles have been reported from both Monticello and Parr Reservoirs in past years and it appears that the habitat created by these impoundments is quite suitable for this species.
A much more unusual sighting occurred during the summer 1981 avian roadside census when an eastern cougar was seen crossing the road just south of Hellers Creek. This species is also listed as endangered and is much rarer than is the bald eagle. Although the habitat surrounding Parr Reservoir is suitable for this species, there is no evidence that i
it is a resident.
i \\e 3.2.5 Summary 8
Avian populations along the control and test auto survey routes were high in both density and diversity. The test route, although showing 1
'N 3.2-7
I I
somewhat reduced numbers of birds from the 1980 survey period, was still higher in avian density and diversity than in most previous years. The control route exhibited an even greater decrease in avian density and diversity when compared to the 1979 levels, but was still at the same level as recorded in 1977-78. The decrease on the control I
route appears directly related to the greater degree of urbanization along this route. The larger number of homes along the control route tends to create a patchiness of habitat on this route. The habitat along the test route is *.ess patchy and does not have the influence of human disturbance, thu', accounting for the higher population levels.
I The Came Bird Cal 1 Cmmt demenstrated that both bubwhite quail and I
mourning dove populations are similar in size, and fairly stable along both the control and test routes. The mourning dove population tends to fluctuate more widely than the quail population, but this is due to I
the migratory nature of mourning doves and their tendency to form flocks.
Bobwhite quail are more sedentary and thus,*the call count is influenced by flocks moving into an area during the survey as is not as the mourning dove count.
The waterfowl survey indicated that Monticello Reservoir is an important sanctuary for ducks and other aquatic bird species. Parr Reservoir was utilized heavily by migrant species during the fall and winter, but few resident species were found there during the summer.
The fluctuating water levels in both Parr and Monticello Reservoirs have caused a decline in resident breeding populations of such species as the wood duck and kingfisher. However, the great blue heron i
appeared to be as common in 1981 as in previous studies and may have j
increased in numbers. Species such as gulls, killdeer, and loons,
! 15.
which first appeared after construction was completed, were still present. The efforts to establish a resident population of Canada geese seems to have been very successful, and some breeding and nesting has been observed, l
13 3.2-8
I In general, the bird populations surveyed in the avian strip counts demonstrated slight reductions in numbers from the 1980 levels. These reductions occurred in all habitats during both seasons, indicating that there was an overall reduction in bird use of the study area in 1981. The reductions were particularly evident in several of the test I
sites. The reasons for the reduced population are unknown at this time.
The two immature bald eagles seen during the 1981 surveys could form a breeding pair in future years. Eagles do not breed until they are 7 to 10 years old, but they form pairs at an earlier age.
Thus, it is pos-cible that, in future year, cagia naaring could occur near the recer-voirs. The eastern cougar which was seen near Hellers Creek could remain in the area, but these animals require very large home ranges, and it is not yet possible to predict whether the animal is or will I
become a resident of the study region.
s I
I I
1 I
I 5
3.2-9 1
I I
Table 3.2.1 Birds observed during the auto survey - summer 1981.
Page 1 of 2 Route Where Observeda ABC D
Common Name Scientific Name Status E.
Turkey vulture Cathartes aura X
P Red-shouldered hawk Buteo lineatus X
P Mourning dove Zenaida macroura X
X P
I Yellow-billed cuckoo Coccyzus americanus X
S l
Chimney swift Chaetura pelagica X
S Common flickcr Colaptes auratus X
P I
Red-bellied woodpecker Melanerpes carolinus X
X P
j Eastern kingbird Tyrannus tyrannus X
X S
Great crested fly-catcher Myiarchus crinitus X
S Barn swallow Hirundo rustica X
X S
3 Purple martin Progne subis X
X S
Blue jay Cyanocitta cristata X
X P
g Common crow Corvus brachyrhynchos X
X P
Carolina chickadee Parus carolinensis X
X P
Tufted titmouse Parus bicolor X
X P
Brown-headed nuthatch Sitta pusilla X
X P
Rough-winged swallow Stelgidopteryx ruficollis X'
X S
Loggerhead shrike Lanius ludovicianus X
P Cattle egret Bubulcus ibis X
S
.g Broad-winged hawk Buteo platypterus X
S W
Mockingbird Mimus polyglottos X
X P
Brown thrasher Toxostoma rufum X
X P
Robin Turdus migratorius X
X P
Wood thrush Ilylocichla mustelina X
X S
I
(
3.2-10 LI
I Table 3.2.1 (Continued)
Page 2 of 2 I
Route Where Observeda Commot Name Scientific Name
~
Status" ABC D
Starling Sturnus vulga s X
P khite-eyed vireo Vireo griseus X
X S
Pine warbler Dendroica pinus X
X P
Prairie warbler Dendroica discolor X
X S
Yellow-breasted chat Icteria virens X
X S
Eastern meadowlark Sturnella magna X
X P
Red-winged blackbird Agelaius phoeniceus X
X P
I Common grackle Quiscalus guiscula X
X P
Brown-headed cowbird Molothrus ater X
X P
Summer tanager Piranga rubra X
X S
Cardinal Cardinalis cardinalis X
X P
Blue grosbeak Guiraca caerulea X
X S
Indigo bunting Passerina cyanea X
S I.
Parula warbler Parula americana X
S Yellow-throated warbler Dendroica dominica X
S Tennessee warbler Vermivora peregrina X
S Rufous-sided towhee Pipilo erythrophthalmus X
X P
Total Number of Species 33 35 3
a Routes are illustrated in Figure 3.2.1 b
g P = Permanent Resident 13 S = Summer Resident W = Winter Resident 8
I 3.2-11 3
I Table 3.2.2 Birds observed during the auto survey - winter 1981.
Route Where Observeda ABC D
Common Name Scientific Name Status Turkey vulture Cathartes aura X
X P
Red-tailed hawk Buteo jamaicensis X
P Killdeer Charadrius vociferus X
P Common flicker Colaptes auratus X
X P
Pileated woodpecker Dryocopus pileatus X
P I
Red-bellied woodpecker Melanerpes carolinus X
X P
Downy woodpecker Picoides pubescens X
P Blue jay Cyanocitta cristata X
X P
I Common crow Cnevna brachyrhynchne Y
Y P
Carolina chickadee Parus carolinensis X
X P
I Tufted titmouse Farus bicolor X
P Slate-colored junco Junco hyemalis X
X W
Northern harrier Circus cyancus X
W Red-shouldered hawk Buteo lineatus X
P Mockingbird Mimus polyglottos X
P Robin Turdus migratorius X
X P
Hermit thrush Catharus guttatus X
W Eastern bluebird Sialia sialis X
P English sparrow Passer domesticus X
P Eastern meadowlark Sturnella magna X.
P Common grackle Quiscalus quiscula X
X P
g Cardinal Cardinalis cardinalis X
X P
y Rufous-sided towhee Pipilo erythrophthalmus X
X P
Chipping sparrow Spizella passerina X
X P
White-throated sparrow Zonotrichia albicollis X
W Total Number of Species 19 18 a Routes are illustrated in Figure 3.2.1 b P = Pern.anent Resident S = Summer Resident W = Winter Resident 1
3.2-12 1
W H
h M
&5 5
'M M
M M
M M
M 8
.M M
Table 3.2.3 Results of 1981 waterfowl surveys.
I Dredge Spoil /
Frees Creek Cannons Creek Farr Reservoir Montice o Reservoir Common Name Winter Summer Fall Winter Summer Fall Winter Summer Fall Winter S mmer Fall Canada goose 18 210 240 215 Mallard 105 100 453 33 6
199 Black duck 150 2
5 Wood duck 1
Greater scaup 1
20 18 Pintail 1
Sboveler 54 Red-breasted merganser 2
Blue-winged teal 150 15 7
Common coot 9
Common loon 3
y Pied-billed grebe 1
N Great blue heron 21 6
3 6
17 3
25 1
10 13 h
Bc'ted kingfisher 2
1 1
Double-crested cormorant 1
7 1
Common Egret 1
l Cull (ring-billed / herring) 12 16 12 80 Woodcock 1
Killdeer 3
l Total Ducks 105 0
400 0
0 18 470 1
96 252 240 435 Total Shore Birds /
Wading Birds 36 0
6 19 1
8 18 4
26 13 17 96 Total Individuals 141 0
406 19 1
26 488 5
122 265 257 531 Total Species 4
0 4
2 1
3 5
3 8
7 3
9
I I
Table 3.2.4 Results of avian strip census conducted in different habitats on test sites during winter and sianmer of 1981.
Selectively Pine Cut Pine Deciduous Common Name Winter Summer Winter Summer Winter Summer Cardinal 1
2 2
2 1
Rufous-sided towhee 2
1 Blue jay 1
1 1
1 I
Tufted titmouse 3
1 1
Common crow 1
Carolina chickadee 1
2 3
1 I
Mourning dove 1
Hermit thrush 1
1 1
Wood thrush 3
Summer tanager 1
2 l g White-eyed vireo Common flicker 1
1 Slate-colored junco 4
I.
Downy woodpecker 1
Brown headed nuthatch 1
i Winter wren 1
s Prairie warbler 1
Blue grosbeak 1
i Red-eyed vireo 2
Parula warbler i
Numbers of Individuals 10 6
13 15 2
3 Number of Species 7
4 9
10 2
3 3
5 8
8 8
I n
(W 3.2-14 lE LE
I I
Table 3.2.5 Results of avian strip census conducted in different habitats on control sites during winter and summer 1981.
I Selectively Pine Cut Pine Deciduous Common Name Winter Summer Winter Summer Winter Summer Cardinal 4
4 2
1 1
1 Rufous-sided towhee 4
1 1
1 3
Blue jay 1
2 1
3 I
Tufted titmouse 2
1 2
Carolina chickadee 1
1 3
3 4
1 American goldfinch 2
I Mourning dove 1
1 1
Hermit th rtish 1
2 Wood thrush 1
1 Summer tanager 4
I White-eyed vireo 1
1 2
Red-eyed vireo 3
Bobwhite quail 1
I Yellow-throated warbler 1
Yellow-billed cuckoo 1
Pine warbler 4
Red-bellied woodpecker 2
1 I
Eastern bluebird 1
Blue gray gnatcatcher 2
Downy woodpecker 1
i Parula warbler 1
Brown-headed nuthatch 1
Number of Individuals 16 18 6
15 14 14 Number of Species 8
11 3
9 8
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8 5
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R I
a 1.o E
I y
os ABC
_ _ _ _ _ _ - _ _ _., ~ ~N o
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1973 1975 1976 1977 1978 1979 1980 19 81 MOURNING 00VE o.21 o.18 o.i 5 I
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1973 1975 1976 1977 19 78 1979 1980 19 81 Figure 3.2.3.
Comparison of Game Bird Call Counts on Avian Survey Routes.
i DAMES 8 MOORE I
3.2-18
Y&
M M
M M
M S
S K EY:
--- CONTROL SITE TEST SITE WINTER SURVEY PINE I
S E L ECTIV E LY 8-CUT PIN E DECIDUOUS E
(,- %
1 i
o
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1974 1975 1976 1977 1979 1980 1981 1974 1975 1976 1977 1980 19 88 1974 1975 1976 1977 1979 1980 1981 G
l SUMMER SURVEY i
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!9 74 1975 1976 1977 1979 1980 1981 1974 1975 1976 1977 1919 1980 1981 1974 1975 1976 1917 1979 1980 1981 i
l l
Figure 3.2.4.
Avian Density in Selected liabitats During Strip Censuses.
DAMES a MOORE
M M
M M
M M
M M
M M
M M
M 6
m i
~
i N EY:
---CONTROL SITE TEST SITE l
WINTER SURVEY S E L E CTIVE LY O 15 PINE CUT PINE DECIDUOUS U
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- 77 $'79
'80
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- 75
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- 74
'75
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'77 i *79 z
O
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- 81 l b
'o SUMMER SURVEY S E L E C T IVELY l
PINE CUT PINE DECIDUOUS 20 a
1 %
in
-",*~~"p*
w gs
's y
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- 81
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'80
'81 Figure 3.2.5.
Avian Diversity in Selected Habitats During Strip Censuses.
DAMES 8 MOORE
r I
4.0 REFERENCES
Battelle, 1974. Battelle Laboratories, Inc., Environmental impact monitoring of nuclear power plants-source book.
Atomic Industrial Forum, Inc.
August 1974, 810 pp.
I Bennett, G.W., 1970. Management of lakes and ponds. 2nd ED.
Van Nostrand Reinhold Company, 375 pp.
Carlander, K.C., 1977. Handbook of freshwater fishery biology, Volume 2.
Iowa State University Press, Ames, Iowa. 431 pp.
I
, 1969. Handbook of freshwater fishery biology, Volume 1.
Iowa State University Press, Ames, Iowa.
752 pp.
I Chengalath, R.,
C.H. Fernawdo, and M.G. George, 197t. The planktonic rotifera of Ontario with keys to genera and species. Department of Biology, University of Waterloo, Ontario. 40 pps.
I Clark, A.L. and W.D. Pearson, 1979. Early piscivory in larvae of the Freshwater Drum, Aplodinotus grunniens, in R. Wallus and C.W.
Voigtlander (eds.), Proceedings of works Ep on freshwater larval I
fishes. Knoxville, Tennessee, February 21-22, 1978. Tennessee Val' ley Authority, Division of Forestry, Fisheries, and Wildlife i
Development, Norris, Tennessee. 241 pp.
5 Dames & Moore, 1978. Environmental monitoring report June 1978 -
December 1978.
For the Federal Energy Regulatory Commission project license number 1894 and the South Carolina Department of Health and Environmental Control.
1979. Environmental uonitoring report January 1979-June l
1979. For South Carolina Department of Health and Environmental Control.
1979a.
Environmental monitoring report July 1979 -
8-December 1979, for the Federal Energy Regulatory Commission Project License Number 1894 and the South Carolina Department of Health and Environmental Control.
1980. Environmental monitoring report January 1980 -
December 1980 for the Federal Energy Regulatory Commission Project License Number 1894 and the Scuth Carolina Department of Health and Environmental Control.
Jes ter, D.B. and B.L. Jensen, 1971. Life history and ecology of the gizzard shad, Dorosoma cepedianum (Le Sueur) with reference to Elephant Butte Lake. Agricultural Experiment Stations Research Report 218. New Mexico State University. 56 pp.
- g l
4.0-1 l
I t
r.
I I
- Knight, C.B., 1965. Basic concepts of ecology. Macmillan Co.,
Toronto. 468 p.
I i
Koo, T.S.Y. and M.L. Johnston, 1978. Larva deformity in striped bass, 1
Morone saxatilis (Walbaum), and blueback herring, Alosa aestivalis I
(Mitchill), due to heat shock treatment of developing eggs.
Envir. Poll. 16: 137-149.
- Lagler, K.F., 1969. Freshwater fishery biology.
Wm. C. Brown Co.,
I Dubuque. 421 pp.
Marcy, B.C., J r., 1971.
Survival of young fish in the discharge canal I.
of a nuclear power plant.
J. Fish. Res. Bd. Canada 28:
1057-1060.
I Vulnerability and survival of young Connecticut 1973.
River fish entrained at a nuclear power plant.
J. Fish. Res.
Board Can. 30: 1195-1203.
I Pickering, Q.H. and C. Henderson, 1966. The acute toxicity of some heavy metals to different species of warm water fishes.
International Journal Air and Water Pollution.
Vol. X, pp. 453.
I.
Document EPA-440/9-76-023. USEPA, Washington, DC 501. p.
Schubel, J.R., C.C. Coutant and P.M.J. Woodhead, 1978..Jhermal effects of entrainment, h J.F. Schubel and M.C. Marcy, Jr. (eds.), Power Plant Entrainment, a Biological Assessment. Academic Press, New N
York, New York.
I Sculthorpe, C.D., 1967. The biology of aquatic vascular plants.
St.
Martins Press. New York.
- Snyder, D.E., 1971. Studies of larval fishes in Muddy Run Pumped I
Storage Reservoir near Holtwood, Pennsylvania.
M.S. Thesis.
Cornell University, Ithaca, New York. 209 pp.
'g Stemberger, R.S., 1979. A guide to Rotifers of the Laurentian Great
.g Lakes.
186 pp. EPA-600/4-79-021.
South Carolina Department of Health and Environmental Control, 1977.
LI Water classification standards system for the state of South i
Carolina.
15 p.
1 l I U.S. Environmental Protection Agency, 1976. Quality criteria for water. Document EPA-440/9-76-023.
USEPA, Washington, DC 501 p.
i f
i 4.0-2 4
I
(
I APPENDIX A METHODS Water quality sampling was conducted monthly, during the two-day period following the second Monday in each month, and was concurrent with the biological sampling.
Sampling dates and locations are indicated in Table A-1.
I The schedule for monthly and quarterly physical measurements and water
. quality sampling is in Tables A-2 and A-3.
Physical measurements were made in situ at the surface (30 cm) and at 1 m intervals to the bottom using electronic instruments with remote probes as follows: Temperature measurements were made using a Montedoro-Whitney TF10 or TC-5C thermistor, dissolved oxygen with a YSI I
Model 51 dissolved oxygen meter, pH with an AMI Model 107 pH meter, and conductivity with a CLI Model 708 conductivity meter. All instruments were given time to stabilize before the readings were recorded at each I
depth. Transparency was determined using a Secchi disc. Appropriate calibrations of all instruments were carried out several times during each sampling day.
Surface water samples were collected for determination of select chemical parameters using plastic bottles. The samples were preserved in the field according to approved procedures and shipped on ice to the I,
analytical laboratory.
The methods used for chemical analysis of water samples are listed in Table A-4.
Inspection for oil and grease residue and unusual odor was conducted daily below Parr Dam (Station SA) by SCE&G personnel.
8 I
A-1 LI
( __
t Table A-1 Water quality sampling locations and sampling dates for the Summer /
Fairfield Environmental Monitoring Program, January 1981 through I
December 1981.
I A
O" AREA LOCATION R
I Broad River 1
Broad River at Highway 34 Bridge SA Broad River below Parr Dam Parr Reservoir 2
Broad River at Frees Creek Trestle 2W Cannons Creek near Highway 28 Bridge Neal Shoals Dam 11 Broad River above Neal Shoals Dam Subimpoundment 18 Monticello Reservoir Recreation Impoundment Monticello Reservoir 12 Monticello Reservoir at Fairfield Intake
~
13 Monticello Reservoir at Summer Intake 14 Monticello Reservoir at Summer Discharge 15 Monticello Reservoir Western Section 16 Monticello Reservoir Near Old Highway 99 17 Monticello Reservoir Northern Tip I
20 Monticello Reservoir Eastern Section SAMPLING DATES January 13-14, 1981 February 10-11, 1981 I
March 10-11, 1981 April 14-15, 1981 May 12-13, 1981 June 9-10, 1981 I
July 14-15, 1981 August 11-12, 1981 September 15-16, 1981 5
October 13-14, 1981 November 10-11, 1981 December 15-16, 1981 A-2 1
I I
Table A-1 Water quality sampling locations and sampling dates for the Summer /
Fairfield Environmental Monitoring Program, January 1981 through December 1981.
I
^
AREA LOCATION R
I Broad River 1
Broad River at Highway 34 Bridge 5A Broad River below Parr Dam Parr Reservoir 2
Broad River ut reccs Cteek Trestle 2W Cannons Creek near Highway 28 Bridge Neal Shoals Dam 11 Broad River above Neal Shoals Dam Subimpoundment 18 Monticello Reservoir Recreation Impoundment Monticello Reservoir 12 Monticello Reservoir at Fairfield Intake 13 Monticello Reservoir at Summer Intake 14 Monticello Reservoir at Summer Discharge 15 Monticello Reservoir Western Section 16 Monticello Reservoir Near Old Highway 99 17 Monticello Reservoir Northern Tip I
20 Monticello Reservoir Eartern Section I
SAMPLING DATES I
January 13-14, 1981 February 10-11, 1981 I,
March 10-11, 1981 April 14-15, 1981 May 12-13, 1981 June 9-10, 1981 I
July 14-15, 1981 August 11-12, 1981 September 15-16, 1981 I
October 13-14, 1981 November 10-11, 1981 l
December 15-16, 1981 A-2
' :s
T I Table A-2.
Monthly sampling schedule for the Summer /Fairfield water quality study.
Station Number:
1 2
SA 11 12 14 15 16 18 I
A.
LABORATORY ANALYSES (surface sample onlv)
I Sodium Hardness I
I I
I I
I I
I NR Calcium Hardness X
X X
X X
X X
X NR Magnesium I
I I
I I
I I
I NR I
Chloride I
I I
X X
X X
X NR Sniface (50 )
I I
I I
I I
I I
E 4
TDS I
X X
I I
I I
I NR TSS I
I I
I I
NR NR NR NR I
Mo-Alkalinity I
I I
I I
I I
I NR P-Alkalinity (CACO )
X X
X X
X X
X I
NR 3
Ammonia (NH )
I I
I I
I I
I I
NR 3
I BOD I
I I
X X
X X
X NR Cadmium I
I I
I I
I I
I NR CCD X
X X
X X
X X
X NR I
Total Chromium X
X X
X X
X X
X NR Copper I
I X
X X
X X
X NR Total Hardness (CACO )
I X
X X
X X
X X
M 3
s Total Iron X
X X
X X
X I
I NR I
Lead X
X X
X X
X X
X NR Mercury I
I I
I I
I I
I h1 Nitrate (NO )
X X
X X
X X
X X
NR 3
I Ortho-Phospriate I
I I
X X
X X
X NR Total Phosphate X
X X
X X
X X
X NR Silica (SiO )
I I
I I
I I
I I
NR 2
Turbidity I
I I
I I
I I
I NR I
Zinc X
X X
X X
X X
X NR Carbon Dioxide I ; I I
I I
I I
I NR Kjeldahl Nitrogen NR NR NR NR NR NR NR NR NR Baron NR NR NR NR-NR NR NR NR NR NR: Not required I
~
B.
IN SITU MEASUREMENTS (1 Meter Intervals Surface to Bottom)
I Temperature Dissolved Oxygen Stations 1, 2, 2W, SA, 11, 12, 13, 14, 15 pH 16, 17, 20 Conductivity C.
IN SITU MEASUREMENT (Surface)
Transparency (Secchi Disc)
Stations 1, 2, 2W, SA, 11, 12, 13, 14, 15 16, 17, 20 A-3 I
1 I
I Table A-3.
Quarterly sampling schedule for the Su=mer/Fairfield water quality study.
I Station Number:
1 2
5A 11 12 14 15 16 18 A.
LABORATORY ANALYSES (surface sample only)
Sodium Hardness I
I I
I I
I I
I NR Calcium Hardness I
I I
I I
I X
X NR Magnesium I
I I
I I
I I
I NR Chloride I
X X
X X
X X
X NR sulfate (SO )
I I
I X
X X
X X
NR 4
TDS I
I I
I I
I I
I I
I TSS X
X X
X X
X X
X X
Mo-Alkalinity I
I I
I I
I I
X X
P-Alkalinity (CACO )
I X
X X
X X
X X
X 3
A==onia (NH )
I I
I I
X X
X X
X I
3 BOD I
I I
I I
I I
I X
Cadmium I
I I
I I
I I
I I
COD I
I I
I I
I I
I NR I
Total Chromium X
X X
X X
X X
X X
Copper I
I I
I I
I I
I X
Total Hardness (CACO )
I
.I X
X X
X X
X X
3 Total Iron I
I I
I I
X X
X NR I
Lead X
X X
X
'I X
X X
X Marcury I
I I
X X
X X
X X
Ortho-Phospb)te Nitrate (NO X
X X
X X
X X
X X
I I
I I
I I
I I
I Total Phosphate X
X X
X X
X X
X X
Silica (SiO )
X X
X X
X X
X X
NR 2
I Turbidity I
I X
X X
X X
X X
Zine I
I I
X X
X X
X NR Carbon Dioxide X
iX X
X X
X X
X NR Kjeldahl Nitrogen NR NR NR NR I
I X
X NR I-Boron I
I X
X X
X NR I
I l
NR: Not required i I B.
IN SITU MEASUREMENT (1 Meter Intervals Surface to Bottom)
Temperature Dissolved Oxygen Stations 1, 2, 2W, SA, 11, 12, 13, 14, 15, pH 16, 17, 20 Conductivity l
C.
IN SITU MEASURDfENT (Surface)
I Transparency (Secchi Disc)
Stations 1, 2, 2W, SA, 11, 12, 13, 14, 15 16, 17, 20 A-4
I 3
Table A-4 Procedures used in chemical analysis of water quality samples g
taken between January 1981 aad December 1981 for the Environ-mental Monitoring Program.a I
Parameter Detection Limits Procedure I
Sodium 0.01 mg/ liter AA - SM Calcium 0.08 mg/ liter ASTM Dll26-67B Magnesium 0.5 mg/ liter ASTM Dll26-67B I
Chloride 0.4 mg/ liter SM Sulfate (SO )
1 mg/ liter ASTM D516-68B 4
Total Dissolved Solids 1 mg/ liter ASTM D1887-67A Total Suspended Solids 1 mg/ liter ASTM D1688-67A I
MO-Alk 2 mg/ liter ASTM D1067-70C P-Alk (CACO )
2 mg/ liter ASTM D1067-74B 3
Ammonia (NH )
0.1 mg/ liter ASTM D1426-74B 3
I Biochemical Oxygen Demand 1 mg/ liter SM 507 Cadmium 0.01 mg/ liter EPA Chemical Oxygen Demand 4 mg/ liter EPA Total Chromium 0.03 mg/ liter EPA Copper 0.02 mg/ liter EPA Total Hardness (CACO )
2 mg/ liter ASTM Dil26-67B 3
Total Iron
'0.02 mg/ liter EPA Lead 0.05 mg/ liter EPA Mercury (pg/1) 0.2 pg/ liter EPA l
Nitrate (NO )
0.2 mg/ liter SM 419-D 3
g Ortho-Phosphate (PO )
0.01 mg/ liter ASTM D-515-72B 4
g Total Phosphate 0.01 mg/ liter ASTM D-515-72B Silica (SiO )
0.04 mg/ liter ASTM D859-68D 2
]
Turbidity 0.01 NTU ASTM D1889-71 l
l W
Carbon Dioxide 1 mg/ liter SM-407-A l
Kjeldahl N i 1 mg/ liter EPA Baron 0.2 mg/ liter SM 107B (1971 ED)
I Analysis Procedures taken from:
1 SM - Standard Methods for the Examination of Water and Wastewater, 1976, 14th ed. Publ. by American Publ. Health Assoc., Amer.
Water Works a. san., Water Poll. Control Fed., Washington, D.C.,
1193 pp.
ASTM - American Society for Testing and Materials, 1975. Annual Book of ASTM Standards, Part 31.
EPA - U.S. Environmental Protection Agency, 1974, Methods for Chemical Analysis of Water and Wastes.
EPA-625-6-74-003.
AA - Atomic Absorption I
A-5 I
.