ML20080A900

Environ Monitoring Rept,1982

ML20080A900
Person / Time
Site:	Summer
Issue date:	12/31/1982
From:	Dixon O DAMES & MOORE, SOUTH CAROLINA ELECTRIC & GAS CO.
To:	Harold Denton Office of Nuclear Reactor Regulation
References
NUDOCS 8402060392
Download: ML20080A900 (200)

Text

ENVIRONMENTAL MONITORING REPORT JANUARY 1982 - DECEMBER 1982 FOR THE FEDERAL ENERGY REGULATORY COMMISSION PROJECT LICENSE NUMBER 1894, THE SOUTH CAROLINA DEPARTMENT OF HEALTH AND ENVIRONMENTAL CONTROL, AND THE NUCLEAR REGULATORY COMMISSION JOB NO. 5182-103-09 l

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SUMMARY

The monitoring programs being conducted at the present time are de-

. signed to meet the licensing requirements of the regulatory agencies.

These agencies include: 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).

The purpose of the environmental monitoring program is twofold: 1) to establish baseline conditions on Monticello Reservoir prior to the

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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 FPSF. These studies will provide for comparison between preoperational baseline conditions and postoperational impacts.

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The Federal Energy Regulatory Commission (FERC) required five years of post operational data for the Fairfield Pumped Storage Facility (FPSF).

This requirement was satisfied at the end of 1982. The FERC requirements included: water quality and biological parameters which were monitored in the Broad River and in Parr and Monticello Reservoirs.

This report, which is the sixth one for the current monitoring pro-

! gram, will be submitted to FERC, NRC, and the SCDEEC. The report includes a summary of data for aquatic biology, surface water chem-t istry, and terrestrial data collected throughout 1982. The discussion of the data compares information collected during this reporting period with previous data, where applicable. 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).

During July / August 1982, the reservoir above Neal Shoals Dam (Station P) was lowered for the purpose of making repairs on the powerhouse and i

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i dam. As a result of the low water levels no biological or water quality samples were collected during this period.

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 32.7*C recorded by the United States Geological Survey (USGS) monitor in Monticello Reservoir during July. Water temperatures generally followed seasonal trends and were highest in July and August and lowest in January. At the Broad River and Parr Reservoir Stations, no sea-sonal 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 May through October.

The dissolved oxygen (DO) concentrations, along with temperature, followed seasonal trends. Higher DO values occurred during the colder months and lower values during the warmer months. At the Parr Reser-voir and Broad River Stations, DO was found throughout the water 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. However, on five occa-sions, from June through September, depressed oxygen levels were recorded at the USGS monitor at the FPSF intake. At the lower strata of the water column 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 the colder months when the reservoir " turned over" and complete mixing of the water occurred.

Most of 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 except for a few occasions during the colder months of the year. During January values of 9.2 and 9.0 were measured ii

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at Stations 2 and SA, respectively, and in February a value of 9.0 at Station 1 was recorded. In Monticello Reservoir the pH exceeded the state standard at the surface of certain stations during July and in the subimpoundment during May. The high values were attributed to photosynthetic activity and can be expected during 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; the exception to this occurred in January / February; the reason (s) for the high values cannot be explained.

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 settling of suspended particles characteristic of reservoirs as com- ,

pared to the more turbid conditions that exist in lotic systems, such as the Broad River and Parr Reservoir.

In Parr Reservoir and the Broad River, nitrate values ranged from 0.1 mg/ liter to 5.7 mg/ liter during the period 1978 through 1982. The

mean value for this 5-year period was 1.85 mg/ liter. The mean values for nitrate have shown very little fluctuation during this 5-year study period , ranging from 1.80 to 1.88.

At the Neal Shoals Dam station, during 1978 through 1982, nitrate values have ranged from 0.5 mg/ liter to 4.8 mg/ liter. The mean value during this 5-year period was 1.96 mg/ liter.

In Monticello Reearvoir nitrate values ranged from 0.1 mg/ liter to 4.5 mg/ liter during 1978 through 1982. The mean value for this 5-year 111

period was 1.3 mg/ liter. There has been no well defined pattern for nitrate values in Monticello Reservoir during this time; this is not uncommon in new reservoirs that have been recently flooded, since nutrients are being leached from the soil. In addition the water quality in Monticello Reservoir is influenced by water that is pumped up from the Broad River. Values of nitrate in the subimpoundment ranged from 0.1 mg/ liter to 2.5 mg/ liter during 1978 through 1982. The mean value during the 5-year period was 0.90 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.

Phosphate levels in Parr Reservoir and the Broad River ranged f rom 0.01 mg/ liter to 0.92 mg/ liter during the period 1978 through 1982.

The mean value for the 5-year period was 0.36 mg/ liter. The trend was a slight increase in the mean value during 1982 (0.23 mg/ liter) after a low mean value of 0.17 mg/ liter was reached during 1981. At the Neal Shoals Dam station the range of phosphate values was from 0.09 mg/ liter to 4.4 mg/ liter; the mean value during the 5-year period was 0.57 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 1982 period was 0.36 mg/ liter. There was a general increase in phosphate mean values from 1978 through 1980, and then the values decreased during 1981, and remained stable through 1982. In the subimpoundment the phosphate values ranged from 0.02 mg/ liter to 2.1 mg/ liter, with a mean phosphate value of 0.27 mg/ liter. The values of phosphate in the subimpoundment have fluctuated, due in part to the application of fertilizer during several months of the year.

Ammonia values at stations in the Broad River and Parr Reservoir ranged from 0.1 mg/ liter to 1.6 mg/ liter during the period 1978 through 1982.

The mean value for this 5-year period was 0.36 mg/ liter. There was a general increase in ammonia from 1978 through 1980 and then a decrease in 1981, followed by a slight increase in 1982. At the Neal Shoals Dam I

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station the ammonia values ranged from 0.1 mg/ liter to 1.1 mg/ liter.

The mean value during the period 1978 through 1982 was 0.36 mg/ liter.

In Monticello Reservoir ammonia values ranged from 0.1 mg/ liter to 1.0 mg/ liter. The mean value during the period 1978 through 1982 was 0.32 mg/ liter. In the subimpoundment ammonia values ranged from 0.1 to 2.2 mg/ liter; the mean value for the period 1978 through 1982 was 0.54 mg/ liter.

Concentrations of heavy metals in Parr Reservoir and the Broad River were detected in water samples but occurred in concentrations at or below the sensitivity of the analytical procedure with the exception of zine and iron. Concentrations of zine were detected at several sta-tions, several times during the year. However in only one case (Station 1, December; 0.06 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 several times during the

- year. The mean concentration of iron exceeded this value at Station 1 during eight months, at Station SA during seven months, and at Station 2 during three months. The highest total iron value recorded among these three stations was 7.6 mg/ liter at Station 1 in December. In general, total iron concentrations were higher during 1982 than in 1981. As has been observed in previous years of this study, the high iron concentrations were sometimes coincidental with high suspended l

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 levels preceeding sampling. These levels are not considered unusual for the study area.

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In the subimpoundment, the concentration of heavy metals was below the l

1evel of sensitivity of the analytical procedure. In Monticello Reser-l voir, the concentration of heavy metals throughout the current moni-toring program, with the exception of iron and zinc, was below the v

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.

Zine values at stations in the Broad River and Parr Reservoir have ranged from 0.01 to 0.59 mg/ liter from 1978 through 1982. The trend has been a decrease since 1978. The mean value for zine each year, during 1978 and 1979, was 0.02 mg/ liter at stations in the Broad River and Parr Reservoir. During 1980,1981, and 1982 the mean values for each year 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. In 1978, 1979, and 1980 the mean values each year were generally 0.02 mg/ liter while during 1981 and 1982 all the stations recorded zine values a 0.01 mg/ liter. Iron values in Parr Reservoir and the Broad River during the past four years have ranged from 0.21 to 29.0 mg/ liter. Mean values of iron concentrations 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 concentra-tion was 2.53 mg/ liter. It was during 1980 that the largest maximum values were recorded, 13, 20, and 29 mg/ liter. The reason (s) for these high values are unknown, but are probably due to rainfall runoff pre-ceding the sampling period. During 1981 the iron values decreased and the mean concentration was 1.12 mg/ liter. In Monticello Reservoir iron values have ranged from 0.02 to 0.94 mg/ liter, during the period 1978 through 1982. 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; during 1982 the mean was 0.40 mg/ liter. The yearly variations may be attributed to rainfall amounts and runoff.

The vascular hydrophyte community surveyed in Parr Reservoir was abundant and contains the greatest diversity of the water bodies studied . Much of the vegetation was located in the backwater areas of the reservoir.

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The Cannons Creak. area supports a rich littoral zone, with dense vege-tation. The community of hydrophytes at the Neal Shoals Dam sampling

[ -station has shown'very

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littl'e change in s'pecies composition since 1978.

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,Willows continue to berthe dominant form of vegetation at this loca-tion. However during July and August, when the reserwoir was drained for repair and maintenance work on the dam, emergent hydrophyte species

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J colonized some of the shoreline areas;. the species included smartweed and sedges. The subimpoundment contains a relatively diverse and 4

abundant community of hydrophytes. The rich assemblage of flora in-cluding soft rush, cattail, and willow may be attributed to the ferti-lization program being carried out at this location. In Monticello Reservoir, vegetative associations, especially within the coves, are continuing to show development. Communities of cattails, rushes, and willows dominate the coves; in these areas the substrate appears to be high in orgarjic content associated with the development of this vege-tation.

The phytoplankton species composition in Parr Reservoir showed definite seasonal patterns during the sampling periods. The mean total den-sities were lowest (1,604/ml) in January and highest (3,774/ml) in July. No major -algal . blooms occurred during 1982. Diatoms predomi-

nated the collections at all' stations during every sampling period, wiih the excepti'on of Station C in July; during this period green algae were the dominant group. At tue Neal Shoals Dam station, diatoms and green algae were the codominant phytoplankton groups during all the sampling pericds. The lowest phytoplankton densities occurred during l January and reached their peak during April. At the subimpoundment, i

phytoplankton densities were highest during' July and lowest in April.

i During January and April diatoms were the most abundant algal group at s this station, representing 90 and 63 percent, respectively, of the community. _During July, blue green algae were the most abundant group, comprising'92 percent of the community, and during October the green algae and diatoms were codominant. In Monticello Reservoir phytoplank-ton densities reached their peak at all stations during the July v

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sampling period and then declined to their lowest level during Decem-ber. Diatoms were the most abundant group of organisms collected during the colder months of the year. As the water temperature warmed (March through' May) the green algae became abundant and formed 20 to 38 percent of the population. The blue green algae then became dominant during the summer months.

An analysis of the zooplankton data during 1982 indicated that the communities did not follow any unusual trends. Based on the assess-ments of taxonomic composition and density the zooplankton communities appeared to follow seasonal expectations; and are similar in structure to the 1978-81 findings. - The data indicate that generally stable zooplankton communities exist. The rotifers were the dominant group collected throughout the study area. The overall densities and taxonomic diversities at the stations appeared to be similar to the historical data. Few differences occurred within each major study area, with Parr and Monticello Reservoirs having particular stable po pulations.

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 clu-peids (gizzard shad) dominated collections of larval fish in all areas.

The numerical abundance and wide distribution of this species .makes it an important forage fish which provides a valuable food resource for many of the recreationally important fish in the reservoirs. The ichthyofauna from Parr Reservoir and Neal Shoals were diverse; from Parr Reservoir there were 11 and 8 species collected from Stations B and C, respectively; from Neal Shoals 8 species were collected.

In the subimpoundment, the centrarchids (bream and crappie) were more abundant than from the other areas; and in general, the highest overall larval fish density occurred in the subimpoundment. Gizzard shad viii

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o increase their numbers in the subimpoundment; they were collected 'in at least one sample during April through June. The colle tions from Parr Reservoir showed the greatest increase from the previous years data. This information suggests that reproduction of

, ,the fishes (primarily centrarchids) in this reservoir is very

, ' successful, and that the fluctuating water levels do not appear to be a

- problem. }

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. Collections- of ichthyoplankton from Monticello Reservoir indicated

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that, in general, more or the same humber of taxa were collected from

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r, ths 8tations, with the exception ci" Station L, than were the previous 3

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s. year. Station L is located iear the {atake of the FPSF and this area J' - is. not being utilized by #A eprodocing fish, as suggested by the data.

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, ,The data from Mondicell'o Reservoir indicates that a developing fishery

,, c 't is' acc.o iing. ,

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The benthic macroinvertebrate communities in all of the water bodies

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• s sampled illustrated stable conditions with respect to density and I) .7 e uiversity of cr,ganiems, compared _to previous years. The only exception j

! to this das at Etation'B in Parr Reservoir; at this location there is considera61y lower ecological' stability and complexity than at any other transects (excluding the subimpoundmenr). This situation has been noted in previous years. This station is" in the ta11 race canal and is subjected to daily, high current velo.ities. Thus, the sub-strate is scoured providing a poor habitat for benthic organisms.

l, / During 1081 and 1982, however, the difference in theses parameters at I

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Transect B and the other transects . tad moderated somewhat due to an f , , , , , improvement in the indicator,s at Tranrect B. However, the relative

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level of physical stress due to thc> ststion's close proximity to the -

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FPSF was still evident. The remaining transects in Parr Reservoir (C and D) corttinue to have diverse benthic macroinvertebrate communities,

illustrative of ecological stability and complexity. At the Neal Shoals Dam station the benthic macroinverteb, tate data cantinued to show ecological stability when compared to previous years.

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The macroinvertebrate communities in Monticello Reservoir, with the exception of Transect J, exhibited relatively stable mean annual values for density, taxonomic composition and diversity, equitability, and biomass. Transect J was the only station in Monticello Reservoir which has shown consistent increases in parameters measured.

For the first time since 1979, the benthic community in the subispound-ment (Transect H) showed a decrease in density; it has continued to show a lower. number of taxa and reduced diversity since the 1981 sur-vey. This trend is expected to continue as long as intensive fertili-zation continues. The subispoundment is the only area sampled to date in which the Asiatic clam has still not been reported.

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 crappie). The clupeid family was represented by one species - gizzard shad. Gizzard shad were collected at least once during the year from every sampling station. The centrarchid tamily 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.

In Parr Reservoir, gizzard shad was the most numerous species collected and bluegill 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 density occurred sporadically from year to year; these groups included some bullheads, madtoms, yellow perch, and darters. Additionally, the whitefin shiner has appeared in collections during 1981 and 1982, and the spottail shiner first appeared in 1982. The whitefin shiner has been collected in X

Monticello Reservoir for the past three years and apparently was trans-ported into Parr Reservoir via the FPSF: the data suggests it is in-creasing its numbers and establishing a reproducing population in Parr Reservoir. Of special. interest is the white bass that occurred in Parr Reservoir for the first time during 1981. This species is occurring in larger numbers in Monticello Reservoir and apparently was transported into'Parr Reservoir through the FPSF. Age and growth studies indicated that five year classes of both gizzard shad and bluegill were found in Parr Reservoir. Most of the gizzard shad were two to three years old while most bluegill were from one to four years of age. Growth of both species was somewhat slower than populations from similar habitats in the southeastern United States. Standing crop estimates from Parr Res-ervoir increased from the previous year; this may have been attributed, in part, to the fish using the littoral zone more during 1982.

At'the Neal Shoals Dam sampling station, the clupeids and centrarchids were the dominant groups collected. The bluegill was the most abundant species captured, and it represented 31 percent of the collection.

Gizzard shad represented 13 percent of the total catch. The groups that have a small population do not appear in the collections every year and include some of the suckers, catfish, including the bu11 heads, and perch. Age and growth studies indicated that four year classes of gizzard shad and five year classes of bluegill were found. Growth of both species was somewhat slower when compared to historical data from similar habitats, in the Southeastern United States. Standing crop estimates from the Neal Shoals Dam area were considerably lower than those obtained in previous years. The low biomass may have resulted from the lowering of the water in the area during July / August 1982.

Recolonization by fish was probably not complete at the time of the rotenone application. The gizzard shad was the nost abundant species collected; it represented more than 75 percent by weight of the collec-tion.

In the subimpoundment, the centrarchid family, which comprised 82 percent of all fish collected, was the dominant group. The bluegill was the most abundant species collected and the gizzard shad was next xi l

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in total numbers collected; it represented 12 percent of the fish col-1ected. Gizzard shad are becoming more abundant every year in the sub ispoundment , in addition those individuals that - are collected are -

much larger than from the other collecting areas. These larger indi-viduals may be affecting population densities by producing more eggs.

. The larger size of these shad are attributed to the low population density, with reduced intraspecific competition, and the greater den-sity of algae present in the subispoundment Age and growth studies .

indict.ted that four year classes of the gizzard shad and five year I classes of the bluegill occurred. Growth of the gizzard shad was l faster in the subispoundment to that found in comparable habitats.

Growth of the bluegill in this reservoir was somewhat slower when

' - compared to historical data for similar areas.

In Monticello Reservoir, the fish community was dominated by the sun-fishes and gizzard shad, with a total of twenty-nine species being col-1ected during 1981; this is comparable to the previous years. Nine species of sunfish were identified with bluegill being.the most abun-dant. Gizzard shad was second in numerical abundance. The spottail shiner which was collected for the first time during 1981 did not appear in the collections this year. However, they were collected in Parr Reservoir. During 1982 only one gar was collected from Monticello Reservoir, the previous year none was collected. The few numbers col-lected during the past two years indicates that their numbers are de-creasing in this reservoir. Age and growth studies determined that six year classes of bluegill and five year classes of gizzard shad were l

found in the reservoir and that growth of both species was slower than other populations 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. The test route showed higher avian density than the

- control route. The game birds, exemplified by bobwhite, were found to be at levels similar to previous years. The bobwhite population tends to be more sedentary than mourning doves, due primarily to the migrat-ing nature of the mourning doves. The avian surveys also identified xii l

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two immature and two adult bald eagles in 1982; eagles have been sighted during the previous four years. It is possible that these im-mature 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.

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, and blue-winged teal were the most common species, accounting for more than 80 percent of the waterfowl com-munity. During the summer months few resident species were observed.

The wood duck is the only resident duck that breed =, here regularly, although mallards will occasionally occur in this region. However ,

wood ducks have not been abundant here since the reservoirs were con-structed. They bred in the 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 flue-tuating water levels in the reservoirs is disturbing to this species, so that wood ducks have probably moved to more stable areas of the Broad River.

The interpretation of the 1982 aerial photographs indicated that there was no discernable evidence of decline or change in tree vigor in the site vicinity. The land use changes noted during 1982 were areas of clear cutting for timber removal on private land, and also a cleared area of ab'out 10 acres for construction of the Nuclear Training Facility.

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TABLE OF CONTENTS Section Pag'

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SUMMARY

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 2.2.1 Introduction . . . . . . . . . . . . . . . . . 2.2-1 2.2.2 Findings and Discussion . . . . . . . . . . . 2.2-1 2.2.3 Susunary ... . . . . . . . . . . . . . . . . 2.2-13 2.3 VASCULAR HYDROPHYTES . . . . . . . . . . . . . . . . 2.3-1 2.3.1 Introduction . . . . . . . . . . . . . . . . . 2.3-1 2.3.2 Findings . . . . . . . . . . . . . . . . . . . 2.3-2 2.3.2.1 Parr Reservoir . . . . . . . . . . . 2.3-3 2.3.2.2 Neal Shoals 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 . . . . . . . . . . . . . . . . . . 2.3-6 2.3.4 Summary . . . . . . . . . . . . . . . . . . . 2.3-8 2.4 PHYTOPLANKTON . . . . . . . . . . . . . . . . . . . . 2.4-1 2.4.1 Introduction . . . . . . . . . . . . . . . . . 2.4-1 2.4.2 Findings and Discussions . . . . . . . . . . . 2.4-1 2.4.3 Summary . . . . . . . . . . . . . . . . . . . 2.4-13 2.5 ZOOPLANKTON . . . . . . . . . . . . . . . . . . . . . 2.5-1 2.5.1 Introduction . . . . . . . . . . . . . . . . . 2.5-1 2.5.2 Findings and Discussion . . . . . . . . . . . 2.5-1 2.5.3 Summary . . . . . . . . . . . . . . . . . . . 2.5-10 2.6 ICHTHYOPLANKTON . . . . . . . . . . . . . . . . . . . 2.6-1 2.6.1 Introduction . . . . . . . . . . . . . . . . . 2.6-1 2.6.2 Findings . . . . . . . . . . . . . . . . . . . 2.6-2 2.6.3 Discussion . . . . . . . . . . . . . . . . . . 2.6-9 2.6.4 Summary . . . . . . . . . . . . . . . . . . . 2.6-12 xiv i

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l TABLE OF CONTENTS (Continued)

Section Page 2.7 BENTHOS . . . . . . . . . . . . . . . . . . . . . . . 2.7-1 i 2.7.1 Introduction . . . . . . . . . . . . . . . . . 2.7-1 2.7.2 Findings . . . . . . . . . . . . . . . . . . . 2.7-2 2.7.3 Discussion . . . . . . . . . . . . . . . . . . 2.7-10 2.7.4 Sumary . . . . . . . . . . . . . . . . . . . 2.7-12 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 Sumary . . . . . . . . . . . . . . . . . . . 2.8-10 3.0 TERRESTRIAL SURVEY . . . . . . . . . . . . . . . . . . . . 3.1-1 3.1 PHOTOGRAMMETRIC ANALYSIS OF THE BROAD RIVER /

MONTICELLO RESERVOIR STUDY AREA . . . . . . . . . . . 3.1-1 3.2 BIRDS . . . . . . . . . . . . . . . . . . . . . . . . 3.2-1 3.2.1 Avian Auto Survey . . . . . . . . . . . . . . 3.2-1 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 3.2.3.1 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 . . . . . . . . . . . . . 3.2-8 3.2.5 Sumary . . . . . . . . . . . . . . . . . . . 3.2-8

4.0 REFERENCES

. . . . . . . . . . . . . . . . . . . . . . . . 4.0-1 APPENDIX A . . . . . . . . . . . . . . . . . . . . . . . . . . A-1 xv

I.

LIST OF TABLES Table Page 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 the chemical analyses of water samples collected at the station indicated during the period of January 1982 through December 1982. 2.2-27 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 1982. 2.2-36 2.3.1 Vascular hydrophytes fnund during shoreline surveys of Parr and Monticello Reservoirs, Neal Shoals Dam, and the subimpoundment, 1982. 2.3-9 2.3.2 Dominant vegetation, fish and wildlife value, expected succession, and probable major limiting factors of the littoral communities of the water water bodies in the study area, 1982. 2.3-13 2.4.1 Density, biomass, number of taxa, and taxonomic diversity of phytoplankton collected during 1982 at Parr Reservoir, Neal Shoals Dam, Monticello Reservoir, and the subimpoundment. 2.4-15 2.4.2 Summary of mean annual values for phytoplankton obtained during monitoring programs from 1978 through 1982. 2.4-22 2.5.1 Zooplankton collected in January, April, July, and October 1982, represented by numbers of organisms per major taxonomic category, species diversity, and biomass. 2.5-12 2.5.2 Summary of mean annual values for zooplankton obtained 2.5-14 during monitoring programs from 1978 through 1982.

2.6.1 Mean monthly densities of larval fish (number /100m3 )

collected in net tows, March through September 1982. 2.6-14 3

2.6.2 Mean annual densities of la~rval fish (number /100m )

1978 through 1982 2.6-21 xvi

)

LIST OF IABLES (Continued)

Table Page 2.6.3. Total annual number of taxa (surface and mid-depth) for 'ichthyoplankton,1978 through 1982. 2.6-22 2.7.1 Summary of benthic macroinvertebrate data collected from twelve stations during the 1982 monitoring program. 2.7-14 ,

2.7.2 Summary of mean annual values for benthic macro-invertebrates obtained during the 1982 monitoring program. 2.7-18 2.7.3 Summary of mean annual values for benthic macro-invertebrates obtained during monitoring programs from 1978 through 1982. 2.7-19 2.8.1 Numbers of fish and their percent abundance (%),

collected by electrofisher and gill nets during the 1982 sampling program. 2.8-12 2.8.2 Fish species collected in 1978, 1979, 1980, 1981, and 1982. 2.8-16 2.8.3 Standing crop (kg/ha) estimates of fishes from Parr and Monticello Reservoirs and the Neal Shoals Dam, 1982. 2.8-19 3.2.1 Birds observed during the auto survey - Summer 1982 3.2-10 3.2.2 Birds observed during the auto survey - Winter 1982 3.2-12 3.2.3 Results of the 1982 waterfowl surveys. 3.2-14 3.2.4 Results of avian strip census conducted in dif ferent habitats on test sites during winter and summer of 1982. 3.2-15 3.2.5 Results of avian strip census conducted in different habitats on control sites during winter and summer of 1982. 3.2-16 xvii

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 1982.

3.1.1 Land modification in study area from 1981 to 1982. 3.1-2 3.2.1 Terrestrial sampling locations and survey routes. 3.2-17 3.2.2 Average number of birds recorded on summer avian survey routes. 3.2-18 3.2.3 Comparison of game bird call counts on avian survey routes. 3.2-19 3.2.4 Avian density in selected habitats during strip Censuses. 3.2-20 3.2.5 Avian diversity in selected habitats during strip censuses. 3.2-21 xviii

)

1.0 INTRODUCTION

The present environmental monitoring program commenced in June 1978.

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.

This report contains the results of the aquatic and tarrestrial data collected for the 1982 Environmental Monitoring Program. The results of the surface water quality program include data taken by NUS Corpora-tion; the biological data were collected by Dames & Moore. The report-ing period for the surface water quality, the aquatic data, and the terrestrial data presented herein is for the year 1982; the data col-lected during 1982 are compared with earlier data where applicable.

The purpose of the environmental 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 Reservoiry 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).

1.0-1

i=

2.0 . AQUATIC SURVEY 2.1 SAMPLING LOCATIONS AND FREQUENCY The sampling locations were documented in the 1978 Biological Monitor-ing Report (Dames & Moore, 1978). The stations sampled during January through December 1982 are identical to those reported in 1978 and are identified 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-voir. During the quarterly sampling programs (January, April, July, and October), all stations and all components of the aquatic ecosystem were sampled, including: phytoplankton, vascular hydrophytes, zoo-plankton, ichthyoplankton, benthic macroinvertebrates, and adult fish.

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-terly program, occurred at Stations I and M in Monticello Reservoir, three weeks prior to and three weeks af ter the 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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1 Figure 2.1.2. Environmental Sampling Program, l January Through December 1982. I 8402060392 -02,

2.2 WATER QUALITY 2.2.1" Introduction Water quality samples and physical measurements were obtained once a month at a series of stations in the Broad River, Parr Re?arvoir, and Monticello Reservoir from January 1982 through December 1982 as part of the water quality sampling requirements for the ongoing Summer / Fair-field Environmental Monitoring Program.

The Water Quality study was designed to determine baseline conditions on Monticello Reservoir prior to the operation of - the Virgil C. Summer Nuclear Station (VCSNS) and to determine what changes -are occurring in Parr and Monticello Reservoirs as a result of operating the Fairfield Pumped Storage Facility (FPSF). The data will also be used to deter-mine if the existing water quality in the river and reservoirs meets the standards set by the South Carolina Department of Health and Environmental Control (SCDREC) as well as the criteria suggested by the United States Environmental Protection Agency (USEPA). The information may also be useful in defining the cause of any changes in the com-munities of aquatic organisms in these water bodies, should they occur.

2.2.2 Findings and Discussions A summary of the results of the in situ measurements of physical param-eters (temperature, dissolved oxygen, pH, conductivity, and Secchi disc transparency) are given by 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 are presented in Table 2.2.3.

2.2-1

The results of the 1982 investigations are discussed below for each of the principal water bodies:

• Parr Reservoir and Broad River

• Neal Shoals

• Subispoundment

• Monticello Reservoir Parr Reservoir and Broad River Physical Measurements - During the 12-month sampling period , water temperatures in the Parr Reservoir and the Broad River (Stations 1, 2, 2W, and SA) ranged from 0.5'C at Station 1 in January to 27.9'c in August at Station SA. Analyses of the data reveal a normal seasonal temperature pattern with the coldest water temperatures occurring during January and generally increasing temperatures through August followed by a decline to the low winter values. All temperatures taken at these stations were below the maximum standard of 32.2*C set by the SCDHEC (1981). No seasonal thermocline was observed at any of the stations sampled due to the shallow depths and ldgh current velocity.

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 13.3 mg/ liter, recorded at Station 1 in January. The minimum concentration, recorded at the bottom of Station 2W in June, was 4.8 mg/ liter. Most DO values fell within a range of 6.0 to 12.0 mg/ liter. The SCDHEC minimum standard for dissolved oxygen is 4.0 mg/ liter.

The pH values at Stations 1, 2, 2W, and 5A ranged from 6.8 to 9.2 units.- The minimum value was recorded at Station 2W in August. The maximum value occurred at Station 2 in January. Most values fell within the range of 6.0 to 8.5 units set by the SCDHEC (1981), except 2.2-2

l in January when values of 9.2 and 9.0 were measured at Stations 2 and 5A, respectively, and in February when a value of 9.0 was recorded at Station 1.

Conductivity values ranged from 60 umhos/cm to 100 umhos/cm. This range of values occurred at most stations throughout the year with higher values probably associated with rainfall runoff.

Transparency, as measured with a Secchi disc, was lowest (0.1 m) at Station 1 during June and December and at Station 2W in January. The highest transparency value was 2.4 meters recorded at Station 2 in November.

In general, physical values recorded between January 1982 and December 1982 at the Parr Reservoir and Broad River Stations are consistent with other data collected since June 1978 under the present environmental monitoring program (Dames & Moore; 1978, 1919, 1979a, 1980, 1981).

Water temperature and dissolved oxygen values conformed to the expected seasonal regime with low water temperatures and high dissolved oxygen concentrations recorded during the winter and maximum water tempera-tures and minimum D0 values occurring during the summer months. The pH values during 1982 were generally within the range of values (6.2 to 8.5 units) recorded during the previous years. The range of conduc-tivity values was slightly lower during 1982 (60 to 100 umhos/cm) than occurred in 1981 (65 to 160 umhos/cm), but was similar to the range encountered in 1979 (30 to 100 pmhos/cm) and 1980 (50 to 100 pmhos/cm).

The range of transparency values recorded during this collection period was similar to that occurring in 1981.

Chemical Analyses - Ammonia values at Stations 1, 2, and 5A averaged 0.4 mg/ liter. The highest ammonia concentration observed at these three stations was 0.8 mg/ liter at Stations 1 and 2 in October. Mean nitrate concentrations varied from 1.7 mg/ liter at Station SA to 2.1 mg/ liter at Station 1. The maxfmum nitrate value recorded was 2.2-3

4.0 mg/ liter at Station 1 in August. Average total phosphate concen-trations ranged from 0.13 to 0.33 mg/ liter with a minimum value of 0.06 mg/ liter at Station 1 in April and a maximum of 0.92 mg/ liter at Station 1 in December. Ammonia levels in the Broad River and Parr Reservoir were slightly higher than those reported during 1981. Aver-age nitrate and phosphate concentrations were somewhat higher than values reported in 1981.

Biochemical and chemical oxygen demands (BOD and COD) were low at all Broad River and Parr Reservoir stations. BOD averaged 1.5 mg/ liter at these stations. C0D ranged from a mean of 6.8 mg/ liter at Station 2 to 7.9 mg/ liter at Station 1. These values were slightly higher than those recorded during 1981.

The highest value for total hardness recorded at Stations 1, 2, and 5A was 36 mg/ liter (SA); this value is within the 0 to 75 mg/ liter criter-ion defining soft water (USEPA 1976). Hardness levels recorded from January through December 1982 were similar to levels which have occurred since June 1978.

Cadmium, chromium, copper, lead, and mercury were detected in all water samples collected from Parr Reservoir and the Broad River but occurred in concentrations below the sensitivity of the analytical procedures.

Concentrations of zine in excess of the analytical limit (0.01 mg/

liter) were recorded only three times during 1982: July, October, and December at Stations 2, 5A, and 1, respectively. However, in only -

one case (Station 1, December: 0.06 mg/ liter) 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) recommended by the USEPA (1976). The 1982 values were lower than those of 1981; the values for the two years reflect natural variation in the waterbodies.

2.2-4

The USEPA criterion for total iron is 1.0 mg/ liter. The mean concen-tration of iron exceeded this value at Station 1 during eight months, at Station SA during seven months, and at Station 2 during three months. The highest total iron value recorded among these three sta-tions was 7.6 mg/ liter at Station 1 in December. In general, total iron concentrations were higher during 1982 than in 1981. As has been observed in previous years of this study, the high iron concentrations were sometimes 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 high iron values were caused by runoff from heavy rainfall levels preceeding sampling. These levels 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. None were observed, except on June 6 when an oil slick about 10 yds wide by about 400 yds long was re por ted. No information is available on the source of this oil slick.

Neal Shoals Dam Physical Measurements - The water depth at this station is normally very shallow (1 meter or less) and during the months of August and September the river was dry at the designated sampling location because of dewatering for repair on the dam. Thus sampling was done in the river channel.

I Dissolved oxygen concentrations varied from 13.2 mg/ liter in January to 6.9 mg/ liter in August. These values are above the minimum value of i 4.0 mg/ liter established by the SCDHEC (1981).

l l

l Values of pH ranged from 6.6 ( August) to 8.8 (February) units. The only occasion when measurements exceeded the SCDHEC (1981) standards of 6.0 to 8.5 units was in February when pH values of 8.7 and 8.8 were f

measured. Conductivity values ranged between 50 and 100 pmhos/cm.

l Secchi disc readings ranged from 0.1 to about 1.0 meters.

2.2-5

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Chemical Analyses - Mean concentrations of ammonia, nitrate, and total phosphate at Station 11 in 1982 were 0.4 mg/ liter,1.9 ag/ liter, and 0.25 mg/ liter, respectively. These means are similar to those observed at this location in 1981. The maximum concentration of ammonia re-corded at this station was 1.0 mg/ liter in September. This compares with the 1981 maximum of 0.6 mg/1. Maxima for the other nutrients were similar for both years. Mean nutrient values at Neal Shoals have varied only slightly since 1978. The average ammonia concentration during 1982 was slightly higher than occurred during 1981. These differences reflect the natural year-to-year variations in nutrients that can be expected in river systems affected by agricultural, domes-tic, and other human activities. Average ammonia values have varied previously from 0.3 to 0.4 mg/ liter, mean nitrate values have varied from 1.8 to 2.2 mg/ liter, and average phosphate values have varied from 0.30 to 0.39 mg/ liter (Dames & Moore; 1978, 1979, 1979a, 1980, 1981).

The mean BOD and COD values recorded during 1982 were 1.8 mg/ liter and 9.6 mg/ liter, respectively. The average total hardness was 18.4 mg/ liter, a value representative of soft water (USEPA,1976). The hardness levels are similar to those reported in the earlier surveys while the BOD cnd C0D values were somewhat higher than previously reported (Dames & Moore; 1978, 1979, 1979a, 1980, 1981). These dif ferences are within the range of values expected in a river system of this type.

In 1982, of the heavy metals which occurred at Neal Shoals in concen-trations greater than the lower limit of sensitivity of the analytical methods, only total iron was found in amounts greater than the criteria recommended by the USEPA (1976). Concentrations of this metal exceeded the 1.0 mg/ liter criterion during eight months: January - Marc h, June - September, and December. The average iron concentration for the 12-month period was 2.9 mg/ liter which is twice the mean observed in 1981. The maximum iron value recorded (9.8 mg/ liter) occurred during 2.2-6

June. Previous studies have indicated that iron concentrations in the vicinity of Neal Shoals Dam are of ten greater than that recommended by the USEPA (Dames & Moore; 1978, 1979, 1979a, 1980, 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 the soils in the region.

Subispoundment Physical Measurements - Water temperatures in the subimpoundment (Station 18) ranged from a low of 5.8'C on the surface in January to 30.0*C in June. The bottom temperatures ranged from 5.5*C in January to 19.0*C in September. The results from these surveys indicate that the temperatures were within the range expected for the seasons sampled.

The dissolved oxygen (DO) concentrations ranged from a low of 7.1 mg/ liter at the surface in October to 12.7 mg/ liter in May. At the bottom the DO values ranged from a low of 0.2 mg/ liter in June, August, and October to 11.0 mg/ liter in January; all of the values were above the prescribed limit established by SCDHEC with the exception of the low values of DO neasured at the bottom during the months indicated above. Oxygen depletion at the bottom of stratified reservoirs is com-

~

mon 'during several months of the year, due to biological decomposition in the sediments and the incomplete mixing of the water.

The pH was seasured only at the surface at this station. The values for pH ranged from 6.5 to 10.1 and these were recorded during March and May, raspec tively. The pH limits established by the SCDHEC ranged from 6.0 to 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 subimpoudment occurs during this month ar.d a bloom in plankton could have caused a shif t in the pH.

2.2-7 i

1 l

Conductivity values recorded at the surface range from 58 pmhos/cm in February to 191 pmhos/cm in June. . Measurements made at the bottom ranged from a low of 59 mhos/cm in February to 128 pmhos/cm in August.

The transparency values recorded ranged from 0.9 m in June to 1.9 m in March and November.

All of the physical measurements made during this reporting period appeared to follow seasonal trends for the area. Except for the high pH value in May and depressed oxygen levels at the bottom during June, August, and October, all values were within the prescribed limits established by the SCDREC.

Chemical Analyses - The subimpoundment was sampled on a quarterly basis during January, April, July, and October. Ammonia concentrations from the four sampling periods ranged from less than 0.1 to 0.3 mg/ liter,

.the mean was 0.3 mg/ liter. Values for nitrate ranged from 0.1 to 2.5 mg/ liter during 1982 and concentrations of total phosphate ranged from 0.02 to 0.14 mg/ liter. Both the maximum and mean ammonia concentra-tions were lower in 1982 than in 1981, but were similar to those pre-viously recorded for this station (Dames & Moore; 1978, 1979, 1979a, 1980, 1981). Nitrate and total phosphate concentrations were slightly lower than 'those reported for 1981.

BOD values during the four sampling periods ranged from 1.0 to 4.0 mg/

liter. Total hardness values ranged from 22.0 to 24.0 mg/ liter and were within the range characteristic of soft water.

As with the 1979,1980, and 1981 surveys, all concentrations of heavy metals measured during the current reporting period were below the level of sensitivity of the analytical procedures.

2.2-8

Monticello Reservoir Physical Measurements - All of the temperatures recorded in the Monti-cello Reservoir (Stations 12-17 and 20) were below the 32.2*C maximum limit for Class B waters set by the SCDHEC (1981). The highest temperature recorded in the Reservoir was 29.6*C at the surface of Station 17 in July. The minimum temperature was 6.0*C at the bottom of Station 20 in January. The water temperatures taken above the thermocline followed the typical seasonal pattern. Water temperatures were generally highest in July and August and lowest in January and February.

A thermocline was observed at Station 20 from June through October at depths of 24 to 31 meters. The temperatures across the thermocline changed by between 7.6*C and 10.3*C. The depth of the thermocline at this station during 1982 is generally consistent with those recorded at this station during previous surveys (Dames & Moore; 1978,s 1979, 1979a, 1980, 1981). During May at Station 12, a weak thermocline was evident between the depths of 4 and 7 meters. Water temperatures varied from 19.8 to 15.3*C between these depths. In May, a steep, regular tem-perature gradient from 21.5*C at the surface go 8.8'C at the bottom (36 meters) was observed at Station 20. There was no sharp inflection (thermocline) discernible in this gradient.

Mean temperature ranges recorded in 1982 by the USGS Monitor located at a depth of about 6 m at the FPSF intake are generally similar to the temperature ranges measured at other stations in the reservoir during this study. On July 21 a maximum of 32.7*C was recorded by this monitor. This value exceeded the limit of 32.2*C set by the SCDHEC (1981).

Dissolved oxygen concentrations recorded at the surface (30 cm) of the Monticello Reservoir ranged between 5.7 mg/ liter and 11.7 mg/ liter.

The maximum surface D0 level occurred at Stations 12 and 20 in Feb-ruary. The minimum surface DO level was recorded at Station 17 in 2.2-9

Oc tober. All surface values were greater than the 4.0 mg/ liter standard set by the SCDREC (1981). Concentrations near the bottom of Monticello Reservoir ranged from 11.5 mg/ liter at Stations 12 and 14 in February and January, respectively, to less than 1.0 mg/ liter at Station 20 in May, July, August, September, and October. Dissolved oxygen concentrations below the state standard (4.0 mg/ liter) were measured at a number of stations during 1982: Station 20 (May through October), Stations 12 and 17 (July and August) and Station 16 (August).

During previous years of the water quality studies, the deoxygenated water was encountered primarily in nearbottom depths at these stations.

However, in 1982 two trends were observed in the pattern of depressed dissolved oxygen levels that had not been seen previously. First, the low DO values extended farther up in the water column than in the past:

at Station 20 in June, DO concentrations below 4.0 mg/ liter were found from depths of 10 meters to the bottom (29.5 meters). Previously, this layer extended to about the 20 meter depth at this station. Secondly, the layer of deoxygenated water extending from 10 to 20 meters above the bottom persisted from June through August at Station 20. In previous years, this layer reached maximum thickness in late summer and persisted for only about one month.

Low dissolved oxygen concentrations are considered typical of waters below the thermocline in deep fresh water lakes (Knight, 1965). More-over, in reservoirs, the decay of organic material on the bottom results in depletion of oxygen in the water column. Typically, this decay process reaches peak levels several years af ter a reservoir is created (Hutchinson,1957). Accordingly, the correlation of lowered dissolved oxygen concentrations with the age of the Monticello Reser-

! voir are to be expected.

At the USGS Monitor, the daily minimum D0 values during the warm season were below the state standard (minimum of 4 mg/ liter) on only five dates: July 2, 3, 4, 5, and 25. Daily mean values ranged,from 3.8 to 7.2 mg/ liter during this month. A minimum hourly value of 3.4 mg/ liter was recorded on July 25.

2.2-10

i t

The pH standards for Class B waters, as set by the SCDREC (1981), range from 6.0 to 8.5 units. The pH values recorded in the Monticello Reser-voir during 1982 ranged from a minimum of 3.6 units at the bottom of both Station 12 in December and Station 20 in October to a maximum of 8.9 units at the surface of Stations 17 and 20 in July. The pH values were below the minimum state standard at the bottom at several stations during 1982: Station 2G during April, June through October, and

'Js December; Station 12 during June, August, September, and December; and Stations 14 and 15 during December. Low pH values such as these are due to decay of organic matter and are not considered unusual near the bottom of reservoirs that are stratified. The maximum permissible pH

- value was exceeded in the pt. otic zone only at Stations 16,17, and 20 in July. These high values are believed to be the result of the photo-

~

s synthetic activity of phytoplankton, Photosynthesis removes carbon dioxide during daylight periods, shifting the system away from the production of carbonic acid and, consequently, to a less acidic state, thereby raising the pH. Thip 'is especially true of soft water areas with low buffering capacity (such as Monticello Reservoir) where wide fluctuations in seasonal and daily pH values may be expected (Knight ,

1965).

The hourly pH values recorded at the USGS Monitor in Monticello Reser-voir were outside the State standards of 6.0 to 8.5 on two occasions: ~

i. on May 8 when a .value of,8.6 was recorded emd on November 21 when a

{', . value of 3.0 'was recorded'. In general, the pH values recorded by this monitor appear to be consistent with those obserned during the Water Quality Monitoring Study.

l

[ Conductivity values in Monticell'o Reservoir ranged between 60 and

< 180 umhos/cm. The maximum vaine was recorded from near the bottom of R i station 20 in May. Most conductivity values recorded were between 80

, 'and 110 umhos/cm. Hourly conduccivity values recorded at the USGS

(' monitoring station in Monticello' Reservoir ranged from 50 to 100 pmbos/cm.

2.2-11

~

t -

4 Water transparency measurements in the Monticello Reservoir ranged from a minimum of 0.3 meters at Station 13 in June to a maximum of 2.3 meters observed at Station 12 in November.

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 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 based on previous years of collecting physical data. The depressed DO values that have occurred at some lo-cations from mid-depth to bottom are considered normal for water bodies of this type. High pH values can be expected in the photic zone during periods of high phytoplankton activity, and low pH occurs near the bottom due to decay of organic matter. Specific conductance has re-mained at a relatively low level throughout the study.

Chemical Analyses - Average ammonia values collected at Stations 12, 14,15, and 16 in the M1nticello Reservoir during 1982 ranged from 0.27 to 0.38 mg/ liter. A maximum ammonia concentration of 0.8 mg/ liter was recorded at Station 16 in October. Mean nitrate and total phosphate levels were within the narrow ranges of 1.29 to 1.65 mg/ liter and 0.10 to 0.13 mg/ liter, respec tively. Ammonia and nitrate concentrations were higher during 1982 than during 1981. Total phosphate concentra-l tions were about the same in both years (Dames & Moore,1981).

Biochemical and chemical oxygen demands in Monticello were low in 1982, j as they have been in each of the four previous years (Dames & Moore; 1

1978, 1979, 1979a, 1980, 1981). Average BOD values were between 1.3 i

and 1.6 mg/ liter. The range of mean C0D levels was between 6.8 and 7.9 mg/ liter. Total hardness values ranged from a maximum of 40 mg/

l liter to a minimum of 11 mg/ liter; these values are characteristic of i

i soft water.

2.2-12

( '.i 1 i

~

a

'- Of the heavy metals measured during 1982 in Monticello Reservoir, only iron and zine were found in concentrations that exceeded the level of

>' j sensitivity of the analytical procedures. However, concentrations of these metals did not exceed USEPA (1976) recommended criteria. Mean i

< total iron values ranged from 0.32 to 0.48 mg/ liter with a maximum concentration of 0.94 mg/ liter observed at Station 12 in June. Zinc

, values averaged 0.01 mg/ liter at all of the reservoir stations with a maximum concentration of 0.07 mg/ liter occurring at Station 12 in November and at Station 15 in May. Iron and zine are natural constitu-ents of tha clay soils in the area; therefore, periodic increases in i

their concentrations are not considered unusual. All of the other heavy metals have remained at low levels throughout the 1978-1982 studies.

2.2.3 Summary Water temperatures observed during the 1982 Water Quality Monitoring drogram were below the 32.2*C standard set by the SCDREC (1981), with the exception of the 32.7'C recorded by the USGS monitor in Monticello Reservoir in July. Dissolved oxygen concentrations recorded in the Parr Reservoir and the Broad River were all above the minimum state .,

standard of 4.0 mg/ liter. However, in Monticello Reservoir the DO levels from June to September were below the standard from mid-depths to the bottom at several sampling stations during the period June to August. The USGS monitor in the FPSF intake indicated that, on five occasions during this period, the daily mean D0 level was below the minimum standard.

The maximum state standard (8.5 units) for pH was exceeded in the photic zone of the Monticello Reservoir during July at several sta-tions. These high values can be attributed to natural photosynthetic activity and can be expected during the warmer seasons. In several instances, pH values in bottom waters of the reservoir were below the standard. Because these values were recorded near the bottom, they are 2.2-13

not considered unusual. At sampling locations in the Broad River and Parr Reservoir, the pH was above 8.5 units at several locations in Jan-uary and February. The depth of the photic zone in Monticello Reser-voir was generally greater than in Parr Reservoir or in the Broad River; this reduced turbidity is thought to be due to the depth and lentic nature of this water body. Biochemical ark! chemical exygen demands were low at all stations throughout the reporting period.

Total hardness values at all stations conformed to the O to 75 mg/ liter criterion for soft water set by the USEPA (1976). Hardness values in the subispoundment were higher than those recorded from the other water quality sampling stations. Mean nitrate, mean ammonia, and mean total phosphate concentrations were slightly greater in Parr Reservoir and tne Broad River than in Monticello Reservoir. Zine and iron were the only heavy metals that occasionally exceeded the criteria suggested by the USEPA (1976). These metals are typical constituents of soils in the watershed and, therefore, the concentrations observed are con-sidered normal.

2.2-14 I

- -x_-_______._.

1 i

Table 2.2.1 Physical measurements (temperature, oissolved oxygen, pri, conductivity, Secchi disc) made during the month

ind ica ted . Bottom depth and approxiinate depth of thermocline are also given.

Page 1 of 12

January 1982 Temperature (*C) Dissolved Oxygen pil Conductivity Approximate (mg/ liter) (umhos/cm) Thermocline Botton Secchi Station Surface Bo t tom Surface Bottom Surface Bottom Surface Bottom Depth (m) Depth (m) Disc (m)

~

I l U.S 0.5 13.3 13.3 8.2 8.3 80 80 NP 2.5 0.3 l 2 2.1 2.9 11.9 11.6 8.4 9.2 80 80 NP 4.5 0.3 2W 3.5 3.2 , 11.1 11.0 8.2 8.6 60 60 NP 3.5 0.1

" a a 80 " NP 1.0 0.3 i SA 5.I 12.I 9.0

^ " a 50 a NP 0.5 0.3 11 0.I l3.2 8.I i

12 6.5 6.2 11.0 13.9 7.2 6.3 80 80 NP 28.0 0.6 a . 13 6.4 6.4 11.0 11.0 7.0 6.7 80 80 NP 5.5 0.6

'7 6.5 6.5 11.5 11.5 7.6 7.4 80 80 14.0 0.8 g 14 NP I 15 6.4 6.4 11.3 11.1 7.4 7.3 80 80 NP 5.0 0.8 i

16 6.7 6.6 11.0 10.0 7.2 6.4 80 80 NP 15.5 1.0 17 6.5 6.5 11.0 11.0 7.2 6.4 80 80 NP 12.0 1.2 b e 12.0 1.7

! l8 5.8 5.5 11.2 11.0 6.7 59 63 NP 20 6.8 6.0 11.0 11.0 7.4 6.6 80 80 NP 31.0 0.7 i

i NP - Not Present.

I " - water depth 1 m or less; only surface measurements made.

l b - Cata collected by Dames 6 Ploore during the aquatic biology sampling. ,

c - Measurement not required.

i i

I i

1

Table 2.2.1 .(Continued) Page 2 of 12 i February 1982 j Temperature (*C) Dissolved Oxygen pH Conductivity Approximate l (mg/ liter) (p ahos/ca) Thermocline Bottom Secchi Station Surface Bottom Surface Bo t tom Surface Botton Surface Bottom Depth (m) Depth (m) Disc (m) i 1 9.4 9.4 11.5 11.5 8.6 9.0 70 70 NP 2.5 0.4 l 2 6.9 6.9 12.0 12.0 7.8 8.2 80 80 NP 4.5 0.5 1

, 2W 10.4 9.7 10.2 10.0 7.8 7.8 60 60 NP 3.5 0.3 i

a a a 1.0 0.4 I SA 9.9 10.9 8.1 80 NP 11 8.7 8.8 11.4 11.4 8.8 8.7 70 70 NP 0.5 0.5 12 7.7 6.2 11.7 11.5 7.3 6.4 80 80 NP 29.0 0.5 13 8.6 7.3 11.2 11.3 7.6 7.9 60 60 NP 13.5 0.5

. 14 8.2 6.5 11.5 11.3 7.3 7.3 70 70 NP 17.0 0.6

[.

I g 15 8.9 8.1 11.4 11.4 7.4 7.6 60 60 NP 4.0 0.6 l 16 9.0 6.4 11.4 11.0 7.4 7.6 60 60 NP 11.5 0.6 17 10.3 6.6 11.5 11.2 7.5 7.6 60 60 NP 12.0 1.0 c C 1.6 18 b 10.0 8.5 12.5 10.7 6.6 58 59 NP 20 8.6 6.2 11.7 11.1 7.4 6.3 80 90 NP 29.5 0.7 1

1  ;

i l NP - Not Present.

I

" - Water depth 1 m or less; only surface measurements made.

j b - Data collected by Dames & Moore during the aquatic biology sampling.

c - Measurement not required.

I i

1 . . - _ _ _ . _

l Table 2.2.1 (Continued) Page 3 of 12 March 1982 Temperature (*C) Dissolved Oxygen pH Conductivity Approximate I

(mg/ liter) (umhos/cm) Thermocline Bottom Secchi Station -Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m) Depth (m) Disc (m) 1 8.7 8.7 11.6 11.6 7.4 7.5 70 75 NP 2.0 0.2 2 9.1 8.2 11.1 10.8 7.3 7.3 80 80 NP 5.0 0.6 2W 9.8 9.8 9.9 10.0 7.6 7.9 70 70 NP 3.5 0.3

" a a- 80 a 1.0' O.4 1 5.5 10.2 10.8 8.2 NF 1

11 8.3 8.3 10.9 10.8 7.8 7.8 70 65 NP 1.0 0.3 l 12 8.7 7.2 10.4 10.2 7.3 7.1 75 80 NP 28.0 0.6 13 8.9 8.3 10.3 10.2 7.3 7.3 75 80 NP 10.5 0.5 r;> 14 9.6 8.0 10.4 10.4 7.2 7.2 70 65 NP 12.0 0.7 C 15 10.4 9.0 11.1 11.1 7.5 7.4 70 70 NP 5.0 0.6 l

i 16 11.4 7.7 11.3 10.6 7.3 7.3 80 70 NP 11.5 0.9 i

i 17 11.0 7.6 11.2 10.9 7.4 7.4 80 80 NP 11.5 0.9 b c c 18 11.5 9.0 11.5 9.7 6.5 59 60 NP g,9 20 8.6 7.7 10.5 10.2 7.3 6.7 80 80 NP 28.5 0.7 i

i NP - Not Present.

i a - Water depth I m or less; only surface measurements made.

j b - Data collected by Dames & Moore during the aquatic biology sampling, j c - Measurement not required.

)

L 1

. m - - - - - -

Page 4 cf 12 Table 2.2.1 (Continued) ,

April 1982 pil Conductivity Approximate Temperature ("C) Dissolved Oxygen Thermocline Bottom Secchi (mg/ liter) (umhos/cm)

Surface Bottom Surface Bottom Surface Bottom Depth (ru) Depth (m) Disc (m).

Station Surface Bottom 7.7 7.6 85 80 NP. 1.5 1.0 '

I 15.3 15.3 10.5 10.4 9.6 7.4 1.6 80 80 NP 3.5 0.8 2 15.2 14.4 9.5 7.2 7.2 100 90 NP 2.5 0.3 2W 15.3 13.5 9.4 7.0 a 8 7.8 a 90 a NP 1.0 0.8 5A 16.2 11.0 9.7 7.6 7.6 80 80 NP 1.0 bottom 11 14.6 14.5 9.8 7.2 6.1 90 90 NP 28.5 1.4 12 12.9 9.4 10.4 9.4 7.2 7.3 90 90 NP 12.5 1.5 13 13.0 12.1 10.6 10.2 7.2 90 80 NP 12.0 1.2 P 14 13.5 12.2 10.7 10.6 7.2 10.3 7.4 7.3 90 90 NP 4.5 1.1 15 15.2 13.1 10.8 7.3 7.3 90 90 NP 13.5 1.1 16 14.6 12.4 10.9 10.0 l 9.8 7.3 7.3 90 90 NP 12.5 0.9 j 17 15.6 12.5 10.9 8.3 c 66 66 NP 11.0 1.6 l 18 b 17.4 11.9 10.8 3.9 7.2 5.2 90 90 NP 25.5 1.3 20 13.2 8.7 10.5 9.8 NP - Not Present.

" - Water depth I m or less; only surface measurements made, b - Data collected by Dames & Moore during the aquatic biology sampling. l l c - Measurement not required. -1 l

l l

l l

i ,

i Page 5 of 12 Table 2.2.1 (Continued)

May 1982 Temperature (*C) Dissolved Oxygen pH Conductivity Approximate

)

(mg/ liter) (umhos/cm) Thermocline Botton Secchi i Station Surface Bottom Surface Bottom Surface Bottom. Surface Bottom Depth (m) Depth (m) Disc (a) i d

1 20.0 20.2 8.2 8.2 7.6 7.7 100 100 NP 2.0 0.9 '

2 17.6 17.5 9.7 9.9 7.5 7.4 95 95 NP 4.0 1.6 9

2W 20.4 19.7 7.6 6.9 7.2 7.4 95 95 NP 3.5 0.5 5

i SA 18.9 a 8.9 a 7.6 a 90 a NP 0.8 bottom 11 20.6 20.6 8.0 8.1 7.6 7.6 100 100 NP 1.0 0.9 21.2 12.7 8.9 7.7 8.1 7.0 90 95 4-7 27.5 1.9

12 21.2 16.0 9.8 8.4 7.6 7.4 95 95 NP 10.5 2.0

! 13 21.3 15.4 9.6 8.3 7.8 6.9 100 95 NP 14.0 1.9

- 14 9.4 8.7 7.9 7.6 95 90 NP 4.0 2.2 l g 15 21.2 19.1 1

16 22.1 15.5 9.8 7.8 8.0 7.4 100 100 NP 11.0 2.2 j

1 22.1 15.3 9.- 6.8 7.8 7.4 100 100 NP 11.5 2.1

, 17 12.3 12.7 0.3 10.1 c 88 73 NP 10.5 1.7 18b 26.0 d

21.5 8.8 9.2 0.3 8.0 6.1 90 180 36.0 2.2 20 NP - Not Present.

! a - Water depth 1 m or less; only surface measurements made, j b - Data collected by Dames & Moore during the aquatic biology sampling.

.: c - Measurement not required.

]

d - No thermocline present but steep, regular temperature gradient from surface to bottom.

I i

1

Table 2.2. (Continued) Page 6 of 12 .

i June 1982

! Temperature (*C) Dissolved Oxygen pti Conductivity Approximate

! (ag/ liter) (unhos/ca) Thermocline Botton Secchi i Station Surface Bnttom Surface Bottom Surface Bottom Surface Bottom Depth (a) Depth (m) Disc (m) i 1 23.6 23.8 7.6 7.8 7.3 7.3 75 75 NP 2.5 0.1 ,

l 2 25.4 24.4 6.8 6.1 7.2 7.2 80 80 NP 5.0 0.2

! 2W 24.9 24.6 6.4 4.8 7.2 7.3 80 80 NP 3.5 0.2 SA !4.8 a 6.6 a 7.8 a 60 a NP 1.0 0.2 11 23.4 23.4 7.6 7.6 7.4 7.6 60 70 NP 1.5 0.1 f

12 23.9 19.5 6.4 4.6 7.0 5.5 70 70 NP 29.0 0.7

13 23.7 23.1 6.5 6.2 7.0 7.1 70 70 NP 13.0 0.3  !

f ." 14 ~23.7 22.4 6.5 5.4 7.0 7.1 70 95 NP 17.5 0.6 w

i ,5 15 25.3 24.4 8.2 6.8 7.2 7.2 75 75 NP 4.0 0.9 O

j 16 26.2 23.1 8.8 5.4 7.5 7.4 75 70 NP 12.0 0.9

.J

. 17 26.9 22.9 9.2 5.0 8.4 7.4 70 75 NP 12.0 0.9 b c c 1.4 18 30.0 14.0 10.8 0.2 8.7 191 81 NP 1

4 20 24.8 11.6 8.3 3.0 7.1 4.0 70 80 26-29 29.5 0.9 l

i j

1 NP - Not Present.

i a - Water depth 1 m or less; only surface measurements made.

j b - Data collected by Dames & Moore during the aquatic biology sampling.

! c - Measurement not required.

1 1

i i

__ . . . . _ _ ~ .

l 4

1 i Table 2.2.1 (Continued) Page 7 of 12 i

July 1982

~~

I Temperature (*C) Dissolved Oxygen pH Conductivity Approximate j (mg/ liter) (pmhos/cm) Thermocline Bottom Secchi i Station Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m) Depth (m) Disc (a)

I '26.9 26.9 6.8 6.8 7.2 7.2 80 80 NP 2.5 0.3 i.

2 26.3 26.3 6.0 6.0 7.2 7.4 80 80 NP 5.0 0.6 2W 27.3 26.6 5.5 5.2 7.3 7.6 80 75 NP 3.5 0.3 '

^ a a 1.0 0.5

! SA 27.6 8 6.2 7.6 70 NP

11 26.1 26.0 7.2 7.2 7.2 7.2 80 70 NP 0.5 0.3 12 27.5 22.8 8.4 2.7 8.1 6.6 80 75 NP 28.0 1.2.

a 13 27.5 25.7 8.8 5.3 8.0 6.9 75 70 NP 10.0 1.3 i

j w 14 28.1 25.4 8.8 4.6 8.2 6.7 80 80 NP 11.5 1.0 t

j 7 15 28.2 27.1 8.4 4.8 8.2 7.0 80 80 NP 3.5 1.2

. w

' "' 16 28.4 25.6 8.9 4.4 8.6 6.8 80 80 NP 10.0 1.2 17 29.6 25.6 9.1 3.2 8.9 6.6 80 80 NP 10.5 1.1 b c 92 95 NP 11.0 1.5 18 29.2 13.3 9.6 0.8 9.0 3 20 27.9 11.2 8.4 0.8 8.9 5.0 80 80 24-26 31.0 1.4 i

4 1

NP - Not Present.

2 a - Water depth I m or less; only surface measurements made.

b - Data collected by Dames & Moore during the aquatic biology sampling.

c - Measurement not required.

t I

i i

)

1

Table 2.2.1 (Continued) Page 8 of 12 4

August 1982 l

Temperature (*C) Dissolved Oxygen pH Conductivity Approximate (mg/ liter) (u mhos/cm) Thermocline Bottom Secchi i Station Surface Bottom Surface Bottom Surface Bottom Surface Bottom Depth (m) Depth (m) Disc (m) 4 1 26.7 26.6 7.1 7.1 7.3 7.2 90 95 NP 2.0 0.2

2 27.5 27.2 6.4 6.0 7.0 7.0 90 90 NP 4.5 0.4 2W 27.7 27.4 5.4 5.3 6.8 6.8 80 80 NP 2.5 0.4 a ^ a a 1.0 0.4 5A 27.9 6.4 7.0 80 NP a a a a 1.0 0.2

1I 26.2 6.9 6.6 90 NP l

\

12 27.0 25.6 5.8 3.0 6.8 5.4 85 85 NP 28.0 0.9 i

13 27.0 26.9 6.1 5.5 6.9 6.8 80 80 NP 12.5 0.7 1

4

,o 14 27.2 26.5 0.6 4.2 7.0 6.8 80 80 NP 17.0 0.8 4

15 27.6 27.5 6.9 6.5 7.1 7.1 80 75 NP 4.0 .1

[

16 28.2 26.8 7.6 2.6 7.2 6.6 70 70 NP 10.0 1,3 i

17 28.8 26.7 7.9 1.0 8.4 6.4 80 80 NP 11.5 1.2 b c c g,3 f 18 28.3 16.3 9.0 0.2 8.5 105 128 NP 20 27.5 12.0 6.9 0.7 7.2 4.6 80 90 27-29 31.0 1.2 i

l NP - Not Present.

a - Water depth 1 m or less; only surface meacurements made.

b - Data collected t.y Dames & Moore during the aquatic biology sampling. '

C l - Measurement not required.

i l

i

Table 2.2.1 (Continued) Page 9 of 12 4

September 1982 _

Teraperature ( *C) Dissolved Oxygen pH 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 23.4 23.0 7.4 7.6 7.2 7.2 100 100 NP 2.0 0.2

, 2 25.2 25.2 6.2 6.2 7.0 7.0 80 80 NP. 4.5 0.8 i 2W 24.9 24.8 6.6 6.4 6.9 6.9 80 80 NP 3.5 0.6 -

a a a a 1.0 0.6

! SA 25.2 6.5 7.0 75 NP

" 7.2 a 7.2 a #

1.0 11 23.5 100 NP 0.2 12 25.3 24.7 6.2 5.8 7.0 5.7 90 90 NP 28.5 1.1

{ 13 25.4 25.4 6.8 6.5 7.0 7.0 80 80 NP 5.5 1.0 14 25.8 25.2 8.2 5.6 7.3 6.8 90 80 NP 12.0 1.2

.[

15 26.0 25.4 9.0 6.2 7.9 7.0 90 90 NP 4.5 1.2 h

! 16 25.7 25.2 6.6 4.4 6.9 6.6 80 80 NP 14.0 1.8 17 26.0 25.2 8.6 4.4 7.3 6.7 90 90 NP 12.0 1.5 c c g,g 18 b 25.7 19.0 8.9 0.3 8.7 78 101 NP 20 25.4 12.5 6.0 0.6 7.0 4.0 90 90 26-28 31.0 1.6 4

NP - Not Present j a - Water der- or less; only surface measurements made.

1 b - Data collt.cted by Dames & Moore during the aquatic biology sampling.

l c - Measurement not required.

1 l

4

Page 10 of 12 Table 2.2.1 (Continued)

October 1982 pH Conductivity Approximate Temperature (*C) Dissolved Oxygen Thermocline Bottom -Secchi (mg/ liter) (p ahos/cm)

Surface Bottom Surface Bottom Surface Bottom Depth (m) Depth (m) Disc (m)

Station Surface Bottom 7.8 7.3 7.2 100 100 NP 2.5 0.8 1 19.5 19.2 7.9 6.5 7.0 7.0 90 90 NP 5.0 1.3 2 23.1 23.1 6.5 5.8 7.0 7.0 80 90 NP 3.5 0.4 2W 22.1 22.1 6.0 a a a NP 1.0 0.7 l

^ 6.8 7.4 90 l 51. 22.5 7.0 7.0 7.1 100 100 NP 1.0 0.8 11 20.1 20.0 7.0 7.0 6.1 85 85 NP 28.0 1.6 12 23.1 22.6 6.9 7.0 7.0 6.9 80 80 NP 12.5 1.6 13 23.1 23.0 6.8 6.8 7.0 80 80 NP 17.0 1.5 l

." 14 23.1 23.1 6.6 6.0 6.9 7.0 7.0 80 80 NP 4.0 1.5 15 23.0 23.0 6.7 6.6 7.0 7.0 80 80 NP 10.5 1.6 16 23.1 23.1 6.6 6.6 6.7 6.8 75 75 NP 11.5 1.8 17 23.0 23.0 5.7 5.8 7.0 e 72 109 NP 11.0 1.7 18 b 23.0 12.3 7.1 0.2 7.0 3.6 80 105 28-31 34.0 1.6 20 23.2 11.4 6.6 0.6 NP - Not Present.

a - Water depth I m or less; only surface measurements made, b - Data collected by Dames & Moore during the aquatic biology sampling, c - Measurement not required.

Table 2.2.1 (Continued) Page 11 of 12 November 1982 Temperature (*C) Dissolved Oxygen pH Conductivity Approximate (mg/ liter) (pmhos/cm) Thermocline Bottom Secchi Station Surface Bo t tom Surface Bo t tom Surface Bottom Surface Bottom Depth (m) Depth (m) Disc (m) 1 9.9 9.7 10.5 10.9 7.6 7.8 80 80 NP 3.5 0.6 2 17.5 17.1 7.9 7.8 7.6 7.8 80 80 NP 5.0 2.4 2W 14.7 13.9 8.2 8.0 7.6 7.7 80 80 NP 4.0 1.0

^ a a a 1.0 bottom 5A 16.9 9.6 8.2 80 NP i

l 11 10.6 10.4 10.9 10.8 8.0 8.4 80 75 NP 1.5 0.7 12 17.4 16.2 8.2 8.0 7.3 6.3 80 85 NP 27.0 2.3 13 17.4 17.4 8.2 8.6 7.4 7.3 80 80 NP 12.0 2.0

] y

! y 14 17.7 17.4 8.4 8.6 7.4 7.4 80 80 NP 14.0 2.0 fU 15 17.7 17.5 8.4 8.6 7.8 7.9 80 80 NP 3.5 2.1 l 16 17.6 17.3 8.0 7.8 7.3 7.3 80 80 NP 11.5 2.1 11.0 2.0 17 17.7 17.2 7.0 7.6 7.4 7.6 80 80 NP b 5.8 7.9 c C 1.9 t

18 15.5 14.0 8.0 65 65 NP 20 17.4 16.3 7.9 5.4 7.4 6.6 80 100 NP 27.0 2.2 NP - Not Present.

a - Water depth I m or less; only surface measurements made, b - Data collected by Dames & Moore during the aquatic biology sampling.

c - Measurement not required.

i i

1

Table 2.2.1 (Continued) Page 12 of 12 December 1982 Temperature (*C) Dissolved Oxygen pil Conductivity Approximate (mg/ liter) (pmhos/cm) Thermocline Bottom Secchi Station Surface Bottom Surface Bottom Surface Bottom Surface Bcttom Depth (m) Depth (m) Di sc (m) 1 6.1 6.1 11.6 12.0 8.2 8.4 60 60 NP 4.0 0.1 2 13.5 9.2 8.5 9.6 7.8 8.0 80 70 NP 4.5 1.1 2W 8.6 7.7 9.5 10.1 8.1 8.4 80 65 NP 4.0 0.2 a a a 1.0 0.2 SA 10.8 10.0 8.2 75 NP 11 6.2 6.2 11.4 11.4 7.9 8.1 60 60 NP 1.0 0.1 12 13.6 10.3 8.7 9.8 7.0 3.6 65 55 NP 28.5 1.7 13 13.6 12.2 8.6 9.1 7.2 6.7 60 65 NP 13.0 1.5

." 14 15.9 13.4 8.5 8.4 6.5 5.8 70 65 NP 13.0 0.7 15 13.7 13.6 8.8 8.8 6.2 5.8 60 60 NP 4.5 1.7 16 13.3 13.2 8.7 8.7 6.9 6.8 60 60 NP 12.5 2.0 17 13.1 13.0 8.7 8.6 7.0 6.8 60 60 NP 10.0 2.1 b c c 1.5 18 11.0 10.5 7.6 7.1 6.7 60 60 NP 20 13.4 11.7 8.6 8.6 7.4 5.0 70 80 NP 28.5 1.8 NP - Not Present.

- Water depth 1 m or less; only surface measurements made.

b - Data collected by Dames & Moore during the aquatic biology sampling. .

c - Measurement not required.

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Table 2.2.2 (Continued) Page 2 of 9 Station 2 Minimum Maximum Standard Determination Units Value Value Range N Mean Deviation

Sodium mg/l 5.5 9.8 4.30 12 8.10 1.16 Calcium mg/l 2.8 5.0 2.20 12 3.45 0.64 Magnesima mg/l 1.2 3.0 1.80 12 1.83 0.48 Chloride mg/l 4.0 ~ 10.0 6.00 12 6.83 1.59 Sulfate (SO4 ) mg/l <l.0 16.0 15.00 12 7.42 3.68 l Total Dissolved Solids ag/l 49.0 114.0 65.00 12 76.33 18.17 i Total Suspended Solids mg/l <1.0 24.0 23.00 12 10.00 8.17

] MO-ALK mg/l 14,0 26.0 12.00 12 18.75 3.08 P - ALK (CACO 3) mg/l 0.0 0.0 0.00 12 0.00 0.00

. Ammonia (Nil3 ) mg/l <0.1 0.8 0.70 12 0.41 0.26 i Biochemical oxygen Demand mg/l <1.0 3.0 2.00 12 1.50 0.67

• Cadmium mg/l <0.01 <0.01 u.00 12 <0.01 0.00 Chevalcal Oxygen Demand mg/l <4.00 18.00 14.00 12 6.75 4.03

.N Total Chromium mg/l <0.03 <0.03 0.00 12 (0.03 0.00 y Co pper mg/l <0.02 <0.02 0.00 12 <0.02 0.00 l g Total liardness (CACO3 ) mg/l 12.0 25.0 13.00 12 16.25 3.17 Total Iron mg/l 0.21 2.80 2.59 12 0.92 0.72

Lead mg/l <0.05 <0.05 0.00 12 <0.05 0.00 j Me rcury mic ro-gm/1 <0.20 <0.20 0.00 12 <0.20 0.00 Nitrate (NO3 ) mg/l 1.4 2.6 1.20 12 1.80 0.36

$ Or ti10-Phos pha te mg/l 0.01 0.16 0.15 12 0.08 0.05 Total Phosphate mg/l 0.07 0.20 0.13 12 0.13 0.05 Silica (SIO2) mg/l 9.0 18.0 8.80 12 13.35 2.58

! Turbidity NTU 4.0 55.0 51.00 12 21.87 16.42 i Zine mg/l <0.01 0.01 0.00 12 0.01 0.00 l Carbon Dioxide mg/l 3.00 15.0 12.00 12 8.67 4.60

) Kjeldahl N mg/l NR NR NR NR NR NR 4 tk> ron mg/l <0.1 0.2 0.10 4 0.12 0.05 I

I i

Note: In those cases where the analyses showed concentrations to be below tl.e detection limit of the analytical procedure, the value of the detection limit itself was used to calculate the mean and

standard deviation. Also, values presented in the text have been rounied to the sensitivity level i of the analytical procedures.

I Note: N = the number of observations NR - Indicates K-N not required at this station.

)

i

. Table 2.2.2 (Continued) Page'3 of 9 Station 5A Minimum Maximum Standard Determination Units Value Value Range N Mean Deviation Sodium mg/l 6.8 9.8 3.00 12 7.78 1.00 Calcium mg/l 2.4 4.0 1.60 12 3.13 0.45 Magnesium mg/l 1.7 6.0 4.30 12 2.31 1.20 Chloride mg/l 4.0 10.0 6.00 12 6.67 1.72 Sulfate (SO4) mg/l 2.0 20.0 18.00 12 7.33 4.96 Total Dissolved Solids ag/l 64.0 94.0 30.00 12 78.75 10.66 Total Suspended Solids ag/l 4.0 89.0 85.00 12 22.08 23.52 MO-ALK mg/l 14.0 27.0 13.00 12 18.00 3.38 P - ALK (CACO3 ) mg/l 0.0 0.0 0.00 12 0.00 0.00 Ammonia (Nti3 ) mg/l <0.1 0.7 0.60 12 0.40 0.17 Biochemical Oxygen Demand mg/l <l.0 4.0 3.00 12 1.58 0.90 Cadmium mg/l <0.01 <0.01 0.00 12 <0.01 0.00 Chemical Oxygen Demand mg/l <4.0 18.0 14.00 12 7.75 3.98 i Tota 1 Chromium mg/l <0.03 <0.03 0.00 12 <0.03 0.00

" Co pper mg/l <0.02 <0.02 0.00 12 <0.02 0.00 7 Total liardness (CACO3 ) mg/l 14.0 36.0 22.00 12 17.42 6.02 i @ Total Iron mg/l 0.34 2.90 2.56 12 1.26 0.66

Lead mg/l <0.05 <0.05 0.00 12 <0.05 0.00 ,

I Me rc ury micro-gm/l <0.20 sJ.20 0.00 12 <0.20 0.00 mg/l 0.25 Nitrate (NO3 ) 1.3 2.1 0.80 12 1.72 Ortho-Phosphate mg/l 0.04 0.28 v.24 12 0.11 0.06 Total Phosphate mg/l 0.08 0.80 0.72 12 0.23 0.20 Silica (S102) mg/l 9.7 17.0 7.30 12 12.56 2.35

Turbidity NTU 7.5 73.0 65.60 12 26.63 17.14 Zinc mg/l <0.01 0.01 0.00 12 0.01 0.00 Carbon Dioxide mg/l 2.0 23.0 21.00 12 8.75 6.15 Kjeldahl N mg/l NR NR NR NR NR NR Boron mg/l <0.1 0.1 0.00 4 0.10 0.00 i Note: In those cases where tue analyses showed concentrations to be below the detection limit of the analytical procedure, the value of the der.ection limit itself was used to calculate the mean and standard deviation. Also, values presented in the text have been rounded to the sensitivity level of the analytical procedures.

Note: N = the number of observations NR - Indicates K-N not required at this station.

Table 2.2.2 (Continued) Paga 4 of-9 Station 11 Minimum Maximum Standard.

Determination Units Value Value Range N Mean Deviation Sodium mg/l 4.2 12.0 7.80 12 6.98 '

2.46 Calcium ag/l 2.8 7.0 4.20 12 3.72 1.08 Magnesium mg/l 1.4 6.0 4.60 12 2.21 1.22 Chloride ag/l 4.0 13.0 9.00 12 7.00 2.59 Sulfate (SO4 ) mg/l <l.0 17.0 16.00 12 5.29 4.46 Total Dissolved Solids mg/l 54.0 112.0 58.00 12 73.50 17.17 Total Suspended Solids ag/l 1.0 320.0 319.00 12 60.58 69.70 MO-ALK mg/1 11.0 26.0 15.00 12 17.58 4.64 P - ALK (CACO3 ) mg/l 0.0 0.0 0.00 12 0.00 0.00 l Ammonia (Nil3 ) mg/l <0.1 1.0 0.90 12 0.42 0.29 j Biochemical Oxygen Demand mg/l <l.0 3.0 2.00 12 1.75 0.75

Cadmium mg/l <0.01 <0.01 0.00 12 <0.01 0.00 Chemical Oxygen Demand mg/l <4.0 20.0 16.00 12 9.58 5.48 i Total Chromium mg/l <0.03 <0.03 0.00 12 <0.03 0.00 o Copper mg/l <0.02 <0.02 0.00 12 <0.02 0.00

! s Total liardness (CACO3 ) mg/l 15.00 41.00 26.00 12 18.42 7.18 1 Total Iron mg/l 0.49 9.80 9.31 12 2.92 3.03 Lead mg/l <0.05 <0.05 0.00 12 <0.05 0.00 Me rc ury micro-gm/1 <0.20 <0.20 0.00 12 <0.20 0.00 '

Nitrate (NO3) mg/l 1.2 3.1 1.90 12 1.92 0.55 j Ortho-Phosphate mg/l 0.04 0.24 0.20 12 0.10 0.06 i Total Phosphate mg/l 0.06 0.44 0.38 12 0.25 0.13 i Silica (Slo 2) mg/l 10.0 17.0 7.00 12 13.92 2.39 Turbidity NTU '

5.00 140.0 135.00 12 48.04 47.04 Zinc mg/l <0.01 0.03 0.02 12 0.01 0.01 ,

Carbon Dioxide mg/l 2.00 20.0 18.00 12 8.25 5.97 Kjeldahl N mg/l NR NR .4R NR NR NR Ibron mg/l <0.1 <0.1 .00 4 <0.10 0.00 4

i

, Note: In those cases where the analyses showed concentrations to be below the detection limit of the analytical procedure, the value of the detection limit itself was used to calculate the mean and

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Note: N = the number of observations NR - Indicates K-N not required at this station.

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2e2-35

Table 2.2.3 Summary of data taken from the USGS monitoring station at ths Fairfield Purped Storaga Facility inte:ks in Monticello Reservoir for the period January through December 1982.

Temperature (*C) Dissolved Oxygen pil Conductivity (mg/ liter) (umhos/cm)

Range Daily Mean Range Daily than Range Daily Mean Range Daily Hean Min. Max. Min. Max. Min. Max. Min. Max. Min. Max. Min. Max. Min. Max. Min. Max.

January 1.0 10.1 4.3 9.8 9.7 14.3 10.0 12.9 6.3 7.0 6.7 6.9 32 71 56 69 February 6.1 11.8 6.7 9.5 10.0 11.8 10.3 11.7 6.5 7.0 6.7 6.9 39 67 50 62 March 6.8 18.4 8.1 13.8 8.7 11.5 9.8 11.1 6.7 7.1 6.7 7.0 50 79 57 71 April 10.0 19.2 11.6 17.6 8.0 10.8 8.4 10.5 6.5 7.5 6.7 7.1 57 82 66 74 May 15.5 26.7 17.0 23.4 6.3 11.4 6.9 10.1 6.4 8.6 6.6 8.4 50 85 61 76 i

y June 21.2 29.2 23.6 26.9 4.1" 9.9" 4.8 7.9 6.3 8.3 6.4 7.2 47 77 57 67 July 25.0 32.7 25.9 29.2 3.4" 9.5" 3.8" 7.0" 6.2" 8.5" 6.3" 7.4" 50" 75" 60* 70*

August 25.4 29.7 26.9 28.3 4.5" 8.5 5.0" 7.3" 6.3 7.7 6.4 7.1 52 76 60 67 September 22.2 28.5 24.4 27.0 4.6 9.4 5.0 7.7 6.4 8.1 6.5 7.0 65 100 68 80 8 8 a October 15.4" 25.0" 18.2" 24.3" 5.6" 9.3" 6.7" 8.7" 6.6" 7.2" 6.7 7.0" 68 95" 70* 77 November 12.2" 20.2" 15.0" 19.2" 7.7" 10.5" 7.9" 8.7" 8.0" 8.1" 6.9" 7.1" 72" 98" 74" 87" December 6.0 16.5 10.8 15.4 6.4 12.1 6.9 9.5 6.5 7.1 6.8 7.0 56 90 77 86

" Data incomplete for the month.

l i;

, 2.3 VASCULAR HYDROPHYTES 2.3.1 Introduction i

The vascular hydrophytes described in this study included those higher plants with specialized conductive or vascular tissue requiring a hydric j

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 growth forms of hydrophytes included in this study, as defined by Sculthorpe (1967), are:

1. Bnergent - These are rooted to the soil and are close to or 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 of ten entangled in other plants. They may be either completely sub-merged, at the surface, or emergent from the surface.

i i

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 much of the year. T Use of these forms was considered both in the categorization of the plant as well as in describing the habitat to which it was confined.

i i

j 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 2.3-1 1

- - , ,_,,~_-,,,.--,v-,.,_rr,,.n-..w,. .-r,.m,,,y., , . _ ,,,.,e, - - -,_r ,.,w -,._, _,._-_... ,, , , , - - . . . . . - , . , _ , , , . , , , . . . . , . , _ , - - - , -

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 were found growing in the study area during 1982 (Table 2.3.1) . Numbers of species in each reservoir variad.

Monticello Reservoir had 19 species observed; Neal Shoals Dam, 13; Monticello Reservoir subimpoundment, 35; and Parr Reservoir had 38 (including adjacent inundated habitats and the Cannons ( eek area).

Stand densities, referred to as abundant, moderately abundant, and sparse in Table 2.3.1 were determined by the growth habit of the spe-cies. For example, cattails (Typha latifolia) and softrush (Juncus effusus) occasionally 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 along the shoreline occurred 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, sof trush, and black willow (Salix nigra) , and bulrush (Sci pus cyperinus) .

i The dominant vegetation form throughout the littoral zone of the study area was emergent (Table 2.3.1). Deeper water usually supported no vegetation; although the Monticello subimpoundment was dominated by Potamogeton which has both submerged and floating leaves (a condition l

termed heterophylly). Thus , most vegetation was usually confined to l

areas with shallow water and gently sloping and non-shaded banks. The l

most extensive hydrophyte communities occurred in Parr Reservoir, either in backwater areas or on the islands. In all areas where the overhead canopy was very dense and the banks very steep, littoral vegetation was sparse ; this re'.uced amount of vegetation is due to the diminished sunlight and unsuitable substrate.

l l

2.3-2

Monticello is a young reservoir which, unlike the subimpoundment, receives relatively little nutrient subsidy (i.e., fertilizer). It is only sparsely vegetated in areas exposed to continuous wave action.

Thus, the development of 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 sub sec tions.

! 2.3.2.1 Parr Reservoir Parr Reservoir supports the most abundant (i.e., most extensive) plant community of the water bodies studied. Species diversity (observed numbers of species) is also highest in this reservoir. These areas are rich in species and support dense populations of composites, grasses, and pickerel weed (Pontederia cordata) . The heterogeneous substrate ,

the presence of extensive, low-lying shorelines and islands, along with the frequently fluctuating water levels, appear to promote the growth of a relatively diverse community of hydrophytes throughout much of Parr Reservoir. However, at the sampling stations (littoral zone), little or no vegetation is supported due to the very rocky and steep banks. The shallow backwater area parallel to the railroad and perpendicular (going north) to the tailrace canal supports numerous aquatic species, includ-ing pondweed (Potamogeton diversifolius) and water-plantain (Alisma subcordatum), which are not found growing elsewhere in the reservoir.

A large, artificial marsh (spoil area) which is periodically floaded (north of railroad, Figure 2.1.1) also supports abundant hydrophytic vegetation and provides support to numerous water fowl. The numerous islands in the reservoir are dominated by either black willow or grasses (principally Echinocloa spp.).

Smartweed (Polygonum hydropiperoides was also abundant in Parr Reservoir. Numerous species were moderately abundant (Table 2.3-1) suggesting a fairly equitable distribution of species in this area.

The Cannons Creek area supports a rich littoral zone, especially along the north side, where the confluence of a small tributary stream with 2.3-3

the reservoir has resulted in densely vegetated, marsh-like habitat.

Dominant species in this area were marsh day flower (Anellema keisak),

Arthraxon hispidus var. cyptatherus, and smartweed.

The sampling station at Cannons Creek supports the most abundant vegeta-tion of any of the sampling stations throughout the study area. Domi-nant species at this station included boltonia (Boltonia asteroides),

bulrush (Scirpus cyperinus), cattails, and lizard's tail (Saururus cernuus).

Besides bulrush, other sedges were also numerous. These included caric sedge (Carex lurida), spikerush (Eleocharis obtusa), and flat-top sedge (Cyperus iria). Although some areas near the landing were periodically mowed, the Cannons Creek area supports a relatively stable and produc-tive littoral community. A few planted cypress (Taxodium distichum) saplings also occur in this area.

2.3.2.2 Neal Shoals Dam During July and August, the Neal Shoals Dam reservoir was temporarily drained for construction and maintenance on the dam. As a result some of the shoreline areas near the landing area were colonized by emergent species. These included moderately abundant populations of smartweed, hibiscus (Hibiscus moscheutos), marsh-fleabane (Pluchea camphorata), and flat-topped sedge. The cove in which the control station is located is dominated primarily by black willow (Salix nigra). No hydrophytic vegetation was observed at the littoral zone sampling station.

2.3.2.3 Subimpoundment The subimpoundment contains a relatively diverse and abundant community of vascular hydrophytes. As a result of monthly (March through August) 2.3-4

fertilisation, nutrient enrichment and accelerated eutrophication have been occurring in this reservoir. This change was manifested by a rapid

. development of the littoral zone, particularly in the coves which are, abundantly populated by sof trush, cattail, and willow. Alder (Alnus serrulata) is also occasionally associated with these species in moder-ate abundance. -Further evidence for the enrichment is the extreme abun-dance of pondweed (Potamogeton diversifolius) during this growing season. This species has .shown somewhat cyclical blooms, being rela-tively sparse during the 1981 season and extremely abundant during the 1980 season. Species which are moderately abundant and occur occa-sionally in this reservoir are spike rush (Eleocharis obtusa and E.

quadrangulata), sof t-stem bulrush (Scirpus validus), and cut grass (Leersia oryzoides).

The sampling station, though slightly exposed ~ b) wave action, appears to maintain a relatively well-developed littoral community. Sof trush is the dominant emergent species although it occurs in small clumps rather than extensive stands. Pondweed (submerged) is dominated in slightly b deeper water at this station. -

2.3.2.4 Monticello Reservoir

, As noted in previous studies (Dames & Moore,1981) vegetative growth has been particularly abundant within the coves of Monticello Reservoir.

These vegetative associations continue to develop in this reservoir as evidenced by the 1982 surveys. The coves are dominated by cattails, sof trush, bulrush, and willows especially near the ends of the coves where the water is shallow. Spike rush was. occasionally distributed as moderately abundant mats along the shores and in deeper water in these Coves.

Some areas have eroded significantly into steep gulleys with kudzu being the only vegetation along the upper edges of the banks.

2.3-5

As observed in the previous sampling period (Dames & Moore,1981), indi-vidual sampling stations in the littoral zone of Monticello Reservoir have supported very little vegetation. M:st of the stations are located along exposed shorelines and therefore exhibited very little vegetative development. Because these areas are frequently disturbed, p1 mat colonization will continue to be slow or negligible in the future.

2.3.3 Discussion 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) eco-systems, hydrophytes are also important contributors of otganic matter to the detrital food chain. These plants aleo provide habitat, cover, and food for many species of animals, such as insect larvae, fish, birds, and mammals. Growth along reservoir edges can also protect the banks from erosion caused by wave action. This latter function is important in stabilizing the littoral zone and its associated faunal components.

The overall controlling factors in the distribution and abundance of hydrophytes in the study area appear to be water depth and wave action.

Thus, the major associations of hydrophytes are usually restricted to shallow areas, primarily protected coves and backwater areas. Because of their rapid vegetative growth, the cattails and sof trush are capable of exploiting these habitats. These species form relatively large mono-typic stands thereby limiting other species from growing within an established stand. However, the overall effect is a stabilization of shoreline substrates and in facilitating development of a littoral community. Organic sediments are usually higher within these stands as a result of increased siltation, allowing perhaps less tolerant species to colonize the stands. Some tall species such as bulrush (S. cyper-inus) are able to grow successfully within softrush stands but less so

- in cattail stands. Other shorter plants, such as spikerush (Eleocharis sp.) appear to colonize the periphery of these stands. This does not 2.3-6

mean that cattails or softrush are indispensable for plant succession, as many areas within the coves are (perhaps randomly) colonized by those propagules first arriving. The facilitation of succession by early colonizers such as cattails is common in shallow areas of lakes (Scul-thorpe , 1967) .

Other significant factors limiting development of littoral zones, besides water depth and wave action, are steep banks and a dense over-head canopy. The effects of these factors are most apparent at the Neal Shoals Dan station where a dense overstory of willows, cottonwoods, and red ~ maple, along with steep banks severely limit herbaceous vegetation along the shoreline. When water levels were dropped during the growing season, some areas exposed to sunlight near the boat launching ramp became densely vegetated. It is likely that limiting factors such as shade, steep banks, and water depth frequently act together to influence patterns of plant establishment. The high turbidity of the Broad River may also contribute significantly as a limiting factor. It is uncertain how the fluctuating water levels have affected plant distribution.

However, it may be that these fluctuations have expanded the width of the littoral zone and those species capable of tolerating such fluctua-tions3(e.g., cattails) become established.

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) as in Juncus; and the production of spongy tissues (aerenchyma) as in pickerelweed which facilitate oxygen metabolism in relatively anaerobic conditions. Thus, many of those species colonizing the shorelines throughout the study area are adapted to a relatively stressful environment.

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 2.3-7

r limiting factors such as depth, turbidity, and fluctuations of water level.

Submerged hydrophytes are more likely to be influenced by increases in turbidity than emergent hydrophytes, not only because of reduced light penetration but also as a result of abrasive ef fects which can damage the leaves.

Table 2.3.2 presents dominant vegetation communities, relative fish and wildlife value, possible successional changes, and factors most evident in limiting the hydrophytes in each reservoir.

2.3.4 Summary A total-of 57 species of vascular hydrophytes were found growing in the study area. Only slight increases in diversity were noted over previous surveys, although the abundance of several species continued to in-c rease . Dominant species which increased in abundance included sof t-rush, cattail, and grasses. The subimpoundment continues to show cutro-phic conditions, with the pondweed population increasing in abundance.

Major factors limiting growth of the littoral vegetation along all banks appear to be wave action, deep water, turbidity, shading by canopy vege-tation, and steep banks which do not provide a suitable area for coloni-za tion. Fluctuating water levels appear to promote development of the littoral zone by providing increased spatial heterogenicity for plant colonization.

2.3-8

Table 2.3.1. Vascular hydrophytes found during shoreline surveys of Parr and Monticello Reservoirs, Neal Shoals Dam, and the subimpoundment,1982.

Page 1 o f 4 a

Form Stand Scientific Name Common Name (Habitat) location DDensitiesc Distributiond AlIsme subcordatum Water-plantain E P S R S S R Alnus serrulata Alder E S MA 0 NS S R Ammonia coccinea Marsh day flower E S S R M S R Anellema kolsak Anellema E,S P A 0 CC A 0 Arthraw n hispidus var. Grass E CC MA R cryptatherus Astor sp. Astor E P Ws C CC(St.C) MA C NS S R M S R S W 0 Bacopa mannelrl Water-hyssop E M S R Bldens frondosa Beggar ticks E M S O S S O P(St.B) S 0 CC S O Boltonia astemides Boltonia E P MA 0 CC(St.C) MA R Carex 1urida CarIc sedge E S(St.H) MA 0 Cephalanthus oce: dentalis Buttonbush E S S 0 CC(St.C) S O P S 0 NS S R Chasmantium latifolium Inland seaoats E S S R NS S R P S R Cicuta psculata Water hemlock E P S R CC S R Cyperus erythrorhizos Flat-top sedge E S(St.H) MA 0

' Cyperus Iria Flat-top sedge E P S R CC(St.C) MA 0 M(St.K) S R NS MA R Cyperus virens Flat-ton sedge E P S O Dlodia virginiana Butto nweed E, S P(St'.9) S 0 M(St.K) $ R 2.3-9

Table 2.3.1 (G ntinued: Page 2 of 4 form a Stand d Scientific Name 6mpon N.we (Habitat) location bDensitiesc Distribution Echinocloa colonum Barnyard-mil l et E S(St.H) m O P A C CC MA C Eeninocloa crusaall! Barnyard-millet E M S 0 S S C P A C CC MA 0 EclIpta alba EclIpta E M S R P S R Elenchaels obtusa Spike rush E,S P S R S MA 0 CC(St.C) MA 0 M MA 0 Eleocharts quandrangulata Spikerush E S MA 0 Erlanthus glaanteus Suge.rcane E M MA C pl umegrass S(St.H) MA C P S 0 CC(St.C) S 0 Fuorina squarrosa Umbrel l a-grass E S(St.H) S R CC S R Hibiscus nescheutos Hibiscus E S S O NS S R P S R CC S 0 Hydmchlos carollnlensis Grass FL CC MA R Hydrolea quadrivalvis Hydrolea E P S 0 Hypericum gentlanoides St. John's wort E NS S O Hypericum mutilum St. John's wort E M S R P S R Juncus acumlnctus Bog-rush E S S R P S 0 CC S O Juncus dichotomus Bog-rush E S(St.H) MA 0 Juncus effusus Sof t rush E M(St.K,1) MA 0 S(St.H) A C CC MA 0 P S 0 Juncus polycephalus Ebg-rush E S S R Leersia cryzoldes Cut grass E 3 MA 0 Lindernia dubla False pimpernet E P S R NS S R Ludwigle a:ternifolla Fal se-loosestr i fe E,S S S 0 S(St.H) S 0 Ludwigla glandulosa False loosestrife E CC(St.C) S O 2.3-10

Table 2.3.1 ((bntinued ) Page 3 of 4 Fo rm" Stand d C

Scientif!c Name Conson Name (Habitat) LocationD Densities Distribution Ludwigla palustris False-loosestri fe E,S M(St.K) S R S S R Mimulus ringens enkey-flower E M S R S S 0 P S 0 CC(St.C) MA 0 Paspalta notatum Paspalum E S(St.H) S O P S 0 Ditch stone crop E P S R Penthorum sodoldes Pluchea camphorata Marsh-fleabane E M(St.M) S R CC S O NS S R P(St.8) S 0 CC(St.C) MA 0 M(St.0) MA 0 Pblygonum hydrupIperoides Smartweed E S C NS R CC MA 0 P A C P(St.8) S C Polymnum lapathifolium Pale s,nartweed E NS S R P S R Pblygonum sagittatum Tearthurnb E P MA O CC A 0 Nntederla cordata Pickereiweed E S S O

~

P m O CC MA C Ntanogeton diversifollus Fb ndweed S,FL S(St.H) A C P MA R Ptllimnlum capillaceum %ck Bishop's CC(St.C) MA R weed Rhynchospora cernlculata Parned rush E CC(St.C) S O P S R Rotala ranoslor Tooth-cup E,S NS S li S MA 0 Sagittarla latifolla Arrowhead E CC S 0 Salix nigra Black willow E P A 0 CC M 0 NS A C M MA 0 S MA C Saururus cernuus Lizard's tall E P S R CC(St.C) S R Scirpus cyperinus Wolgrass bulrush E S A C CC MA C P MA R M(St.1,K) A C 2.3-11

l Table 2.3.1 (Continued) Page 4 of 4 a Stand Form d Scientific Name Con.an Name (Habitat) locationD DensitiesC Distribution j Scirpus valldus Sof t-stau bulrush E S m 0 P m O CC m 0 Taxodlum distichum Bald cypress E CC S 0 M(St.1) S R S S R Typha latifolla Cattall E M(St.M,K) A 0 S A C CC MA 0 P MA 0 a Symbols for form (or habitat) of plants are as follows:

E = Faergent S = Submergent FL = Floating leaved b Symbols for locations of populations are as follows:

M = m nticello Reservoir P = Parr Reservoir S = Subiminundment CC = Cannons Creek Area NS = Neal Shoals Reservoir St._ = IndivIdJal station mrrespondIng io nearest littoral benthlC macroinvertebrate sampling location.

c Symbols for stand densttles are as follows:

A = Abundant (a great number of Individuals / stand)

MA = %derately abundant S = Sparse (one or two individuals / stand) d Symbols for distribution are as follows:

C = Common 0 = Oc:aslonal R = Rare 2.3-12

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, 1982.

Dominant Fish and Expec ted Probable Major Location Vegetation Wildlife Value Succession a Limiting Factors Cannons Creek Area Diverse; Anellema, cat- Modera te to high No significant change Steep. banks ; turbid tails, boltonia, and in the marshy likely. water.

sedges. areas.

Subimpoundment Diverse; cattails, willc,ws, High Trend is toward eutro- Fertilizer accelerating sof t ruch; pondweed in phication. growth; shade, coves. .

Parr Reservoir Abundant willow stands, High No significant change Fluctuating water level, .

smartweed, grasses, sedges likely, shading, steep banks,.and also abundant. turbid water.

Y Moderate Continued development of Steep, clay banks, wave C Monticello Reservoir Cattails and sof t rush in coves. Bulrush also littoral zone in coves action, deep water.

abundant. where erosion is not significant.

Neal Shoals Primarily willows. Low to moderate. Little succession expected. Steep banks, deep water, in near future. heavy shading from canopy.

" 'Ihese trends are ex pcted if current management practices remain the same, i

d d I 4

L2.4 PHYTOPLANKTON 2.4.1 ' Introduction Phytopisnkton are microscopic, free-floating plants which make up an important: component of the aquatic ecosystem. They occupy the lowest trophic level in the ' food web within the aquatic environment and are consumed by many types of higher life forms, inclu d ing invertebrates, fish, and occasionally, vertebrates such as waterfowl. Thus, the i 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 numerous - abiotic factors which are also of importance. Knowledge of phytoplankton species composition is useful in interpreting water quality and predicting potential problems concerning nuisance aigal

, growths. Nuisance algae can cause water taste and odor problems, and bio-fouling in filters, screens, pumps, and other types of water handling equipment.- -

2.4.2 Findings and Discussion Parr Reservoir t-1982 Data. Stations in Parr Reservoir (Stations B, C, and D) were sampled during January, April, July, and October. The complex phyto-L plankton assemblage showed definitive quarterly (temporal) patterns.

t These patterns were exemplified by evaluating mean total densities, collectively, from Stations B, C, and 9 These density data are

provided in Table 2.4.1.

l- ,

Mean total densities in Parr Reservoir ranged from 1,604/ml in January  ;

. to 3,774/ml in July. Patterns of density fluctuation were signalled first at Station B, with densities at Stations C and D following the ,

2.4-1 4

- - - . . . . - - , ,,-,.m - m..--,.m,-, ,,_m w, .,--,,,yn m,,,-.,m. m.i.,, ,-- ,m._,,,m_ _.n-,-m_.m,, , ,,. ,,- - m-ww-

trend several months later. For example, phytoplankton concen'

• ions showed a three-fold increase at Station B between January ' 5 and April (4,101/ml), but density increases were not evide Stations C and D until the period between April and July.

time, densities did not rise as much at Stations C (double, ce

.than one and one-half times) as they had at Station B. In as t a. .

although phytoplankton numbers began to decrease between July and October at Station B, a decline ' ras not evident during that period at Stations C and D. No major blooms such as the one noted in Parr Reservoir during January 1981 occurred during 1982.

Except at Station C in July, diatoms (Baci11ariophyta) were Lae pre-dominant algal group at all of the Parr Reservoir stations for every sampling effort. This group of organisms comprised between 95 (Jan-uary) and 53 (July) percent of the average seasonal phytoplankton population in Parr Reservoir. In January and April, diatoms comprised the entire (100 percent) phytoplankton tiora sampled at Station C; diatoms were the least numerous at Station C in July, when they com-prised only 27 percent of the population there.

Green algae (Chlorophyta) were present in all samples from Station B ,,

but were not found at Stations C or D in January or at Station C in April. The highest numbers of green algae occurred in July at all of the Parr Reservoir stations. Green algae comprised between 42 (July) l and 2 (January) percent of the average Parr Reservoir phytoplankton community. This group of organisms showed the highest dominance at l Station C in July (63 percent of the community) and represented the l

smallest percentages of the community (when it occurred) at Station B l

in January, April, and October. It accounted for between 5 and 6 per-cent of the community collected at Station B during those months.

Blue-green algae (Cyanophyta) represented less than 10 percent of the phytoplankton community at all of the Parr Reservoir stations during every month except at Station D in October when this group comprised 2.4-2

l-h 25 percent of the total community collected. During the course of the quarterly sampling, euglenoids and chrysophytes were the only algal groups other than the diatoms, green, and blue green algae which were found in the Parr Reservoir samples. None of these groups made up more than 8 percent of the total algal densities during the four surveys at the Parr Reservoir stations.

Mean annual biomass (ash-free weight of organic matter) values were the highest at Station C (8.1 og/ liter) and lowest at Station B (6.8 mg/

liter during 1982. The highest biomass measurements occurred in April at Station C and in July at Stations I and D. The lowest biomass read-ings were reported in October from all stations.

Collections in October yielded the greatest average number of taxa (10.3). The number of taxa collected during the other three quarterly surveys ranged from an average 8.0 and 8.3 (April and July, respec-tively) to 7.3 (January). The average species diversity in Parr Reservoit (a measure of the distributioa of taxa among the number of individuals per taxon) was highest during October (2.73) and lowest during July (2.32).

During each sampling period, the predominant species were quite similar in Parr Reservoir. In January, Cyclotella was a codominant species at all of the Parr Reservoir stations, comprising from 33 percent of the phytoplankton community at Station D to 19 and 22 percent of the com-munities, respectively, at Stations B and C. The diatoms, Navicula and Synedra, were also important components of the phytoplankton community at Station B and C while Melosira was a codominant at Stations C and D in_ January.

During April, Pinnularia and Navicula were among the predominant species at all of the Parr Reservoir stations, with Cyclotella (Stations B and C) and Synedra (Stations B and D) remaining as 2.4-3

l codominant species. Achnanthes was also present in high numbers (16 percent of the population) at Station C.

Synedra and the green alga Chlamydomonas were codominant at all of the '

Parr Reservoir stations in July, representing a total of 78 percent (Station C) to 49 percent (Station D) of the phytoplankton sampled.

Navicula, representing 21 percent of the community sampled, continued to be a codominant at Station D during July, but this species comprised less than 5 percent of the phytoplankton community at Stations B and C.

Synedra was a very important component of the algal community at all of the stations in October, when it comprised from 34 percent of the community at Station D to 26 percent at Station B. Chlamydomonas continued to be present in high numbers at Stations C and D where it comprised 35 percent and 11 percent of the respective communities, but it occurred only as 5 percent of the total number of organisms found at Station B. Other cudominant genera were Melosira at Station B (29 percent of the population), Pinnularia at Station C (13 percent), and Lyngbya (23 percent) and Navicula (14 percent) at Station D.

Historical Trends. Since samples were only collected during three quarters in 1978, the data for that year have not been used for comparative purposes.

Mean annual phytoplankton densities at the Parr Reservoir stations have been relatively stable since 1979, except during 1981 (Table 2.4.2). In 1981, a large phytoplankton bloom at all of the Parr Reservoir stations in January caused the average densities to greatly exceed previous levels. Mean annual densities have ranged between 1,837/ml and 3,333/mi at Station B, 2,619/ml and 4,426/ml at Station C, and 705/mi and 2,617/ml at Station D, excluding 1981 densities. Except in 1982, when ths average annual phytoplankton densities were essentially the 2.4-4

same as at Stations C and D, Station D has typically exhibited lower densities than those found at the other two Parr Reservoir stations.

Since 1979, the mean annual phytoplankton biomass at the Parr Reservoir 4

stations tus shown a general decline every year except 1981 when extremely high densities occurred.

The average. annual number of taxa has decreased at all of the Parr

. Reservoir. sta tions since 1979.- It has decreased from 18.8 to 9.0 at t Station B,19.0 to 8.0 at Station C, and 21.5 to 8.5 at Station D during that time. . However, mean annual diversity has remained relatively constant at all of the stations since 1979; mean annual

~

diversity did register a noticeable increase at Stations B and C in

. 1982 and in 1981 at Station D.

Neal Shoals Das 1

1982 Data. The phytoplankton density increased. to a high of 11,476 cells /ml in April from a February low of 3,060 cells /ml, and then ,

declined ~ to 9,521 cells /ml in October. No samples were collected from this station during July because the reservoir was drained by SCE&G in order to repair the dam and power house. As at the Parr Reservoir stations, diatoms wereL the most abundant algal group collected during

[

every season; these organisms made up approximately 83, 67, and 76 percent of the total density, during February, April, and October, respec tively. The green algae were codominant during each sampling

- period, ranging in density from 28 percent of the community in April to j 11 percent in February.

The nean annual biomass was 13.9 mg/ liter at Station P, the highest mean value ' recorded for any of the statf ons sampled in 1982. A high of

! 19.1 mg/ liter was measured in January while. the low of 10.2 mg/ liter was found in October.

t 2.4-5 m- -~,-e,-,,.wm., r - .. - , , . . , . , ..mm%.r,, ,,.,.,.y, ,..,..,,,,-.p,.,.-__...y.,-,._,m., ,.._c., .,m -- , . - . -,

The - taxa number was highest in October (15) and lowest during February (6); the April taxa number (14) was similar to that found in October.

The species diversity indices at Station P were similar during April (3.19) and October (2.85) but somewhat lower (2.13) in February. The mean diversity for the three sampling periods was 2.72.

During February, Cyclotella accounted for 50 percent of the phytopJ ank-ton community at Station P while Navicula accounted for 14 percenc and Melosira and Chlamydomonas each comprised 11 percent of the phytoplank-ton collected. In April, Synedra comprised 25 percent of the community and Navicula (18 percent); Mougeotia (11 percent), Chlamydomonas (10 percent), and Cyclotella (10 percent) were also important. Synedra represented 43 percent of the community in October; two other diatoms, Nitzschia and Cyclotella were codominant, accounting for 12 percent and 11 percent, respectively of the total community.

Historical Trends. Since samples were only collected during three quarters in 1978, the data for that year have not been used for comparative purposes.

Mean annual phytoplankton densities at Station P have been rather erratic over the 1979-1982 study period, alternating between increases and decreases (Table 2.4.2). Tite density decreased by more than a

! factor of two between 1979 and 1980. Between 1980 and 1981, the mean

' annual density increased more than three-fold, but decreased again to half the 1981 level in 1982.

l The mean annual phytoplankton biomass at Station P was at its highest level of 27.1 mg/ liter in 1979. It declined to less than half that value in 1980 and has increased annually since then to a level of 13.9 mg/ liter in 1982.

2.4-6

,-+---,,--,,--,-m- -

,, , - - - . ~ -

The mean annual number of taxa increased slightly between 1979 and 1980, rising from 19.3 to 21.0. Since 1980, the number of taxa has steadily decres,ed to _11.7 in 1982. The mean annual species diversity has been relatively stable since 1979, ranging from 2.05 in that year

, to 2.87 in 1981.

Subimpoundment 1982 Data. Phytoplankton densities in the subimpoundment were highest in-July (206,325 cells /ml) and lowest in April (3,864 cells /ml).

During January and April, diatoms were the most abundant algal group at Station H, representing 90 and 63 percent of the community, respective-ly. During July, the blue-green algae were the most abundant group (92 percent) due to an Anabaena bloom. In October, the green algae ,

euglenoids, and diatoms were almost equal in abundance, with each of these groups accounting for between 25 and 28 percent of the total community.- Blue-green algae (representing 15 percent of the com-munity) were also important in October. Chlorophytes were an important component of the phytoplankton community in January and April also comprising 10 and 28 percent of the total community at Station H.

Biomass measurements at Station H were similar in January, April, and

( July (6.7 to 6.8 mg/ liter), but had recreased in October to 5.6 mg/

liter. The mean annual biomass at Station H was 6.5 mg/ liter.

l The total number of taxa collected from Station H increased from 11 in l

l January to 18 in October. Although a massive Anabaena bloom occurred in July, a total of 14 other taxa were collected then. Species diver-sity averaged 2.51 for the year and ranged between 0.72 (July) and 3.50 (October). In January, the diatoms Melosira (42 percent), Cyclotella l and Navf cula (13 percent each), and Synedra (12 percent) were the most abundant species. Melosira was again one of the dominant genera in April with 22 percent of the community; however, Chlamydomonas was l

2.4-7

~, _ - _ _ ~ _ , _ _ _ _ _ _ _ _ . _ . _ _ _ _ _ _ _ _ . _

equally abundant, and the diatom Achnanthes (17 percent) was also an extremely important component of the phytoplankton community at Sta-tion H. During the summer, the blue-green Anabaena bloomed to form 91 percent of the algal community. No other genus collected from this station in July comprised more than 2 percent of the phytoplankton com-munity. By October, no Anabaena were collected. The euglenoid, Cryptomonas (26 percent), was the most abundant organism collected, followed by Cyclotella (11 percent) and the cyanophyte, Spirulina (10 percent).

Historical Trends. Since samples were only collected during three quarters in 1978, the data for that year have not been used for comparative purposes.

The mean annaal phytoplankton densities in the subimpoundment have increased every year since 1979 (Table 2.4.2). Mean annual densities almost doubled between 197 9 and 1980, increased slightly in 1981, and then showed a dramatic increase in 1982 to almost four times the 1981 levels. The high density recorded for 1982 resulted primarily from a bloom of Anabaena which occurred in July.

The mean annual biomass measurements made at Station H since 1979 showed a high of 10.0 mg/ liter in 1980. Since that time, the biomass has decreased to 6.5 mg/ liter in 1982.

The mean number of taxa recorded in 1979 and 1980 was similar, but a i

noticeable decrease occurred in 1981. The mean annual number of taxa appeared to have stabilized, at least temporarily, in 1982 when the number was almost identical to that of the previous year. Mean annual l

species diversity remained staole during 1979 and 1980 and then increased noticeably in 1981 before apparently stabilizing again in 1982.

2.4-8

~ _ . - . -. -_ .

4 4

i

~Monticello Reservoir L .

-1982 Data. ' Phytoplankton density _ trends varied somewhat among stations on a month to month basis. These variations were especially noticeable

^

when-blooms occurred at an individual station in Monticello Reservoir-i but not ' at . the others during a particular month. However, mean den-

~

~

sities for the combined Monticello Reservoir stations showed definite seasonal trends, especially when blooms at an isolated station were not considered in the averages. In the colder months, the average phyto-plankton density at all of the stations was relatively-low, ranging from 2,138/ml in December (excluding bloom condition densities of

[r~

52,084/ml at Station K, only) to 4,572/ml in January (again, excluding

. blocm. densities at . Station I in' Februcry). Mean spring phytoplankton densities ~ for all of the Monticello Reservoir stations were similar to

. those recorded in. the winter, ranging from 3,978/ml in March to

- 5,814/al' in May. The average densities showed a dramatic rise in the summer when they ranged from 86,365/ml (including blooms at Stations I and 0 in June) to 9,479/ml in August (excluding a bloom occurring only at Station I) . - ht the fall, mean densities 'for the reservoir stations declined. to 6,242/ml and 3,210/ml in September and October, respective-ly. - During 7 of the 12 months sampled, Station I had the highest den-sities recorded with najor blooms occurring at this station during three sampling periods. Station L recorded lower densities more fre-quently (during 6 of the 12 months sampled) than any other Monticello Reservoir station.

> Mean densities for phytoplankton at all of the Monticello Reservoir stations indicated that diatoms were the most numerous group during every month, comprising 93 (January) to 41 (July) percent of the community. As expected, diatoms generally formed a greater percentage of the mean phytoplankton community in the reservoir during the cooler L months when iower water temperatures do not favor the growth of chloro-I phytes or cyanophytes. As temperatures warmed from March through May,

! the green algae became more abondanc, rising in number f rom 21 percent g

2.4-9

to 38 percent of the mean density. During the period from June through August, the water was warm enough to support large populations of blue-green algae; cyanophytes comprised from 28 (July) to 33 (August) percent of the mean community size during the summer months. However, green algae and diatoms were also present in high numbers during these months. The green and blue-green algae centinued to be important componenta of the mean Monticello Reservoir phytoplankton community throughout the fall and early winter and were more important during the summer. By December, the blue-green algae were found only at Sta-tion L, where low numbers were collected. The euglenoids were the only other major algal group collected during the 1982 survey in high con-centrations; this group appeared primarily at Stations 1 through M during February when it comprised 27 percent of the mean community in the Monticello Reservoir.

The mean annual biomass measurements ranged from 5.6 mg/ liter (Sta-tion N)~ to 6.7 mg/ liter (Station K). The lowest mean biomass readings were recorded in May, October, and November. The highest mean biomass readings were recorded in January and April.

Mean species diversity at the Monticello Reservoir was lowest (1.60) in January but increased during the next several months until it reached 2.10 in May. The diversity then decreased to its second lowest value (1.68) in June before rising to its highest level (2.68) in August.

During the next three months, the diversity ranged between 2.24 (September) and 2.51 (October) before declining to 1.97 in December.

The highest mean number of taxa (10.7 aus 13.9) in Monticello Reservoir occurred in June and July, respectively. The mean number of taxa rose from 6.7 in January to 8.2 in March. It then declined somewhat until increasing to the year's high of 13.9 in July. The mean number of taxa declined continually from 9.5 in August to 6.8 in December 1982.

2.4-10

. s ,

r i

Cyclotella was the most abundant organism at all stations during Jan-uary and February, except at Station K in January when Melosira was slightly more numerous. Melosira was as abundant as Cyclotella at Station M in January, and the euglenoids were as abundant as Cyclotella at Station K in February. Although Cyclotella was still an important component of the phytoplankton community in March at all stations except M, Chlamydomonas also became ebundant at all of the statians sampled. Melosira was only collected at Stations K and N, where it comprised 6 and 10 percent, respectively, of the phytoplankton collec- ,

tions. By April, Cyclotella and Chlamydomonas remained important at all stations, but Melosira showed a strong increase in numbers. In May, the relative numbers of Cyclotella and Melosira had declined in the reservoir as a whole, although the latter remained an Laportant component of the algal community at Stations I cnd L. Chlamydomonas was still codominant at all of the stations along with Asterionella, which was previously present only in low densities. Other species which were numerous during May were Anabaena (Station I) and Fragilaria (Stations K and L). A Fragilaria bloom occurred at all stations during June, along with an Anabaena bloom at Station I. Anabaena was numerous at all stations but N during June; Chlamydomonas remained abundant at 4

all stations, and Melosira was again an important component of the phytoplankton community at Stations L and M. By July, Fragilaria had almost disappeared from the community, being replaced by large numbers of Synedra at all stations. Chlamydomonas was an important codominant at all but Stations I and J, where it was found only in relatively low l

numbers. The blue-green alga Anabaena comprised from 7 percent (Sta-tions K and M) to 67 percent (Staticn I) of the community, except at

' Stations L and N where it was-not found. Lyngbya was abundant at all but Station I in July. In August, dominance was again spread among

j. different genera in Monticello Reservoir. Generally, the most numerous genera were Synedra, Cymbella, and Spirulina. However Chlamydomonas I was the most abundant genus at Station M, and Anabaena was the dominant organism at Station N. In September, Chlamydomoras was one of the most numerous phytoplankters at all stations and Nitzschia was very i

2.4-11 i

l

- - = .

abundant at all but Station M. Glosira was an important component of the community at Stations I and K, Synedra at Stations M and N, and Cyclotella at Stations K and O. Synedra and Melosira were among the most important algal genera at all of the stations in October with

! various different genera being codominants at each sampling location.

Codominants were even more varied among the stations in November than they had been during the previous month. Chlamydomonas was the most abundant organism at Stations I and 0 and was, with Cyclotella, one of the two most abundant groups at Station L. Cyclotella was also the densest phytoplankter at Station K. Lyngbya predominated at Stations M and N. By December, the species composition among stations was sim-ilar, except at Station K where a Fragilaria bloom occurred. At all other stations, Cyclotella and Melosira were among the most abundant phytoplankton groups collected. Fragilaria was also codominant at Scation N, Synedra and Chlamydomonas at Stations I, L, and 0, Navicula at Station 0, and Asterionella at Station I.

Although the monitoring results occasionally differed noticeably among the Monticello Reservoir stations for the monthly sampling efforts, i

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, the southern Monticello Res-ervoir stations (L, M, and N) appeared to have lower densities than the other stations, with the exception of Station J. Mean annual densities j

at Stations L through N ranged from 6114/ml (Station L) to 8874/ml (Station M) while the mean density at Station J for 1982 was 8009/ml.

Mean annual phytoplankton densities at the other stations ranged from a t

high of 26,741/ml at Station I, which experienced a number of major blooms and had the highest densities of any station during 7 of the 12 months sampled, to 13,958/ml at Station 0. Similar density patterns were noted in 1981. The maan annual diversity indices showed a pattern similar to that of the densities; the species diversity values were higher at Stations J through M, ranging f rom 2.34 (Station M) to 2.28 2.4-12

> (Stations J and K), than at Stations I (2.03), N (2.11), and 0 (1.97).

Station K recorded the highest mean annual number of taxa and Station 0 the lowest.

Historical Trends. - Since samples were only collected during three quarters in 1978, the data for that year have not been used for

. comparative purposes.

Mean ' annual densities at most of the Monticello Reservoir stations typically increased from 1979 through 1981 and then showed a decline in

'1982. Except at Station I, the greatest mean annual densities were recorded in 1981 when large blooms were noted several times during the year; Station I experienced its greatest mean annual density in 1982, when particularly large blooms occurred during several sampling periods.

Since 1979, the mean annual phytoplankton biomass increased at most stations to its highest level in 1981 and then declined in 1982.

The mean annual number of taxa showed an increase between 1979 and 1980 and then decreased every year thereaf ter. The only exceptions to this pattern were at Station K, where the mean number of taxa were similar in 1979 and 1980, and Station 0, where the mean number of taxa actually l

declined somewhat during the 1979-1980 period. However, at both Stations E and 0, the mean number of taxa decreased every year from l

1980 to 1982. Mean annual species diversity showed either a decrease

-in value or remained almost the same at most Monticello Reservoir stations between 1979 and 1980 and then increased through 1982.

I 2.4.3 Summary

! i i

During previous studies (Dames & Moore, 1978,1979,1979a,1980) other than in 1981, parameters measured for the phytoplankton communities in i Parr Reservoir were observed to be similar to those found at the Neal i Shoals Das sampling site; additionally, the subimpoundment was found to i

2.4-13

exhibit phytoplankton community characteristics similar to those recorded for Monticello Reservoir. With the exception of species composition during 1981, the phytoplankton sampling results from Parr Reservoir showed little . similarity to those from the Neal Shoals Dam station. The same-dissimilarities, again with the exception of generic composition, were evident between the Monticello Reservoir and subia-poundment stations during 1981 and the first two seasonal surveys of 1982. During the July and October 1982 surveys, species composition became more and more dissimilar in Monticello Reservoir and the subim-poundment. During the quarterly surveys in Parr Reservoir, biomass showed little correlation to phytoplankton density. Likewise, no con-sistent biomass-density relationship occurred in Monticello Reservoir.

during 1982. In the past, biomass generally fluctuated inversely to density in Parr Reservoir and was at least somewhat correlatable to density in Monticello Reservoir.

The monthly fertilization program which was carried out in the subim-poundment from April through Geptember 1982 had a definite effect on the phytoplankton densities at Station H. Except in April, when sam-ples were collected just before initiation of the fertilization pro-

• ' _ gram, phytoplankton densities at Station H were always higher than the average densities in Monticello Reservoir. In April densities in the subispoundment were below or similar to these in Monticello Reservoir.

- As in Monticello Reservoir, the highest densities occurred in the summertime at Station H. However, the July phytoplankton density in the subispoundment was much higher, 206,325/ml, than the highest mean average density encountered in Monticello Reservoir 56,698/ml (in June).

The generic population shift, which has been noted in previous reports and which is apparently caused by fertilization within the subimpound-ment, was noted only during July and October 1982. During July, an Anabaena bloom caused 92 percent of the algal population at Station H to be blue-green algae; this compares to 24 percent at the combined Monticello Recervoir stations. In OcMber, green algae and euglenoids were much more abundant at Station H than in Monticello Reservoir.

2.4-14 I

i Tabl e 2.4.1 Density, biomass, number of taxa, and tamnomic diversity of phytoplankton collected during 1982 at Parr Reservoir, Neal -

Shoals Dam, Ibnticello Reservoir, and the subispoundment.

Page 1 of 7 Area Parr Reserwir Neal Shoals Dam -

D P Station B C Density JLb o (cells /ml) J A JL 0 J A JL 0 J A JL 0 J A Chlorophyta 84 256 1494 175 - - 2224 1275 - 169 1001 598 340 3230 - 1530 85 262 - - - 85 - - - - 170 170 - 255 Eugl enophy ta - -

Chryrnphyta 84 - -- - - -

85 85 - - - - -

255 -

85 Bacil l orlophyta 1176 3760 2905 2711 1955 1615 939 1700 1428 1772 2169 2223 2550 7736 - 7226 166 175 - 256 255 84 -- 83 940 -

85 - 425 1

Cyarophyta - - -

To tal 1344 4101 4565 3323 1955 1615 3504 3400 1512 1941 3253 3761 3060 11476 - 9521 i

Blomass (mg/l) 7.4 6.1 8.2 5.5 8.1 10.0 7.9 6.2 7.7 7.5 8.9 5.8 19.1 12.4 -- 10.2

, b)

= Species Diversity Indexa 2.35 2.61 2.40 2.91 2.76 2.42 1.76 2.65 2.34 2.58 2.79 2.62 2.13 3.19 -

2.85 f

m

• tb. of Taxa 7 10 8 11 8 6 7 11 7 8 10 9 6 14 - 15

• Shannon-Wiener species diversity Index (Plelsu,1%6).

tb samples mllected due 10 dewatering at this station.

1 i

1 I

i l

1

i Table 2.4.1 ((bnirinued) Page 2 of 7 Area Subimpoundment enticello Reservoir Station H I Taxa J A JL 0 J F M A M JU JL A S 0 N D Chlorophyta 683 1092 6750 5068 427 935 1512 1344 1190 14960 2508 4911 8356 170 913 238 4

Euglenophyta - - --

4732 - 7907 - - - -- - --

522 255 -- -

336 225 1099 - - - - - 170 - 85 - 79 Chryso phyta - - -

4 Bacil l arlophyta 76 % 2436 8775 4393 5730 10542 6805 6888 2550 98621 3374 50840 4091 3655 1660 1905 Cyano phyta 171 - 193575 2620 - - - -- 1020 46252 13412 14961 609 850 - --

i 8550 3864 206325 17912 6157 19384 8317 8232 4760 159833 19924 70902 13578 5015 2573 2222 To tal 9.1 5.6 3.6 5.3 9.1 7.7 6.7 4.5 3.9 2.8

, ." Biomass (mg/l) 6.7 6.8 6.8 5.6 8.9 6.0

! s~

i 1 Species 1.92 1.55 1.94 2.62 1.77 1.71 2.36 2.09 2.85 2.00 2.49

@ Diversity Index 2.61 3.22 0.72 3.50 1.00 14 15 18 6 12 9 6 8 11 Il 12 13 10 5 7 tb. of Taxa 11 1

Shannon-Wiencr species diversi1y Index (P lelo u, 1966) .

i i

l 4

1 l

l 4

Table 2.4.1 (Continued) Page 3 of 7 Area k nticello Reservoir Station J K Taxa J A JL 0 J F M A M JU JL A S O N D Chloro phyta 169 2381 3521 332 256 516 2197 1105 3507 5324 4813 3742 1282 765 595 84 Eugl enophyta - - - 83 -

1463 -

595 - -- - - -

85 - --

Chryso phyta -- - 26; -- -- -

169 - - - - -

Bacil l arlophyta 5492 2720 9420 2573 6670 2495 3547 2295 4019 39043 3499 4265 2906 2975 2005 51328 Cyano phyta - - 4667 498 - - - --

512 10564 3239 6268 171 595 935 672 Total 5661 510 17872 3403 6926 4474 5913 3995 8038 54931 11551 14275 4274 4420 4335 52084 Blomass (mg/l) 5.4 7.6 6.0 4.2 8.5 5.9 6.5 9.1 5.0 5.6 6.5 9.7 9.4 3.8 4.5 5.8

• Species 1 Diversity Index a 1.62 1.93 3.05 2.51 1.81 2.26 2.36 2.72 2.28 1.69 2.68 2.93 2.42 2.77 2.69 0.78 u

No. of Taxa 6 7 15 9 7 8 11 8 9 11 13 11 8 10 9 11

• Shannon-Wiener species diversity I. edex (Plelou,1966).

(Continued)

Page 4 of 7 l Table 2.4.1 l

l l

Area kbnticello Reservoir t-Stat ion l M A M JU JL A S O N D Taxa J F l

l 85 756 2112 2296 22632 792 1319 85 756 504 l

Ch lorophyta 510 -

l 591 85 - -- -- - - 165 - --

Euglenophyta -

l -- -- -- -- -- -

l Chrysophyta -- -- --

595 2688 7013 18536 16187 792 1565 1025 1260 1848 Bacil l ariophyta 3826 1774

-- -- -- t'4676 2970 704 -

85 84 420 Cyano phyta - --

4336 2365 765 3444 9125 25508 41779 2288 3049 1195 2I00 2772 To tal 6.0 5.0 8.5 3.1 5. 5 8.5 6.4 8.1 4.0 4.2 6.7 Biomass (mg/l) 9.4

. Species 2.35 2.19 2.62 a 2.63 1.91 2.70 2.91 2.70 y Diversity index 1.38 1.99 2.64 1.82 6 8 5 tb. of Taxa 7 5 7 5 10 10 13 9 10 6

" Shannon-Wiener species diversity index (Plelou,1966) .

i A

Table 2.4.1 (Cont inued ) Page 5 of 7 Area  % nticello Reservoir Station M Taxa J F M A M JU JL A S O N D Chlorophyta 255 174 337 94 0 1445 2296 17754 4191 583 774 935 83 Euglenophyta - 261 --

.- -- - 174 -- - 258 - --

Chrysophyta -- 174 - -- -- - -- --

1 Bacillarlophyta 3400 2437 927 4189 2295 15130 20348 3421 2338 3527 1785 1079 4 Cyanophyta - 87 - -- -

2295 9448 1367 250 258 1360 -

a Total 3655 3046 1264 5129 3740 19721 47724 8979 3171 4817 4080 1162 Blomass (mg/l) 8.6 7.5 5.8 8.2 5.1 6.1 7.2 6.6 6.0 3.9 3.5 4.2

' .N q ,L Species ,

, u) Diversity Index, 2.34 2.37 2.68 2.23 2.23 1.89 2.68 2.77 1.71 2.65 2.62 1.87 i

No. of Taxa 9 9 8 7 7 13 16 9 7 11 8 5

• Shannon-Wiener species diversity index (Plelou, 1966).

'?

I i

L i

)

l Tablo 2.4.1 ((bntinued ) Page 6 of 7 Area %nticello Reservoir

, Station N .

I M Ju JL A S O N D M J F M A Chlorophyta 341 168 765 1092- 1360 2211 5112 850 7097 588 504 86 i Eug t enophyta -

84 - 84 - - - - -

Chrysophyta - 84 85 - - -- -- 255 - - -- --

Bu:ll i ar lophyta 3334 2436 3230 2688 2550 10542 6072 850 4926 1176 1512 2322 l

4 Cyanophyta - 84 - -- -- 680 3598 5016 417 336 1092 --

- Total 3675 2856 4080 3864 3910 13178 14782 6971 12440 2100 3108 2408 j ." Blomass (mg/l) 7.8 3.6 8.7 10.3 3.0 5.2 6.4 6.1 4.9 4.0 3.7 3.7

+

1 4

o Species Diversity Index, 1.44 1.69 2.34 2.31 1.99 1.52 2.84 2.43 2.36 2,.39 2.67 1.75 4

4 No. of Taxa 7 7 9 7 5 8 16 8 13 6 9 5 i

" Shannon-Wlaner species diversity index (Plelou, 1966).

l 4

4

,A

t i

Table 2.4.1 (Cbntinued) Page 7 of 7 i

1

! Area Monticello Reservoir I Station O Taxa J F M A M JU JL A S O N D l

i Chloro phyta 168 -

430 1615 3320 6760 16423 4704 256 84 1245 425 f Euglenophyta - - -

340 - - -- - -- - - --

j Chrysophyta -- 85 - -- -- -- -- -- -- -- - --

Bacil l ar lophyta 1344 5471 3097 4250 1992 52060 25483 7183 597 1182 2075 1700 I Cyanophyta 84 - - - - 8198 13514 2993 85 253 83 -

l Total 1596 5556 3527 6205 5312 67018 55420 14880 938 1519 3403 2125 Blomass (mg/l) 7.2 6.4 6.5 6.3 4.3 5.8 7.0 6.2 5.8 3.2 4.8 4.4 i .

c- Species 4 Diversity index" 1.63 1.56 1.33 2.30 1.44 1.29 2.66 2.66 2.16 2.06 2.38 2.28 No . o f Taxa 5 7 5 7 6 11 13 8 5 5 8 5

]

I l

" Shannon-Wiener species diversity index (Plelou, 1966).

I 4

(

)

i i

1

Table 2.4.2 Summary of mean annual values for phytoplankton obtained during monitoring programs from 4978 through 1982*.

Neal Sub-impoundment knticello Reservoir Area Parr Reservo!r- Shoal s O

H I J K L M N Station B C D P .

1305 1347 1855 1529 1809 2351 903 Density 1978 7637 533 155 1305 2802 8099 7830 8299 5888 4855 17826 5856 5819 (cells / mil 1979 2972 4426 1801 10177 14436 10266 28088 11367 12325 10216 10276 12165 1980 1837 3418 705 4755 20965 45117 20254 15944 10811 18887 22199 1981 37472 36101 10729 16039 15568 59163 26689 8009 14601 8227 8874 3484 13958 1982 3333 2619 2617 8019 12.5 25.0 4.1 72.3 2.4 4.9 3.5 17.0 6.5 Blomass 1978 17.7 17.8 10.0 6.5 5.5 12.I 27.1 6.7 7.6 6.2 7.1 5.9 6.7 (mg/l) 1979 9.1 15.5 8.5 8.9 7.3 7.5 7.3 9.6 11.1 11.7 10.0 8.3 5.3 8.3 1980 9.9 11.4 10.3 10.1 8.5 11.1 11.5 12.3 8.2 9.6 8.4 9.5 1981 6.7 6.3 6.1 5.6 5.7 1982 6.8 8.1 7.5 13.9 6.5 6.1 5.8 l

9.3 18.0 12.7 13.9 12.0 15.7 14.0 17.4 Number 1978 11.7 17.7 13.0 10.3 17.0 19.3 18.5 15.8 15.5 16.5 15.5 14.6 15.3 of Taxa 1979 18.8 19.0 21.5 16.6 15.9 16.3 16.3 16.3 21.0 20.3 17.8 16.5 16.6 17.0

.N 1980 15.5 10.1 9.5 10.5 10.8 10.3 11.3 9.5 12.8 14.3 12.0 10.5 12.3

- 1981 9.7 7.3 9.1 8.3 7.1 8.0 8.5 11.7 14.5 9.2 9.3 d

N 1982 9.0 1.43 1.06 1.97 f.33 I.66 1.39 I.43 1.69 f.77 Mean Species 1978 1.53 1.96 5.83 1.63 1.71 1.74 l

2.09 2.05 1.78 1.72 2.66 1.66 1.66 Diversity 1979 1.69 1.98 1.71 1.59 1.53 I 1.97 2.63 1.79 1.63 1.25 1.38 1.64 1980 1.57 2.06 1.85 2.03 1.81 1.98 1.69 2.47 2.87 2.66 2.35 1.73 2.11 1981 1.67 2.13 2.34 2.14 1.98 2.57 2.40 2.58 2.72 2.51 2.03 2.28 2.28 1982

' 1979 data represent the resul ts of three seasonal sampling ef forts. Data from four seasonal ef forts are included for the remainder of the years.

i l

1

2.5 ZOOPLANKTOM 2.5.1 Introduction Zooplankton form the animal constituent of the plankton community.

These organisms are primary consumers which feed directly on the phytoplankton, bacteria, and other zooplankton and form a portion of the food web base for higher organisms.

Replicate samples of zooplankton were collected in January / February, April, July, and October 1982 at the aquatic biology stations indicated i

in Figure 2.1.1. Organisms were identified to the lowest practicable

! taxon and enumerated for each replicate. The findings were averaged for each station and collection period and summarized in Table 2.5.1.

In presenting these findings, quantitative comparisons were made between stations for number of taxa, densities, distribution of the taxa within the four major sampling areas, and species diversity. Taxa l comprising 10 percent or more of the collection were considered codominants in the community. The species enumerated from the samples were referenced to two crustacean orders, Cladocera and Copepoda, and the phylum Rotatoria (rotifers). Unidentified eggs and other immature stages of zooplankton, excluding copepod, naupliar, and copepodite forms, were omitted from these analyses.

2.5.2 Findings and Discussion Parr Reservoir 1982 Data. The biological survey conducted in Parr Reservoir included the collection of zooplankton at three stations (see Figure 2.1.1) during the four quarterly sampling periods. The highest density (organisms per liter) was obtained in October with a mean of 81.67, and the two lowest densities occurred in January and April with means ,

of 12.31, and 13.60, respectively. July densities had a mean of 46.03.

2.5-1

During 1982, Station C had higher densities than Stations B and D,'due perhaps to the more lentic conditions at Station C.

i The rotifers comprised more than half of each quarterly collection at ,

Parr. Reservoir (59, 56, 58, and 74 percent, respectively). The cope-pods, which comprised between 35 percent of the zooplankton community

in January and 21 percent in April, were the next most commonly occur-

~ ring group of organisms. The Lamature stages or nauplii were found in l

every collection and accounted for 26 percent of the copepod community I

in January,'13 percent in April 23 percent in July, and 15 percent in f October. Cladocera, although represented by several genera, only comprised about 7, 23, 11, and 3 percent of the respective seasonal I collections.

Community composition was generally similar for the three stations f during the four sampling periods. Nauplii and Keratella were codomi-1 I

nants at every station during the mont* sampled; Polyarthra was codominant in all stations during July and October but only at Station C for January and April. Other genera that were also codominants but.

4 l on a less frequent basis were Synchaeta, Kellicottia bostoniensis, Bosmina, Lecane, and an unidentified rocifer. Lecane only appeared at two stations one time; once as a codominant at Station C in April, and in very low numbers at Station D in July. The rotifers Keratella, I

Synchaeta, Polyarthra, and the copepod nauplii were the most numerous zooplankters collected at all sampling locations during 1980 and 1981 l

(Dames & Moore, 1981).

i I

Several other genera, although less abundant, occurred at all three stations. The mean number of taxa collected was 18 in January, 19 in April, 21 in July, and 17 in October. The range was from 15 at Sta-tion C in January to 24 at Stations B and D in April and July. The mean number of taxa was greater during each season this year than in ,

I 1981.

j 2.5-2

~-n- - - - -v-,--wemn,,-.,,---o,---w ee,,w-mm-,, en,.,n,v,.,,,w.- ,.nm,w--w-,,,,, ,,-,o-n,.w~enya,ww.,w w-w y p,-,c, ,-,,m-e-.y -,my,~,, -

-m-e

Similar to the mean number of taxa, the lowest mean Shannon-Wiener diversity index for Parr Reservoir occurred in October (2.65) and the highest mean diversity occurred in July (3.16). January had the lowest mean number of taxa at 18, yet a slightly higher mean diversity at 3.07 (19.3 and 3.03 in April, respectively). The highest diversity value was in Parr Reservoir at Station D during January (3.16), and the lowest was at Station C in October (2.55).

Zooplankton biomass was determined for all sampling periods, with values averaging 0.060 mg/ liter for January, 0.062 mg/ liter for April, 0.061 mg/ liter for July, and 0.060 mg/ liter for October samples. The greatest biomass was measured at Station C both in January (0.088 mg/ liter) and in October (0.087 mg/ liter). The mean value for January was twice as much as the 1981 mean. The April, July, and October means were 12 to 15 fold higher than the 1981 biomass means for the same sampling periods.

Historical Trends. Historical data from 1978 to 1982 were reviewed and i analyzed for possible trends in density, taxa count, species diversity, and biomass. Mean annual densities at the Parr Reservoir stations fluctuated during the period 1978 through 1982 (Table 2.5.2). The 1978 values for all water bodies were based on three sampling periods -

June, July, and October. The remaining years values were calculated from quarterly samples - January, April, July, and October. Mean annual densities ranged between 33.91/ liter and 101.18/ liter at Station B, 57.58/ liter and 231.32/ liter at Station C and 23.73/ liter and 103.25/ liter at Station D. At all of the sampling locations the highest densities occurred during 1978 and then showed a general decline through 1982.

l The mean annual phytoplankton biomass at the Parr Reservoir stations showed some variability when compared to the density values. In 1978 i

when phytoplankton densities were high the biomass values were gen-erally low with the exception of Station C where a value of 2.5-3

0.341 mg/ liter was recorded. During 1982 when the densities werc low

, the biomass values were consistently high.

The average annual number of taxa was generally consistent throughout each year at all of the stations. . The mean annual diversity also remained relatively constant at all of the stations during the study period.

l I-Neal Shoals ,

1982 Data. Zooplankton samples were collected from one station (Figure 2.1.1) in the Neal Shoals Dam area during the January / February, April, and October quarterly sampling programs. The reservoir above the dam was dewatered during July and August for dam repairs thas preventing a I

July sampling. Although 90 percent of the total zooplankters collected at Station P in 1982 were contained in the October samples, this value is skewed since a July sample was not taken; the largest densities in the 1981 survey of Neal Shoals occurred in July.

The compositions of the January / February and April samples were quite similar. As in Parr Reservoir, the rotifers comprised over 50 percent of both collections (50 and 60 percent, respectively). The abundance percentages for the cladocerans and copepods were 17 and 33 percent in l January and 12 and 29 percent in April, respectively. In October, the copepods were the dominant group of zooplankters, increasing to 75 per-cent of the community. Rotifers represented 24 percent, and cladocera appeared as less than 1 percent.

Community composition for the three sampling periods was quite diverse.

Nauplii were one of the two most abundant codominants during each l

sampling effort comprising 29, 20, and 71 percent of the total zoo-plankters collected in January / February, April, and October, respec-tively. In January, the other codominants Kellicottia bostoniensis, ,

i Keratella, and Bosmina, were quite similar in density, with Filinia the 4

v 2.5-4

~ _ ._ _ _ _ . _ ._ - _ _ _ , _ _ . __. ,_ . _. . _ _._ . _ ._ _ _ _ _ _ _ _ . - _ , . . _ . _ _ . _

i only other genus nearing 10 percent in abundance. Synchaeta, which appeared only in small numbers in October and not at all in January, was the most abundant zooplankter collected in April. Polyarthra, also a codominant in April, did not appear in high numbers in January or at all in October. For October, 22 percent of the zooplankton populations were Conochilus unicornis, 5 percent were cyclopoid copepods, and as noted above, 71 percent were nauplii. Besides nauplii, no other taxon comprised more than 1 percent of the populations present. This number of taxa was probably due to the fact that the reservoir had been drained only a few weeks before.

The number of taxa collected during January, April, and October were 16, 17, and 9, respectively. During the previous year, collections yielded 12, 13, and 11 taxa; and the year before that yielded 22, 18, and 13 taxa.

The species diversity index (along with the number of taxa) for Neal Shoals decreased between the April quarterly sampling effort. The values reported were 2.84 in January, 3.00 in April, and 1.18 in October. The October 1982 value was the lowest ever reported for the entire study area, but it is similar to 1978.

l Zooplankton biomass was determined for three periods with values of 0.229 mg/ liter for January, 0.243 mg/ liter for April, and 0.086 mg/ liter for October. The 1982 biomass means for January and April were 46 and 40 fold, respectively, larger than the 1981 means; the 1982 l-October mean was only five times as large as in 1981.

1 1

)

Historical Trends. Historical data from 1978 to 1982 were reviewed and analyzed for possible trends in density, taxa count, species diversity, and biomass. The annual mean density was highest in 1978 (915.87/

l liter' then decreased sharply during 1980 to a value of 200.33/ liter.

l Mean density values increased in 1981 to 544.92/ liter, then decreased by nearly two-fold in 1982. Mean annual taxa counts fluctuated every I

l 2.5-5 l

year with the lowest occurring in 1979 (11.5), and the highest (18.3) occurring in 1980. Mean annual species diversity was lowest in 1979 (1.87) and highest in 1980 (2.70); values then decreased to 2.34 in 1982. The biomass values at Neal Shoals ranged from a low of 0.115 mg/

liter in 1981 to a high of 1.33 mg/ liter in 1982.

Sub impoundment 1982 Data. Zooplankton samples were collected from one station (Figure 2.1.1) in the subimpoundment during the four quarterly sampling pro-grams. The highest density was obtained in October with a mean of 160.03 and the lowest in July with 25.96. January and April collec-tions had means of 117.30 and 61.88, respectively. The number of taxa collected during January, April, July, and October were 14, 19, 22, and 20, respectively. The last two values were much higher than last years taxa counts of 12 and 13 for July and October. Fertilizat ion of the subimpoundment occurred from April to September, with a concomitant increase in phytoplankton abundance. The release of substances from some phytoplankton, particularly blue green algae, is thought to exclude zooplankton from certain areas and these substances may even be toxic if sufficient quantities of these algae ara present (Dames &

Moore, 1978). After the last application of fertilizer in September, zooplankton density greatly increased from 7 percent in July to 44 percent in October, as mentioned above. The phytoplankton bloom may have accounted for low zooplankton densities during July.

- The Rotatoria dominated all collections by 69 to 92 percent, except in April when only 28 percent of the zooplankters were rotifers. The copepods represented the dominant group in April (52 percent) and comprised lesser densities in January (29 percent), July (7 percent),

and October (16 percent). Cladocera appeared in only small numbers, accouating for 3 and 2 percent of the January and July zooplankton populations, respectively. No cladocerans were found in October, but in April they comprised 20 percent of the community.

2.5-6  !

Community composition between the four sampling periods yielded a diverse group of codominants. Keratella comprised over 75 percent of the rotifers in January and was also a codominant in. July; this organ-ism appeared in low quantities f oc the other two quarters. During the 1980 and 1981 investigations, a Keratella species and the copepod nauplii were the dominant taxa. According to Stemberger (1979) Kera- ,

tella is perhaps the most common limnetic rotifer in fresh water.

Nauplii were codominant for both the January and April sampling periods. Daphnia was a codominant in April with a value of 0.88/ liter as Trichocerca was in July with 0.39/ liter; these were the only times these genera appeared as codominants in 1982.

The species diversity values were directly related to the taxa values with the lowest in January (2.26) progressing upward to a high in July (3.32), and then dropping slightly in October (3.10). This trend is opposite to the 1981 diversity indices, when the highest diversity occurred in January (2.75) and the lowest in July (1.42) (Dames &

Moore, 1981).

Zooplankton biomass was determined for all sampling periods with values of 0.020 mg/ liter for January, 0.030 mg/ liter for April, 0.017 mg/ liter for July, and 0.038 mg/ liter for October. The 1982 April and July biomass means were nearly twice as high as the 1981 means. The 1982 January mean was over three times as high as in 1981, and was over 19 times as high in October 1982 as in 1981.

Subimpoundment i

Historical Trends. Historical data from 1978 to 1982 were reviewed and analyzed for possible trends in density, taxa count, species diversity, and biomass. The mean annual density was highest in 1978 (469.60/

) liter) and then decreased yearly through 1982 (91.27/ liter). Mean I

annual taxa counts fluctuated yearly; the lowest mean value occurred in 1981 (14.3)_ and the highest value in 1980 (19.8). Mean annual species 2.5-7

diversity values also fluctuated yearly; the lowest mean value was in 1981 (2.05) and the highest in 1982 (2.90). The mean annual biomass values were highest in 1978 (0.324 mg/ liter), remained low from 1979 through 1981, then increased in 1982 to a mean (0.188/mg/ liter); this value was nearly half the 1978 value.

Monticello Reservoir 1982 Data. Zooplankton samples were collected from Monticello Reser-voir at seven stations (Figure 2.1.1) during the four sampling periods.

The average density fot July (75.28/ liter) was slightly higher than for October (65.39/ liter). The densities for April (30.04) and for January (13.55) were much lower. Mean densities for individual sampling stations were similar between Stations K and 0, 62.40/ liter and 64.30/

liter, respectively. Stations I, J, and M provided mean densities between 36.62/ liter and 51.03/ liter. Stations L and N had similarly lower densities of 31.30/ liter and 35.28/ liter, respectively.

The copepods dominated approximately half of the January and April stations sampled accounting for nearly 50 percent of all zooplankton captured. The rotifers comprised 50 to 60 percent of all zooplankton in July and October. The cladocerans consistently had the lowest abundance, attaining their peak in April with 17 percent of the mean collected from all Monticello Reservoir stations.

Community composition between the seven sampling stations was very similar as evidenced by the codominant taxa. With a few exceptionsgthe l

codominants seemed to be the same for all sampling periods. As in past surveys, the nauplii were the most abundant, accounting for 22 to 1

i 38 percent of the total zooplankton community. Keratella, Polyarthra, and Synchaeta were also regular codominants. Kellicottia bestoniensis, I

the cyclopoids, and the calanoid copepod also were found as codominants a few times, and Bosmina was codominant once. The most codominants I occurred in January.

l

', 2.5-8

_.n - - . - - - - , - . , . - - - - - -- - . , , . , . , -

In addition to these codominants, several other species were frequently observed in the samples collected from the Monticello Reservoir, al-though in lower overall densities. The number of zooplankton taxa enumerated at the sampling stations ranged from 14 to 18 during Jan-uary, 14 to 19 during April, 15 to 21 during July, and 16 to 21 during October.

Species diversity ranged from 1.88 at Station I in July to 3.35 at Station M in January. Overall, January had the highest mean species diversity (3.25); diversity values decreased from April (2.80) to July (2.64) and October (2.61). Even though January had the highest mean diversity index, it did not have the highest taxa count; July and October, produced the highest numbers and taxa. Monticello Reservoir was the only water body in the survey with the highest mean diversity index in January. In 1981, it was the lowest diversity in January (Dames & Moore, 1981).

Zooplankton biomass was determined for all sampling periods, with values averaging 0.029 mg/ liter for January, 0.023 mg/ liter for April, 0.039 mg/ liter for July, and 0.019 mg/ liter for October. Station K produced the highest biomass over all the other stations during January, April, and July. However, in October it yielded the lowest j biomass. The 1982 January biomass value was slightly higher than the 1981 value; the 1982 April value was 2.5 fold the 1981 value; the 1982 July biomass value was ten times as high as in 1981; and the October value was almost twenty times as much as in 1981.

l Mo'nticello Reservoir l

Historical Trends. Historical data frem 1978 to 1982 were reviewed and analyzed for possible trends in density, taxa count, species diversity, and biomass. The mean annual density (of all the stations) was highest in 1978 (161.09/ liter); and then decreased through 1982 when the lowest l

value (46.10/ liter) was recorded. As in the other reservoirs, mean 2.5-9 l

i taxa counts fluctuated yearly. The lowest count was in 1978 (14.8);

high taxa counts occurred in 1980 and 1982 (17 and 17.5), respectively.

Species diversity values were uniform throughout the 5 year period; the

. mean values ranged from a low of 2.54 in 1981 to a high of 2.91 in l

! 1978. The mean annual biomass values were highest in 1978 (0.362 mg/

liter). During 1979 through 1981 the values (0.035 through 0.066 mg/

liter) were stable but remained low. During 1982 they increased to 2

0.197 mg/ liter, but yet were much less than the 1978 values.

1 2.5.3 Summary i The zooplankton communities observed during January, April, July, and October 1982 did not indicate any unusual trends. Based on assessments i

of taxonomic composition, densities, distribution among the stations, and species diversity, these zooplankton populations appeared to be progressing through normal seasonal changes'. The wide range of biomass l values recorded during the past few years has fluctuated both inversely and posit'ively to zooplankton density. These relationships may be due in part to the influence of high turbidity at some of the sampling stations, and the influence of non planktonic contamination. The i species composition of zooplankton at the twelve stations in the study area was similar to that reported during the 1978-1981 investigations.

L

! The rotifers were, overall, the dominant organisms collected during this study; these organisms are characteristic of limnetic habitats I

such as that found throughout the study area. Rotifers being dominant j and copepods and cladocera being less abundant appear to be a true representation of the overall zooplankton population even though it is known that most copepods and cladocera migrate upward from deeper waters to upper strata as darkness approaches (Pennak, 1978). The distribution of taxa indicates that generally stable zooplankton

[

communities exist. An exception to this occurred at Neal Shoals Dam during October; the reservoir above the dam was drained during July and f August and the zooplankton populations had not returned to their 6

earlier density levels. The frequency of zooplankter occurrence at all i 2.5-10 i_...._.._,_.__._,_,_._~_._

of the other stations indicated that few differences occurred within each major study area, with Parr and Monticello Reservotrs having particularly stable populations. Overall densities and taxonomic diversities at the stations for all areas did not appear to change appreciably from previous years.

Zooplankton fluctuations among the stations and through the seasons are probably reflections of a full range of environmental influences.

These effects may be mediated by timing of reproduction of plankti-vores, and increase in algal productivity with both positive and nega-tive influences, and effects of various abiotic changes. The co-existence of several different species in the same volume of water is assumed possible due to their differing tolerances and to optimum ranges of environmental conditions. Mechanisms include seasonal separation, vertical stratification, and size differences in relation to available food particles utilized. Non-abundant genera and species do not affect an area or ecosystem, but do reflect the diversity of the area.

2.5-11

a Table 2.5.1 Zooplankton collected in January, April, July, and October 1982, represented by numbers of organisms per major taxonomic category species diversity b, and biomass.c Page 1 of 2 Sub- E of x of Neal 2nticello Reservoir 1-0 Area Parr Reservoir B-O Shoals impo undment H I J K L M N O C D P - - - J Station B- - - -

80.38 13.98 3.94 4.95 3.59 5.09 4.59 3.30 5.66 Fbtatoria 4.16 10.54 7.03 7.24 33.48 1.79 1.00 5.23 0.79 0.86 2.08 1.22 Cl adocera 0.93 0.14 1.43 0.86 11.40 3.08 1.51 33.84 7.46 7.02 9.11 3.15 11.04 5.81 3.25 6.67 Copepoda 3.01 4.30 5.38 4.23 22.51 67.39 117.30 22.95 12.15 15.06 11.97 16.92 11.26 8.61 13.55 Total Density 8.10 14.98 13.84 12.33 17 18 18 18 17 17 21 18 16 14 17 14 l Total Taxa 18 15 3.28 3.35 3.31 3.24 3.25 2.95 2.66 3.61 3.07 2.84 2.26 3.28 3.10 3.17 Species Diversity 0.025 0.022 0.011 0.029 0.029 0.060 0.229 0.020 0.021 0.021 0.088 0.012 Blomass 0.062 0.088

" April 17.28 16.78 7.17 16.35 7.53 5.52 7.82 II.26 10.32 Rotatoria 2.58 19.50 0.65 7.60 29.97 12.12 9.46 2.65 6.02 2.15 2.22 2.22 10.54 5.02

" Cladocera 0.79 8.32 0.36 3.15 5.81 14.41 32.48 16.13 9.25 31.40 6.88 6.52 7.39 25.53 14.70 Copepoda 3.44 3.87 1.29 2.87 61.88 42.37 19.07 53.77 16.56 14.26 17.43 47.33 30.04 j Total Density 6.81 31.69 2.30 13.62 50.19 15 14 19 14 15 19 16 24 18 16 19 17 19 15 Total Taxa 2.74 2.74 2.79 2.89 2.87 2.77 2.81 2.80 Species Diversity 3.24 3.06 2.79 3.03 3.00 2.90 0.243 0.030 0.022 0.019 0.047 0.010 0.017 0.020 0.028 0.023 Blomass 0.053 0.068 0.066 0.062 l

Page 2 of 2 Table 2.5.1 (Continued)

Sub-E of i of Neal 1-0 Parr Reservoir B-0 Shoals impoundment %nticello Reservoir Area O Station B C 1 P H I J K L 1 N 23.88 7.24 15.70 43.67 26.10 76.93 36.14 51.77 36.78 Ibtatoria 22.94 32.62 25.31 26.96 0.00 0.36 4.45 4.66 3.44 3.15 1.72 4.52 5.45 3.94 Cladocera 3.51 7.46 3.87 4.95 0.00 0.00 1.72 63.24 38.79 37.57 18.50 13.34 23.02 47.68 34.56 Copepoda 15.42 16.35 10.61 14.12 0.00 25.% 74.93 59.15 84.68 47.75 91.99 63.68 104.90 75.28 Total Density 41.87 56.43 39.79 46.03 20 15 21 16 20 21 19 Total Tsxa 19 20 24 21 0.00 22 19 1.88 2.85 2.65 2.82 2.49 3.06 2.73 2.64 Species diversity 3.06 3.11 3.32 3.16 0.00 3.32 0.00 0.017 0.036 0.013 0.071 0.015 0.049 0.036 0.055 0.039 Blomass 0.0 51 0.063 0.068 0.061

,N October 255.68 133.79 15.06 25.88 65.82 31.26 52.20 27.31 60.16 39.65 Rota toria 53.78 103.25 24.81 60.59 Y 1.65 3.01 2.37 2.65 2.58 2.87 2.51 1.29 0.00 2.94 3.30 2.29 C Cladocera 3.51 1.15 33.56 23.16 26.24 13.62 26.31 27.96 15.99 25.74 19.07 Copepoda 21.51 22.87 11.40 18.5' 729.29 160.03 31.62 55.49 96.07 48.90 80.95 48.75 96.37 65.39 Total Density 78.60 127.27 39.08 81.67 1049.26 16 17 19 18 21 18 18 17 9 20 17 17 Total Taxa 16 18 2.49 2.50 2.64 2.51 2.65 2.78 2.74 2.61 Species Diversity 2.57 2.55 2.85 2.65 1.18 3.10 0.038 0.030 0.028 0.005 0.009 0.024 0.019 0.015 0.019 Biomass 0.032 0.087 0.062 0.038 0.086 bunts are in numbers of organisms per liter.

b (Shannon-Wiener species diversity index (Pielow 8966).

c Blomass is in mg/ liter of ash-f ree, dry weight.

l l

Table 2.5.2 Summary of mean annual values for Jooplankton obtained during monfioring programs from 1978 through 1982.

Neal Sub-Area Parr Reservoir Shoals impoundment M>nticello Reservoir P H I J K L M N O Station B C D Density (no/llter) 469.60 154.67 383.65 133.65 95.52 173.97 135.99 50.19 1978 101.18 231.32 103.25 915.87 92.85 59.73 115.08 74.71 823.40 128.20 117.37 107.84 116.94 83.39 101.89 1979 64.67 78.80 53.34 1980 66.75 132.79 68.76 200.33 186.13 70.70 82.31 162.97 66.39 106.62 66.11 544.92 278.84 88.33 94.36 119.60 54.35 69.69 130.06 55.50 1986 85.11 177.31 64.31 57.58 23.73 291.68 91.27 42.95 36.64 62.31 30.11 51.12 35.28 1982 33.91 U

Blomass (mg/ liter) 0.074 0.732 0.324 0.367 0.488 1.450 0.042 0.081 0.065 0.047 1976 0.093 0.341 0.041 0.019 0.045 0.053 0.046 0.215 0.050 0.045 0.043 0.033 0.026 0.039 1979 0.029 0.027 0.024 0.134 0.047 0.407 0.160 0.090 0.032 0.032 0.045 0.020.

1980 0.072 0.036 0.074 0.070 0.079 0.115 0.059 0.074 0.083 0.097 0.040 0.058 1981 0.206 0.174 0.195 0.355 0.549 0.404 1.330 0.188 0.196 0.145 0.378 0.083 1982 m Number of l

' Taxa ,

v 14.3 17.3 12.7 15.0 l 1978 12.0 14.3 12.7 14.7 15.0 15.0 13.0 16.0 20.8 11.5 16.5 16.0 16.0 16.8 17.0 18.3 15.8 17.8 1979 20.3 19.0 17.8 17.5 l 18.5 20.0 18.3 19.8 18.25 17.5 14.5 16.3 17.3 1980 19.3 15.0 15.0 16.3 l 1981 14.5 14.5 17.0 13.0 14.3 15.25 17.0 13.0 15.3  ;

14.0 18.8 17.25 16.25 15.5 18.8 16.8 17.8 19.5 1982 19.3 17.8 19.8 l j

Moan Species  ;

Diversity i 2.73 2.97 2.27 3.04 2.99 2.84 3.18 3.11 1978 2.69 3.13 2.58 2.48 3.03 2.72 2.99 3.17 1.87 2.56 2.78 2.90 2.85 2.95 2.96 1979 3.06 2.64 2.70 2.80 2.76 1980 2.92 2.67 2.93 2.70 2.78 2.72 2.78 2.61 2.47 2.05 2.56 2.58 2.43 2.61 2.47 2.53 2.63 1981 2.60 2.63 2.70 2.84 2.98 2.88 1982 2.% 2.85 3.14 2.34 2.90 2.60 2.80 2.81 2.88

_ = _ _ _ . _ . _ ._

i 2.6 ICHTHYOPLANKTON 2.6.1 Introduction Ichthyoplankton, comprised of the egg and larval component of the ichthyofauna, are of fundamental importance in assessing fishery suc-cess for two reasons:

1. Ichthyoplankton are the products of a species' reproductive efforts; therefore, ichthyoplankton abundance and survival bear directly on the reproductive success of a species.

2. Ichthyoplankton, particularly of forage species such as giz-zard shad, provide a valuable food resource to a number of desirable fish species.

The seasonal abundance of ichthyoplankton reflects the seasonal nature of reproductive activity by the parent fish. In temperate areas, 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 area by adult fish.

Because of their limited mobility, eggs and larvae are particularly 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 ef fluents discharged during power generation (Battelle, 1974). Thermal stress can kill organisms (Marcy,1971; 1973), weaken them and thus make them more vulnerable to predation (Schubel et al.,1978), or, in the case of eggs, cause abnormal development of the embryo which of ten results in death soon af ter hatchi,ng (Koo and Johnston, 1978).

2.6-1

Mechanical stress can also weaken or kill exposed organisms (Marcy, 1973). .

Ichthyoplankton samples were collected throughout 1982 at eleven sta-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 stations except C (Parr Reservoir) and P (Neal Shoals). At these two stations, only surface samples were taken because of the shallow water.

Data provided by these sampling efforts are described below for each of ,

the four study areas (Section 2.6.2) and then related to the present and developing fisheries in these areas (Section 2.6.3). The following characteristics are described 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 September 1982. No ichthyoplankton were found in samples collected in January, February, October, November, or December of 1982.

l l

l Presently, the limited knowledge of early developmental stages of many fish species restricts the level to which identification of ichthyo-l plankters can be made. Although identification of clupeid postlarvae to the species level is not presently possible, the preponderance of gizzard shad in adult collections from the study area indicates that l larvae listed broadly as Clupeidae are probably gizzard shad and will l be discussed as such. Uncertainty in identifying Lepomis larvae to the 1 2.6-2

, e - --. . . , . . . - - --,g --. .- - - m.. . . . . - - - , _ . .- - , - - . - ,- ,- -- --,--

species level (Conner,1979) warrants the conservative designation of these as Lepomis spp. (sunfish), although the majority of spacimens fit the " bluegill type."

Parr Reservoir t

1982 Data. Two distinctly different habitats were sampled in Parr Reservoir. Station B is located in the tailrace canal for the FPSF and is subject to high velocity and scouring currents. Most ichthyoplank-ton found at 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, and only surface samples are taken. This protected area harbors a resident larval fauna.

t i At Station B, patterns of increase and decline followed those of Monti-cello Reservoir, particularly Station L. This is to be expected be-t cause most larvae collected at Station B probably come from Monticello Reservoir via the FPSF. Larval fish were first collected at Station B in March and only included Morone sp. Clupeids were the most abundant larvae collected; second in abundance was Morone sp. Clupeid densities 3

(including Dorosoma sp.) reached 47.9/100 m in May, and the highest Morone sp. abundance was 5.5/100 m 3 in March. Densities for these predominant clupeids were highest in May and showed a declining trend in June, July, and August. Morone sp. density was highest in March and not found af ter May. Other taxa collected at Station B included minnows (Cyprinidae), suckers (Catostom!dae), sunfish (second in abundance in 1981), crappie, darters, yellow perch, and the mosquito fish (Gambusia) . This was the first time that the mosquitofish was

! collected from any of the water bodies in the study area; it only occurred in June. Moxostoma spp., a Catostomidae (collected only in April), also appeared here for the first time.

! 2.6-3

Station C showed a higher density than all other stations sampled in April (375.9 larvae /100 m3) and June (248.3/100 m3 ); and consisted

- mostly of the Clupeidae along with Dorosoma sp. (366.6 to 247.9/100 m3 )

during these respective months. Clupeids did not appear at all in March and then rose suddenly to their peak density of. 366.6/100 m 3 in

!. April. Clupeids were very abundant in May and June, were very low in numbers during July and August, and were not found at all in Septem-ber.

Other taxa collected at Station C were Morone sp., Cyprinidae, Lepomis r

sp, Perca flavescens, other Percidae, Centrarchidae, and an unidenti-4 fled Catostomidae. Pomoxis spp. was the second most abundant organism i found at Station C with its highest mean (18.36/100 m3 ) occurring in May, rising from 0.95/100 m3 in April. Morone sp. was the first larvae obtained in March, and was second in abundance in April (6.29/100 m3 ), and then declined in May and did not appear in sub-sequent samples.

Historical Data. Through the years, mean annual densities showed yearly fluctuations at Stations B and C (Table 2.6.2). Values de-creased from 1978 to 1979, increased in 1980; then decreased again in 1981. In 1982, Station B larval densities decreased by about one half while Station C densities doubled. Larval densities at Station C were

}

greater than at Station B during all of the collecting periods. Total

[

l number of taxa for Stations B and C, respectively, were 4 and 2 in l 1978- 9 and 8 in 1979, 10 and 8 in 1980, 7 and 8 in 1981, and 12 and 8 in 1982 (Table 2.6.3). Increases in abundance and diversity showed a '

trend toward more stable populations. In all years Clupeids were the dominant larvae, and were more common at Station C than Station B.

Neal Shoals i

1982 Data. Neal Shoals, Station P, is a control station removed from

! the influence of the FPSF and its attendant fluctuationc in water i 2.6-4 I

4

- , . . - . - . - . -,--..,,n,,--+.. .,-~,.,,,,-.,,m.--,, -7,, , , - , .n--,-- ,n,.,.,,_.,_,-n. , , , - , . , _ , .---n,-, . , - - - , - . , .

level; only surface samples are collected here. The peak in larval density was observed at Neal Shoals in May as a result of the presence 3

of numerous clupeids including Dorosoma sp. (413.8/100 m ); there sus a 2.5 fold increase over collections taken during May 1981 (Dames &

Moore, 1981). Total density declined sharply in June to 32.7/100 m3 .

of this density 30.9/100 m3 were Clupeids. Low densities of minnows, crappie, sunfish, darters, and brown bullhead were also present in these samples. The Percidae were the only taxa to be found in March (6.6/100 m3 ), and over 60 percent of the larvae found in April belonged to this family. They did not appear again in collections during 1982.

The water body above Neal Shoals Dan was drained during July for main-tenance and repair work on the powerhouse. As a result of this de-watering no ichthyoplankton samples were taken in July or August, and no specimens were found in samples taken during September through December. Historical data, from September through December, indicate that only an occasional specimen is collected, usually in September.

The peak spawning period occurs during April through June, therefore draining of the water body above Neal Shoals Dan did not have a negative Lnpact on the ichthyo plankton.

Historical Trends. Mean annual densities for Neal Shoals nearly doubled every year from 1978 through 1980. Values decreased in 1981 and then increased again in 1982, but not up to the 1980 level (Table 2.6.2). From 1979 to 1981 Neal Shoals values were similar to Station C in Parr Reservoir; however, in 1982 the density at Station C doubled that of Neal Shoals.

The total number of ichthyoplankton taxa found at Neal Shoals has in-creased by one or two every year, from 2 in 1978 to 8 in 1982 (Table 2.6.3). Throughout the years Clupeids, Pomoxis spp. Lepomis spp and Percidae were the abundant taxa; minnows were not collected until .

j 1981.

2.6-5

Subimpoundment 1982 Data. Station H is located in a subimpoundment at the northern end of Monticello Reservoir and is sampled at both surface and mid-depth. The fertilization program being carried out in the subimpound-ment is responsible for maximizing the development of a desirable fishery in this area. The first taxa were collected at this station in April and included clupeids, sunfish, and crappie (by far the most 3

abundant, especially from the surface collection (68.5/100 m )).

Af ter April, no other crappie were taken in collections at this station.

Sunfish larvae were present. in moderate abundaace (mean at surface was 6.7/100 m3 ; mean at mid-depth was 26.2/100 m3 ) in May, then appeared in low densities (no higher than 1.57/100 m3 ) from June through September. These sunfish densities are much lower than last year's mean surface June density of 86.3/100 m3 . Even though the ichthyo-plankton samples yielded low sunfish densities, the centrarchid family was the dominant adult group at Station H in 1982. These data suggest that the adult centrarchids are using the coves as spawning and nursery areas, and the larval fish are not collected since sampling is accom-plished in open water.

Clupeids reached their peak at Station H in May with surface and mid-depth means of 103.9/100 m 3 and 976.3/100 m 3 , respec tis ely. The latter was the highest mean density ever collected during this study, from any station, (Dsmes & Moore, 1978, 1979, 1979a, 1980, 1981).

Clupeids, during 1981 replaced centrarchids as the nunerically predomi-nant larval fish collected from the subimpoundment.

Other taxa collected at Station H in 1982 were channel catfisn (0.28/100 m 3 ), the only taxon caught in July, and an unidentified Centrarchid caught in September along with Lepomis spp.

Historical Trends. Mean annual densities at the subimpoundment have increased every year since 1978 which is expected since this is a new 2.6-6

-- - - - - - - -- -- g

water body (Table 2.6.2) . Lepomis spp. were the dominant taxa col-lected through 1980 and most were captured at the surface. Clupeidae were very few in numbers during these early years. However, in 1981 Clupeidae became the dominant organism (most were collected in the mid-depth samples) attaining greater densities than had been previously produced by Lepomis spp. Lepomis spp. became dominant again in Jure 1981 when few Clupeidae were found. Clupeidae were dominant again in 1982; Lepomis spp. were not very abundant and crappies appeared only in the surface samples in April.

The total number of taxa collected varied during each collection year, (Table 2.6.3), ranging from 1 in 1978 to 5 in 1982.

Monticello Reservoir 1982 Data. The seven stations (I, J, K, L, M, N, and 0) sampled in Monticello 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 March with a 3

mean density of approximately 0.17 organisms /100 m  ; the density increased in April to 6.6/100 m 3 and 1.83/100 m 3 in surface and mid-depth samples , respectively. From April through September, all stations collectively showed higher larvn1 fish densities in the surface samples; in March the densities were similar at both depths.

The frequency of taxa occurring in a total of 98 surface and mid-depth samples from March through September ranged from one for two different Ictaluridae (catfish) to 60 for Clupeidae (shad). The next most fre-quently occurring taxa were Lepomis spp. (25), Morone sp. (18), Pomaxis spp. (14), Percidae (13), and Cyprinidae, Catostomidae, and channel

catfish f rom 4 to 8 occurrences each. Two new genera appeared in Mon-ticello Reservoir in 1982

Moxostoma spp. in April at Station 0 (surface) and Erimyzon spp. in May at Station M (mid-depth).

2.6-7

Densities of larval fish at all stations increased in May and decreased in June with clupeids dominating the collections. In May 1982, the highest density of clupeids was found at Station M. The high numbers of clupeids may be concentrated in this sampling area due to it being a preferred spawning area, and also because of wind action causing the larval fish to be transported here by water currents from other parts of the reservoir. The area is located at the extreme southern end of Monticello Reservoir (Figure 2.1.1) in the close proximity of the FPSF.

This area is replenished with plankton and other food organisms due to pumping of water from Parr Reservoir as associated with the FPSF. As a result this area is proving to be an ideal location for harboring larval fish. The lowest density of clupeids was found at Station L; the low numbers are likely a result of strong water currents associated with the FPSF intake. Mean surface densities were nearly double those of the mid-depth densities of clupeids in May and only slightly higher at the surface than at mid-depth during June. Other major taxa col-lected at all stations during May and June had considerably lower densities than clupeids and included Pomoxis spp., Lepomis spp.,

suckers, darters, cyprinids, and white bass; all were generally more numerous in May than June. In June, total densities declined, mainly associated with a decline in clupeid abundance. Pomoxis spp. were not found at all in June or August, and were rare in July and September.

Percidae frequency and abundance increased slightly from May to June.

Sunfish frequency and abundance decreased substantially from May to June.

In July, densities continued to decline and sampling resulted in collections at two stations, J and M. Channel catfish were the most abundant larvae collected at Station M (11.06/100 m3 ). Additional taxa collected at both stations in July included minnows, suckers,.

Lepomis spp., Pomoxis spp., white catfish, and Clupeids. In August, Lepomis spp. was the most abundant genus captured although it was found at only three stations. Minnows, a darter, channel catfish, and an unidentified catfish each appeared at one station. The highest mean 2.6 8

density in August was 2.19/100 m3 (surface and mid-depth) for the channel-catfish. Catfish appeared in June, July, and August of 1982; only catfish appeared in September 1981. In September, averaged densities were the lowest recorded during 1982, and only three taxa, 1,epomis spp. , crappie and an unidentified sunfish were collected.

Lepomis spp. were found at Stations I, L, M, and O. Crappie and the unidentified sunfish occurred only at Station I. The mean of the surface densities was 0.14/100 m3 ; no specimens were found at the mid-depth.

Historical Trends. Overall, Monticello Reservoir stations showed an -

increase in mean annual density from 1978 through 1980, and then decreased in 1981. In 1982 there was no consistent trend among the stations (Table 2.6.2). Station M is the only one in which ichthyo-plankton abundance increased during 1981 and 1982. Since this is a newly formed reservoir, larval fish densities have been consistently lower than the other water bodies. A possible reason is that the I reproducing adult fish populations have not reached the high numbers typical of the other areas.

Taxa counts in Monticello Reservoir increased every year and increases were greater here than in the other reservoirs (Table 2.6.3). Stations M and I showed the greatest increases from 2 to 11 and from 1 to 9, respectively. The only station in Monticello Reservoir which showed a decline in number of taxa from one year to another was at Station L; a drop from 7 to 3 taxa occurred from 1981 to 1982.

2.6.3 Discussion A typical seasonal succession of fish larvae was observed in the study area during 1982. The first larvae to appear consistently in March were temperate bass; suckers and percids were also found once at

! separate stations. In early April crappie and clupeids appeared, and l by the end of April suckers, Lepomis spp., and minnows were collected.

\

2.6-9 l

l

. - _ _ _ _ . . . _ , _ _ . . . . _ _ _ _ _ _ _ _ _ - _ , . . , _ _ _ _ . ~ _ _ _ ,_ _ .. . _ _ _ _ _ _ _ . _ , _ _ , .

Ictalurids did not appear until mid-June. This succession is expected, based upon our knowledge on preferred spawning temperatures of the adult fish of these taxa.

Shallow water areas, especially Stations C, H, M, and P, with morpho-metric features conducive to influencing increased water temperature, were the first to produce relatively high abundances of larval fish.

(This comparison excludes the artificially enhanced fishery fn the subimpoundment .) The reason for these areas to produce larval fish early in the season was likely due to a rapid but stable increase in water temperature in these shallower, protected areas, resulting in the earlier attainment of preferred spawning temperatures. The earlier occurrence and abundance of Morone spp. larvae in March, and the higher larval fish densities in samples collected during April, indicated earlier spawning activity in 1982 than in 1980 or 1981. During the 1982 sampling program, overall monthly larval fish densities peaked higher than 1981 densities at all stations except B, J, and L. These increased densities could possibly indicate more favorable environmen-tal conditions for adult fish, 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 1982.

Ichthyoplankton sampling in Parr Reservoir resulted in collections of 12 ichthyoplankton taxa comprised predominantly of Clupeidae including Dorosoma sp., Lepomis spp., Pomoxis spp., and Cyprinidae. The ichthyo-plankton community at the Neal Shoals station was composed of 8 taxa comprised predominantly of Clupeidae and Lepomis spp., while Monticello Reservoir samples were composed of 16 taxa; the predominant species were Clupeidae, Morone sp., Lepomis spp., Pomoxis spp., and Percidae.

l The subimpoundment contained 4 larval fish taxa and, ranked in order of high to low abundance, included Clupeidae (shad), Poxomis spp. (crap-pie), Lepomis spp. (bream) (higher in frequency than Pomoxis spp.), and 2.6-10

. _ __ = . . . - .

i-i l

Ictalurus punctatus (channel catfish). Overall, the number of larval

. fish taxa collected monthly was lower at Neal Shoals than at Parr Reservoir, highest at Monticello Reservoir, and the lowest at the subispoundment. The subimpoundsent had the highest average larval fish density of any of the. water bodies. Neal Shoals was second, Parr Reservoir was third, and Nnticello Reservoir was fourth. This was the same order of abundance as in 1981. The subimpoundment was the most productive reservoir and verifies the success of the SCWMRD program to i

establish a recreational fishery here. De moderately high densities and variety of larval fish collected from Parr Reservoir reflects its relatively mature development. He overall low densities in 2nticello Reservoir, except at F*ation M, likely reflect it being a new impound-ment and a less developed ecobystem. The unusually high clupeid density at Station M in May (triple the 1981 value) and in June (double 4

the 1981 value) was the major factor for Monticello Reservoir having a higher average density than before. The Station M area appears to be developing into a productive fish rearing ground; it also yielded the most dense collection of adult clupeids.

Further evaluation of data on larval fish distributed among Monticello Reservoir stations showed that the greatest ntsnber of taxa was col-(

lected during 1982 at Stations M. I, and O. This high diversity, along with high abundance , may be due in part to the relatively shallower, somewhat protected environment at Station M compared to the other stations in the reservoir. The c 'erall high larval fish diversity expected at Station L, influenced by the FPSF, did not occur this year as it did in 1981. This correlatas with the low larval density at Station B, also influenced by the FPSF, during 1982. As in 1981, sun-fish populations in Monticello Reservoir during 1982 were relatively low considering the numerically abundant adult population. Iower den-sities of sunfishes may be due to fluctuating water levels in Monti-cello, caused by the operation of the FPSF, which interferes with '

reproduction by nest building species such as centrarchids. Snyder

{

I (1971) found that a pumped storage facility with similar fluctuations 2.6-11

O in water level limited the area used by nest ouilders. These species may also have been missed during ichthyoplankton sampling because areas 1 where they are likely to occur most abundantly are not sampled, such as the protected and shallow areas of the coves around the periphery of Monticello Reservoir.

The abundance of clupeid larvae in nearly all areas of Monticello Res-ervoir provides a valuable food resource to several recreationally important species (largemouth bass, crappie, and white bass) which, 4

both as larvae and adult, prey upon immature forage species such as gizzard.thad (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 the 1981 data are quite similar to those observed in previous years (Dames & Moore; 1978, 1979, 1979a, 1980, 1981). The

' early peaks in densities at Stations C and P in 1981, although varying in time by several weeks, were apparently the result of an unusually warm period in early spring at those stations that were more environ-mentally suited for fish spawning. Clupeid larvae were more abundant throughout the study areas in 1982, compared to 1981, yet similar to 1980 values. Steady increases in most other larval fish diversities and overall abundance were also evident from Monticello Reservoir data.

This trend should continue until Monticello Reservoir approaches maturity.

2.6.4 Summary A typical succession of larval fish species was observed in the study area during 1982. Morone sp. was the first taxon to appear in March and clupeids the ff rst to occur in notable abundance. The presence of these taxa was followed by that of the crappie.

2.6-12

4u- -

Clupeids dominated collections in all areas. The numerical abundance and wide distribution of clupeids in the study area make it an impor-tant forage fish which provides a valuable food resource to some of the recreationally important fish species present in the area. Parr Reser-voir and Neal Shoals produced the highest densities of clupeid fish (except for Station H in May) but also maintained a relatively diverse larval fish assemblage among areas sampled. In the subispoundsent, i

sunfish and crappie were proportionally more abundant than in other -

collections; this was presumed to be the result of directed management of this water body for recreational fishing. The subimpoundment had the highest overall larval fish density. Neal Shoals was second, Parr Reservoir third, and Monticello Reservoir was fourth. Parr Reservoir showed the greatest increase from 1961 in larval fish diversity, although overall abundance was below that found in the subimpoundment or in Neal Shoals during 1982. Parr Reservoir and Neal Shoals showed some characteristics typical of a mature fishery whereas Monticello Reservoir was typical of a naturally developing fishery, and the subispoundment showed characteristics of an enhanced or managed fishery.

i t

i 2.6-13

1 Table 2.6.1 Mean nonthly densities of larval fish (number /100 m 3) collected in net tows, March through September 1982. Page 1 of 7 Neal Sub-MARCH 1982 Area Parr Shoals imk>undment Monticello Stat ion B Ca pa H I J K L M -

N O.

Scientific Nay Comnon Name Dorosoma sp. Herring Sic - - - .

Mid (-) (-) ( -) (-) (-) (-) (-) (-) (-) (-) (-)

1 Clupoldae, Unid. Herring Sfc - - - - - - - - - -. -

(-) (-) (-) (-)

l Mid (-) (-) ( -) (-) (-) (-) (-)

i f

Cyprinus carpio Carp Sfc - - - - - - - - - - -

Mid (-) (-) (-) (-) (-) ( -) (-) (-) (-) (-) (-)

• Cyprinidae Minnows Sfc - - - - - - - - - - -

l Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) ,

a-Catostomidae, Unid. Suckers Sfc - - - - - - - - - - - i Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (0.20) i i mrone sp. Temperate bass Sfc 1.74 0.11 - - -

0.18 - - 0.66 -

0.32 r p Mid (3.75) (-) (-) (-) (-) (-) (0.49) (-) (0.49) (-) (-)

i i T Lepomis spp. Sunfish Sfc - - - - -

(-)

(-)

(-)

(-)

(-)

(-)

4 g Mid (-> (-> (-) (-) (-)

j Ponoxis spp., Crappie Sfc - - - - - - - - - - -

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) 1 Centrarchidao, Unid. Sunfish Sfc - - - - - - - - - -

l Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

i l Percidae Darters Sfc - -

6.62 - - - - - - - -

r

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-}

~ s 1

! Damaged , Un id. Sfc - - - - - - - - - -

! Mid (-) (-) (-) (-) (-) (-> (-) (-> (-> (-) (->

Total Sfc 1.74 0.11 6.62 - -

0.18 - -

0.66 -

0.32 l j Mid (3.75) (-) (-) (-) (-) (-) (0.49) (-) (0.49) (-) (0.20) l' i

j 16te: Sic = Surf ace Samples; Mid = Mid-depth a

l Only surf ace samples taken at Stations C and P 3

1 .

,l i

,i

)

I

r  ;

)

)

46 ) ) 6) 6) 14 ) 6) ) ) 8) 6) 70 2 2 4 2 44 35 68, 2. - - - - - -

7 O

72 0-( 0-( 30(

(

0

( ( (

1

(

0-( 33 3(

f 2( ( (

o 2 ) ) )

78 9) ) ) ) ) ) 06 e

g

) 48 01

) ) ) )

11 1 43 a - -

20 00 0-( - - - - - - - - - -

20 P N -( ( ( ( ( ( ( ( ( ( ( ( (

) )

)

) 30 ) ) ) ) 08 ) 5) ) 1) 6) ) 58 06 08 2 04

- - - - - - -- - - -- 2. - - - 5. - 0 75 M 54 ( 10 0 0 ( (

1 ( ( ( ( ( ( ( ( ( (

l o ) ) ) ) ) ) ) ) ) ) ) ) ) )

l e - - - - - - - - -- - - -- -- - - - - - - - - - - - -

i c L ( ( ( ( ( ( ( ( f ( ( ( ( (

t n

)

2 ) 32

)

) ) ) ) 1) ) ) ) ) ) ) 42 3 92 62 K

e 0U

(

(

(

(

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0- ( (

(

( (

(

(

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(

)

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00 J 0 ( ( ( ( ( ( ( ( ( (

( ( (

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) 35

) 46 ) ) ) ) 1 ) 08 ) 6) 3) )

94 9 81 1 3 25

- - 0 00 0 0 22 I 01 ( ( ( ( ( ( ( ( ( (

( ( ( (

t ) )

n )

2) 9 ) ) ) ) 90 e ) 71 ) ) ) ) )

51 97

-m - -

75 7

bd 0 85 95 un H (

00

( ( ( ( ( ( ( 6( ( ( ( ( 6(

Su o

p i

m

0) ) ) ) ) ) ) ) ) ) 2) ) 2)

- s )

6 laal ap - - 4 - - - -- -- - - -- -- - - - - -

6-( - - 0. -

1 eo Nh (

4

( ( ( ( ( ( ( ( ( ( ( 1(

S

) ) ) 3) 9) ) 5) 6) ) 8) 6) 8)

2) 9) 1 2 8 a 5 1 - 4 - - - -- - - 2. - -- 9. -

0-( -- 0-( 0. - -

C 2

(

4

( ( (

0-( 6

( (

0

( (

1

(

5 7(

6( 3 3

r r

a ) ) ) ) )

P ) 0) ) 71 ) 1 ) 4) ) 0 37

) 85 4) 2 2 62 20 1 68

- 1 - 4. - - - - -

0

-- O 0 36 B 24 0 0 01( ( ( ( ( ( ( (

( ( ( ( ( (

P

- n cd cd cd cd cd cd cd cd cd cd o cd cd cd cd f fi fi fi ii fi fi fi fi d fi fi ii fi fi SMi SM SM SM SM SM SM SM SM h n a i t

e a SM SM SM SM SM t p

a r t e C A S d s - s s d i

n a h io b c M r t e = a e

m e t F S t

a g g s s s a h e h s id N n n w r r r s s w r o o e e ip i o e M t n irr i

r p n h k p i

f p f l t a r r n d c m n a n l r  ;

o e e u e u r u e a s n n e a i R S T S C S Y D e e m H H C M k 2 o lp a 8 C m t

) 9 . a d 1

. d S s e i e u L id n e l n I n U s c p i

R .

o U n a m t P d . , e . f a n A i ip p , e c d r s o n r p e . a s i u C e . U s a . p d e n S e

( m p a p p v u c a s , c e d .

s s i

a = a N e a a i p h c e , f a a s d m m s l a c r 1.' c m u o o s s r f d d

n i

n t t e i i a d e f u 6 i o

s l

e s s n m x r a i g l S s

. f p

i r

i r o o o o o t c c a a 2 i o

r u p p x t r p n n r r m t y t

n y y o a e o e o e a o  : l e o l C C M C m L P C P P D T e n l e D C t O b

ic o a N a T S F&s~Ln

' l ,Ij 4 i$;' j i1]4  ; 1

Table 2.6.1 (Continued) Pag) 3 cf 7 Neal Sub-MAY 1982 Area Parr Shoals impoundment Monticello Stat ion 8 Ca pa -

H I -

J K L ~~

M N O Scientific Name Connon Name Dorosoma sp. Herring Sfc 2.30 5.51 257.35 6.01 0.43 -

8.53 0.73 1.14 2.38 1.58 Mid (4.03) (-) ( -) (24.44) (0.47) (1.84) (22.21) (3.98) (1.50) ( 7.35) (3.18)

Dorosoma cepedianum Gizzard shad Sfc -

4.80 0.73 - - - - - - - -

a Hid (-) ( -) ( -) (7.33) (-) (-) (-) (-) (-) (-) (-)

l Cl upeidao, Unid. Herring Sfc 16.95 175.34 155.75 103.91 107.97 29.18 30.60 39.92 471.52 55.05 52.03

Mid (24.61) (-) ( -) (976.25) (75.81 (97.38) (72.38) (2.89) (121.09) (36.88) (29.0 5)

' Cyprinus carpio Carp Sfc - - - - - -

0.11 - - - -

i Mid (0.14) (-) ( -) (-) (-) ( -) (-) ( -) (-) (-) (-)

Cyprinidao, Unid. Minnows Sfc - -

0.24 -

0.11 - - -

4.98 - -

Mid (0.19) (-) (-) (-) (-) (-) (-) (-) (0.28) (-) (-)

Erimyzon spp. Chubsucker Sfc - - - - - - - - - - -

Mid (-) (-) (-) (-) ( -) (-) (-) (-) (0.30) (-) (-)

t Catostomidao, Unid. Suckers Sfc - -

0.24 - - - - -

0.31 - -

Mid (-) (-) (- ) (-) (-) (-) (-) (0.72) (-) (-) (-)

. Morone sp. Temperate bass 5fc 0.15 0.89 - -

0.15 -

0.16 -

0.62 - -

)

Mid (- ) (-) (-) (-) (-) (-) (0.29) (-) (-) (-) (- )

f

• Leromis spp. Sunfish Sfc 1.53 2.84 0.97 6.61 0.11 -

0.26 0.69 5.71 0.27 0.50 i Mid (0.39) (-) (-) (26.15)' (-) (-) (-) (0.36) (1.43) (-) (-)

0.22 1.25 0.10 0.24 j Fbnoxis spp. Crappie Sfc 0.31 18.36 0.65 -

0.29 - -

Mid (0.19) (-) (-) (-) (-) (-) (0.14) (-) (0.28) (0.16) (-)

Centrarchidae, Unid. Sunfish Sfc -

0.28 1.54 - - - - - - - -

Mid (-) (- ) (-) (- ) (-) (-) (-) (-) (-) (-) (-)

Perca flavescens Yellow perch Sfc 0.15 - - - 0.61 0.47 0.11 -

0.21 0.26 -

Mid (-) (-) (-) ( -) (-) (-) (-) (-) (-) (-) (-)

i Percidae, unid. Darters Sfc 0.15 0.14 - -

0.52 - - -

0.31 - -

Mid (-) (-) ( -) (-) (0.16) ( -) (-) (-) (-) (-) (-)

Damaged, Unid. Sfc - - - -

0.11 0.50 0.15 - - -

0.26

! Mid (- ) (-). (-) (-) (-) (-) (-) (-) ( -) (-) (-)

To tal Sfc 21.54 208.16 417.47 116.53 11.03 30.15 40.14 41.34 486.05 58.06 54.61

, Mid (29.55) (-) ( -) (1034.17) (76.44) (99.22) (95.02) L7.95) (124.88) (44.39 (32.23) 3 Note: Sfc = Surf ace Samples; Mid = Mid-depth 1

• Only surf ace samples taken at Stations C and P

- . . _ . . - . . - - - _ - - . - -- - - - . _ _ _ . _ . . - .- - .- -, _ _ . . . . ~,

Page 4 of 7 Table 2.6.1 (Continued) _

JUNE 1982 Area Parr Sinals ivroundrent Monticello j

! Station B Ca pa H I J K L M N O j Scientific Name Comnon Name i - -

Dorosoma sp. Herring Sfc 0.46 0.75 5.01 - - - - - -

' Mid (0.12) (-) (-) (-) (0.38) (-) (-) (-) (0.35) (-) (-)

Gizzard shad Sfc 1.75 1.43 0.66 - - - -

0.80 4.28 0.11 -

Dorosoma cepedianum (-)

4 2 Mid (0.51) (-) ( -) (0.31) (3.05) (-) (-) (0.95) (0.92 (-)

a Clupeidae, Unid. Herring Sfc 6.03 245.71 25.2 2.18 1.68 2.01 3.46 8.22 51.61 7.04 2.55 '

l Mid (6.91) (-) (-) (15.95) (6.02) (1.54) (4.15) (3.15) (26 .16 ) (7.54) (7.22)

~

1 - - -

$ Cyprinus carpio Carp Sfc 0.12 - - - - -

Mid (-) (-) ( -) (-) (-)' (-) (-) (-) (-) (-) (-) '

7 - - - 0.31 - '-

! Cyprinidae Minnows Sic 0.11 - - - -

4 Mid (-) ( -) (-) (-) ( -) . ( -~) (-) (-) (-) (-) (-)

$ - - - 0.33 - -

?

Catostomidae, Unid. Suckers Sfc - - - - -

) Mid (-) ( -) (-) (-) (-) (-) (-) (-) (0.19) (-) (-)

1

( - - - - - -

Fbrone sp. Temperate bass Sfc - - - - -

(-)

3 1 Mid (-) ( -) (-) (-) (-) (-) (-) (-) (-) (-)

a f

Sunfish Sfc 0.33 0.12 0.22 0.27 0.12 - - - 0.17 0.48 -

y Lepomis spp. (-)

'

• Mid (-) (-) (-) (-) (0.26) ( -) (-) (-) .(-) (0.16 )

cn I - - - -

~ Crappie Sfc - 0.33 - - - -

Ponoxis spp.

Mid (-) (-) ( -) ( -) (-) (-) (-) . (-) (-) (-) (-)

Centrarchidae, Unid. Sunfish Sfc - - 1.28 - - - -

l (-) (-)

' Mid (0.12) (-) (z) (-) (-) (-) (-) (-) (-)

Perca flavescens Yellow perch Sfc - - - - - -

0.24 - - - -

Mid ( -) (-) ( -) ( -) (-) (-) ( -) ( -) (-)- -) ) (-)

i Sic 0.12 - - - 0.25 - - 0.16 0.10 -

l Percidae Darters -

(-) (-) (0.47) (-) (0.24)-

- Mid (-) (-) (-) (-) (-) ( -)

1 - - - - - -

! Gambusia affinis Mosqui to f ish Sfc 0.11 - - - -

(-)

3 Mid (-) (-) (-) ( -) (-) (-) (-) (-) (-) (-)

1 f ctalurus nebulosus Brown bullhead Sfc - -

0.35 - - - -

5

' Mid (-) ( -) ( -) ( -) (-) (-) (-) ( -) (-) (-) (-) t Ictalurus punctatus Channel carf Ish Sfc .-

(-)

Mid (-) (- ) (- ) (-) (-) (-) (-) (-) (0.85) (-)

Damaged, Unid. Sfc - - - - -

g

- Mid ( -) ( -) ( -) (-) (-) (-) (-) (-) (-) (-) ( -)

Sfc 9.03 248.34 32.72 2.45 1.8 2.26 3.7 9.02 56.86 7.73 2.55 l Total (4.1) (28.94) (7.7) ( 7.46) ;

Mid (7.66) (- ) (-) (16.26) (9.71) (1.54) (4.15)

Note: Sfc = Surface Samples; Mid = Mid-depth a Only surf ace samples taken at Stations C and P

-v- - - e -_ sm +-

Table 2.6.1 (Cont inued ) Page 5 of 7 Nsal Sub-

! JULY 1982 Area Parr Stosi s Irpoundmont  % nticallo

] Station B Ca pa H I J K L M N O Scientific Name Comnon Name Dorosoma sp. Herring Sfc - - - - - - - - - - -

Mid (-) (-) ( -) (-) (-) (-) (-) (-) (-) (-) (-)

Clupendae, Unid. Herring Sfc 0.23 0.23 - - - - - - - - -

Mid ( -) (-) (-) (-) (-) (0.29) ( -) (-) (-) (-) (-)

4 i Cyprinus carpio Carp Sfc - - - - - - - - - - -

l Mid (-) (-) ( -) (-) (-) (-) (-) (-) (-) (-) (-)

, Cyprinidae Minnows Sfc 0.25 - - - - - - -

2.10 - -

j Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

s Catostomidae, Unid. Suckers Sfc - - - - - - - - 1.62 - -

l Mid (-) (- ) (-) (-) (-) (-) (-) (-) (-) (-) (-)

1 l mrone sp. Temperato bass Sfc - - - - - - - - - - -

I Mid ( -) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

Lepomis spp. Sunfish Sfc 0.51 0.22 - - - - - - 0.23 - -

j Mid (-) (-) (-) (-) (-) (-) (-) (-) (0.25) (-) (-) '-

w Fbnoxis spp. Crappie Sfc -

0.22 - - -

0.27 - - - - -

• Mid (-) (- ) (-) (-) (-) (-) (-) (-) (-) (-) (-)

c.

I - -

i ~ Centrarchidae, Unid. Sunfish Sfc - - - - - - - - -

• Mid (-) (- ) (-) (-) (-) (-) (-) (-) (-) ( -) (-)

i Perca flavescens Yellow perch Sfc -

0.22 - - - - - - - - -

< Mid (-) ( -) ( -) ( -) ( -) (-) ( -) (-) (-) (-) (-)

1 I -

{ Percidae Darters Sfc - - - - - - - - - -

1 Mid (-) ( -) ( -) (-) (-) (-) (-) ( -) (-) (-) (-)

4 1

Ictaturus catus White catfish Sfc - - - - - - - -

0.34 - -

Mid ( -) (~) (-) ( -) (-) ( -) (-) (-) ( -) (-) ( -) t Ictaturus punctatus Channel catiish Sfc - - - - - - - -

11.06 - -

Mid (-) (-) ( -) (0.28) ( -) (-) (-) (-) (-) (-) (-)

i 4

i Damaged, Unid. Sfc - - - - - - - - - -

t Mid (-) (- ) (-) (-) (-) (-) (-) (-) (-) (-) (-)

Total Sfc 0.99 0.89 - - -

0.27 - -

15.35 - -

' Mid (-) (- ) (-) (0.28) (-) (0.29) (-) (-) (0.25) (-) (-)

pte

Sf c = Surf ace Samples; Mid = Mid-depth

! Only surf ace samples taken at Stations C and P

%I

Ttble 2.6.1 (Cbnt inued ) Pag) 6 of 7 Neal Sub-

• . Shoals impoundment Monticello AUGUST 1982 Area Parr

. Station B -Ca -

pa -

H I J K "

L 'M N O Scientific Name Comnon Name Dorosoma sp. He. ring Sfc - - - - - - - - -

H!d (-) (-) (-) (-) (-) (-) (-) (-) (- 1 (-) (-)

1 Clupeldae, Unid. Ibrring Sfc -

0.23 - - - - - - - - -

Hid (-) (-) (-) , (-) (-) (-) (-) (-) (-) (-) (-)

Cyprinus carpio Carp Sfc - - - - - - - - - -

1 Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

Cyprinidae Minnows Sic 0.27 - - - - - - - 1.84 - -

I Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

Catostomidae, Unid. Suckers Sfc- - - - - - - - - -

1 1

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

H>rone spp. Temperate bass Sfc - - - - - - - - -

j Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

sa Lepomis spp. Sunfish Sfc 0.27 - -

0.25 0.69 0.51 0.24 - - - -

, Mid (0.26) (-) (-) (1.32) (0.43) (0.30) (-) (-) (-) (-) (-)

4 1

g Fbmoxis spp. Crapple Sfc - - - - - - - - - -

! Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

Centrarchidae, Unid. Sunfish Sfc - - - - 0.23 - - - - - -

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

Percidae Darters Sfc - - - - - - - -

0.21 - -

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

i Ictaturus spp. Catfish Sfc - - - -

0.24 - - - - - -

(-) (-) (-)

~

Mid (-) (-) (-) (-) (-) (-) (-) (-)

letalurus punctatus Channel catfish Sfc - - - - - - - -

0.21 - -

Mid (-) (-) (-) (-) (-) (-) (-) (-) (1.98) (-) (-)

j Damaged, Unid. Sfc - - -

0.25 0.24 - - - - - -

Mid (-) (-) (-) (-) (0.43 (-) (-) (-) (-) (-) (-)

To tal . Sf c 0.54 0.23 -

0.50 1.40 0.51 0.24 -

2.26 - -

Mid (0.26) (-) (-) (1.32) (0.86) (0.30) (-) (-) (1.98) (-) (-)

p te: Sic = Surface Samples; Mid = Mid-depth Only surface samples taken at Station C.

tb samples taken at Station P.

l 1

-t

t-Table 2.6.1 ((bnt inued) Page 7 of 7 I Neal Sub- .. .

i SEPTEMER 1982 Area Parr Shoals impoundment %nticello '/

Stat ion B Ca pa H I J K L M N O Scientific Name Connon Name Dorosoma sp. Herring Sfc - - - - - - - - - '- -

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

l Clupeldae, Unid. Herring Sfc - - - - - - - - - - -

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

Cyprinus carplo Carp Sfc - - - - - - - - - - -

Mid (-) (-) (-) (-) (-) (-) (-) (.) (-) (-) (-)

j Cyprinidae Minnows Sfc - - - - - - -

i Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

j Catostomidae, Unid. Suckers Sfc - - - - - - - - - - -

l Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

i

! %rone sp. Temperate bass Sfc - - - - - - - - - - -

! Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

, w

, Lepomis spp. Sunfish Sfc - - -

0.13 0.16 - - 0.17 0.16 -

0.16 i Mid (-) (-) (-) (0.43) (-) (-) (-) (-) (-) (-) (-)

\

N 2 o Fbnoxis spp. Crapple' Sfc - - - -

0.15 -

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

Centrarchidae, Unid. Sunfish Sfc - - -

0.16 0.18 - - - - - -

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

i i Percidae Darters Sfc - - - - - - - - - - -

l Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

letaluridae Catfish Sfc - - - - - - - - - - -

Mid (-) (-) (-) (-) (-) (-) (-) (-) (-) (-) (-)

]

Total Sfc - - -

0.29 0.49 - -

0.17 0.16 -

0.16

! Mid (-) (-) (-) (0.43) (-) (-) (-) (-) (-) (-) (-)

l pto: Sfc = Surface Samples; Mid = Mid-depth Only surface samples taken at Station C.

Pb samples taken at Station P.

i

}

4 1

1

50 3I 03 47 28 30 63 90 34 01 O 44 86 81 36 60 31 1 1 00 40 13 60 49 35 40 18 60 74 N 74 02 97 90 31 21 11 55 37 11 60 05 26 90 29 62 21 M 33 64 48 13 20 21 82 l

o l 55 04 77 69 22 e 05 16 40 36 27 c L 76 85 71 i 42 40 t 3 2 n

55 69 93 74 37 K 25 72 54 85 42 92 34 29 95 64 32 1 1 2

8 16 86 00 94 9

1 J

35 27 7%

0 17 76 h 80 01 56 53 44 g 1 31 11 1 u

o r

h 06 90 29 t 00 03 47 25 66 80 23 8 I 07 07 22 7 12 12 9 2 1 32 1 1 1

)

3 m t 0 n 0 e 1 m 49 19 17

/ bd 65 43 r un H 18 62 81 20 11 e Su 40 63 54 23 71 b o p 1 2 34 25 m 1 u m n i

(

h P s s 3 3 9 3 .

i ll a d s f aa p 4 6

0. - 2. - 8. - h n h eo Nh 1 2- 6 6 6 t a t l

S 2 4 7 5 6 p n a e C o v d n r - s a 9 7 9 9 d n n l a 0 4 2 i o ev f C

0. - 5. - - - 0. - M i t e 3 9 2 9 9 o 0 3 6 5 1 = a s 1 t s r 2 d S f

_ e r i o

a M t it P 13 34 56 a mu i 50 47 s 04 37 61 63 37  ;

n s n.i m e B 34 44 55 44 56 e e

_ 21 11 kd x d 11 lp aea n m tl pm l

o cd cd cd a a

u i ii cd cd fi fi fi SM fi SM s smaea n a t SM SM SM e l sr n e a y c p o a r t a msf A S t f ah n i r std a s u ne e n S eot M e cnc

_ D = a e

_ f rl 2 l f rul a c uoo 6 u S sf c

_ n 2 n yya A

e D c9 c0 c c2  :

e lnna l x l n 8 7 8 1

8 8 t OOT b a 7 9

a e 9 9 9 1

9 1 1 b c T M 1 1 t Fmb~

Table 2.6.3 Total annual number of taxa (surf ace and mid-depth) for Ichthyoplankton, 1978 through 1982.

4 Neal Sub-Area Parr Shoals lepoundment R>nticello I

Station B Ca pa H I J K L M N O 1978 4 2 2 1 1 1 2 1 2 1 1 1979 9 8 4 3 5 3 3 4 4 3 5 l

, 1980 10 8 5 5 5 3 5 6 7 5 5 ,

1981 7 8 6 3 6 6 6 7 9 5 7 198h 12 8 8 4 9 6 6 3 11 6 7 l

i

.i y tbte:

T Clupoldae and Dorosoma sp. are considered as one taxa.

N Damaged (unidentitled) Individuals are not counted as a separate taxa.

" Taxa counts were summarized from Table 2.6.1 in the Dames & Moore reports 1 (1978, 1979, 1979a, 1980, 1981).

l 1

1 i

1 J

2.7 BENTHOS 2.7.1 Introduction i

l 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 indicators of the physical and chemical quality of aquatic ecosystems.

The benthic macroinvertebrate community may also provide an indication l of important trophic or food wcb relationships within the aquatic

! environment.

The purpose of this section is to discuss the benthic data collected quarterly during 1982, and to discuss important ecological trends and relationships which have occurred since June 1978. Evaluation and comparison of the benthic macroinvertebrate data collected during 1982 was based on seasonal variables among the transects sampled and on mean annual values calculated from composite quarterly survey data (Tables 2.7.1 and 2.7.2). Mean annual values were calculated from triplicate

( samples which were collected at.each transect in January / February, May, July, and October. The evaluation of trends and relationships which have . occurred in the benthic communities at and among the transects sampled was based on a comparison of the 1982 data with that collected since 1978. Benthic data for the period 1978 through 1981 are con-tained in the respective Environmental Monitoring reports (Dames &

Moore; 1978, 1979, 1979a, 1980, 1981) and are summarized along with the 1982 data in Table 2.7.3.

Quantitative benthic macroinvertebrate samples were collected from twelve transects in the study area (Figure 2.1.1) and analyzed for species presence and density. Biomass, number of taxa, diversity, and equitability were also determined. Each of these data points provides valuable information about the well-being of the benthic community and l

i l

2.7-1

,e, ,. --7..- . -.y - , . _ . , - , , . . _ . , , , , , . . . , . , ,-, ,m ,, , . , , . ~ . , _ . -._m., r,_,,....~,.-_-y.-....,,n_, , ...---.._--y. _ , , ,__y-

the aquatic ecosystem at the transects sampled. The component of density provides information on the upper and lower ranges of the num-ber of organisms per square meter of a particular taxon or community.

Biomass data supplement density measurements with weight per square meter measurements and also show upper and lower limits for specific taxa and entire communities. The community components of diversity and equitability provide evaluations of taxonomic richness or variety, and evenness or the apportionment of individuals among taxa. Higher diver-sity and equitability values generally indicate more complex food webs (numerous functional feeding groups present at different trophic levels) and increased consnunity stability (reduced oscillations or mod-eration from extreme variations of density, biomass, and taxonomic makeup).

2.7.2 Findings Parr Reservoir 1982 Data. The average density for total benthic macroinvertebrates, obtained from the mean densities of all three sampling locations, ranged from 1863/m 2 in May to 860/m 2 in July. The highest mean density occurred at Transect B in May (4000/m2 ); the greatest mean annual density (1814/m 2 ) also occurred at this transect. High densi-ties in May were primarily the result of large concentrations of the Asian clam (Corbicul_a_mani1~ensis)"at Transect B and large numbers of clams and oligochaetes (mostly tubificids and naidids) at Transects B and D (Table 2.7.1) during that month. The lowest benthic community counts were found at Transect C in May (384/m2 ); Transect C also had the lowest mean annual density (1070/m2 ). Mean annual biomass was 133.18 g/m 2 at Transect B, 6.46 g/m2at Transect C, and 27.18 g/m 2 i

at Transect D. Transect B showed a substantial increase in mean annual l

biomass over past values. This was primarily a result of an increase l in the numbers and mass of the Asian clam (Corbicula manilensis).

in 1981 to 6.46 g/m2 in 1982.

1 Transect C decreased from 12.78 g/m 2 1

2.7-2

Community composition varied among the four sampling periods. Gen-erally, however, benthic community characteristics at Transect C were more similar to Transect D than to those found at Transect B (Table 2.7.1). In January / February, bivalves were the most abundant organisms collected from Parr Reservoir, making up almost 40 percent of the total community. These organisms were particularly abundant at Transects B and C where they made up 57 and 40 percent, respectively, of the total collections at these stations. Ephemeropterans (Hexagenia limbata) and dipterans were the next most abundant organisms collected from Parr Reservoir during January / February, but only at Transects C and D. A large number of coelenterates of the genus Hydra (531/m2 ) were col-lected from Transect B in January; this group of organisms appeared only one other time, at B in July, and in very low concentrations (14/m2 ). In May, bivalves were again the most abundant group of benthic organisms collected from Parr Reservoir, but only because of the large number (2784/m2 ) encountered at Transect B; few were found at the other two transects (Table 2.7.1). Oligochaetes (tubificids and naidids, primarily) were also very abundant in May, while the number of dipterans and ephemeropterans declined over January levels, probably due to spring emergence of adults. In July, oligochaetes were the dominant organisms at all of the Parr Reservoir sampling stations, with bivalves being the second most numerous group. In October, the dipter-ans (chiefly chironomids, Glyptotendipes sp. and Dicrotendipes sp.)

were obtained in large numbers and were the most abundant group of benthic organisms at Stations B and C, along with oligochaetes (chiefly unidentified tubificids and Branchiura sowerbyi) at Trar. sect D. The number of ephemeropterans increased over the May and July' levels especially at Transect C, but were not found at Transect B.

l As with community composition, the mean annual number of taxa col-lected, species diversity, and equitability of the benthic populations studied were similar at Transects C and D as compared to Transect B.

The mean annual number of taxa was 13.0 and 12.3 at Transects C l

l 2.7-3

- - - ---,.-,,,g. - - - - , -. - -------,y - , , . - , - . - - - ,,n , -,, ,

d i and D, respectively, whereas at Transect B it was only 8.5. Mean ,

annual species diversity (1.81) was also lowest at Transect B compared l with 2.53 at Transect C and 2.61 at Transect D. Mean annual equita-

, bility at Transect B (0.60) was lower than at Transects C and D, where equitabilities of 0.73 were recorded.

Historical Trends. During 1982, the benchic macroinvertebrate com-munities in Parr Reservoir showed trends among transects which were similar to those found during previous surveys (Dames & Moore; 1978, c 1979, 1979a, 1980, 1981) (Table 2.7.3).

2 After more than doubling between the 1979 and 1980 surveys (395/m to 871/m2 ), the mean annual density at Transect B remained stable during 1981. However, the mean density at Transect B doubled again between 2

2 to 1814/m 1981 and 1982, increasing from 882/m . This increase l was due primarily to the larger number of Asiatic clams and oligo-

! chaetes at Transect B in May, coelenterates in January / February, and nematodes and dipterans in October. Comparing the surveys or 1979 with l

1980 (1978 data are presented in Table 2.7.3 but are not discussed f since sampling was performed for only three seasons instead of four as in the following years), the mean annual taxa, diversity, and equit- *

' ability values declined at Transect B in contrast to Transects C and D  ;

i which increased slightly (Table 2.7.3) . This trend at Transect B reversed during the 1981 survey; the mean annual values of these param-eters. continued to increase through 1982 at this transect (Table 2.7.3). Since increases in the number of taxa, diversity, and equita-bility indicate greater stability in aquatic ecosystems, these changes

! are considered to reflect slight improvement in the benthic macroinver-tebrate community at Transect B over the past two years. However, the j

indicator values remained below those for che other transects in Parr Reservoir, indicating that -the tailrace area is a physically stressed environment.

[

The trend towards a decreasing mean number of taxa, diversity, and equitability at Transect C from 1979 through 1981 was reversed in 1982.

2.7-4 i

l l

,c.m. - _ , _ . . . . . _

.-__._.-,._..-,,---....._,_,_.,_.,_.-.,_..-.._-..._r,...

_.,-__.-.-,,,,e

However, the 1982 mean annual density at this transect (1070/m2 )

declined and was less than 59 percent of the mean density recorded for 1981 (1817/m 2 ) and less than 54 percent of that recorded in 1980 (1985/m2 ). If these trends continue, the benthic community at Transect C may become more stabic due to the presence of a greater variety of organisms but may also provide a less concentrated food source for predators as a result of the benthic population decline.

No consistent trends in density, number of taxa, diversity, or equi-tability have been evident in the benthic community at Transect D dur-ing the 1978-1982 study period (Table 2.7.3).

Neal Shoals 1982 Data. The mean benthic macroinvertebrate density at Neal Shoals Dam was highest in January (4205/m 2

) and lowest (743/m2 ) in October. Low population levels in October were likely a result of water drawdown in the study area above Neal Shoals Dam during July for dam and powerhouse repair. No samples were collected from Transect P in July because the reservoir was dry. Dipterans (particularly 2 Chironomus sp, Procladius sp., Tanytarsus sp., Coelotanypus sp.,

Polypedilum sp.) and oligochaetes (primarily tubificids) were th most abundant groups of benthic organisms collected during each of the sampling periods; bivalves (Corbicula manilensis) rivalled the oligo-chaetes in importance at Transect P only during January / February.

l The mean annual number of taxa collected at Transect P, together with that at Transect J (15.0 each), was the highest recorded for any of the l

sampling locations in 1982. The mean annual diversity (3.07) at Tran-I sect P was higher than that of any other transect, and mean annual equitability (0.80) was among the three highest values recorded (Table f 2.7.2). The winter and spring biomass values showed a decline from the 1981 results.

l l

l 2.7-5

- - - - ~ . , _ . .-. - _ - -. . _ . -

Historical Trends. Since 1979, the benthic population at Transect P has been very stable (Table 2.7.3). The 1978 data were not compared to other years since sampling was performed for only three seasons instead of four as in the following years. The 1982 data indicate continued stability at this sampling location.

Subimpoundment 1982 Data. The mean density at Transect H was highest in October 2

(16,626/m2 ) and lowest (3143/m ) in July. The mean annual density (7632/m 2 ) was higher at Transect H than at any of the other sampling locations (Table 2.7.2). Dipterans (primarily Chaoborus spp., in-cluding Chaoborus punctipinnus; Chironomus sp.; and Glyptotendipes spp.) and oligochaetes (especially tubificids and naidids) were almost the exclusive inhabitants of the sediments at Transect H, comprising a minimum of 95 percent of the benthic community during each sampling period. The mean annual number of taxa (9.8), mean annual species diversity (1.85), and mean annual equitability (0.59) found at Transect H were similar to values reported for Transect B.

The mean annual biomass at Transect H (0.58 g/m 2 ) declined consider-ably from 1981 levels (1.26 g/m2 ). These data indicate that the carrying capacity of benthic macroinvertebrates may have been attained in this managed reservoir. It is likely that future sampling-will show benthic organism biomass and densities similar to those observed in 1982. Densities below the thermocline are likely to remain at a rela-tively constant level because of the limiting effect of low dissolved oxygen concentration; organisms living in the well-oxygenated littoral and sublittoral zones will probably remain at similar density levels because of the limiting effect of fish predation. If, however, the fertilization program is altered, the benthic population can be expect-ed to fluctuate. To this date no Asian clams have been discovered in .

2.7-6

i the subimpoundment. If this species is introduced the benthic biomass

- may be expected to increase substantially.

Historical Trends. The benthic community at Transect H has changed considerably in species composition, density, biomass, diversity, and equitability from 1978 through 1982 (Dames & Moore; 1978, 1979, 1979 a ,

1980,1981) (Table 2.7.3) . However, the 1978 data were not compared to other years since sampling was performed for only three seasons instead of four as in the following years. The mean annual density increased 2

by about 81 percent between 1979 and 1980 (3343/m2 to 5833/m ,

respectively), and continued to increase although at a slower rate (41 2

percent) through 1981. The size of the 1982 (7632/m ) benthic com-munity was almost 7 percent smaller than that collected in 1981 (8201/m2 ), however. The mean annual number of taxa declined from a high of 19.0 in 1980 to 9.8 in 1982; mean annual species diversity followed a similar trend, falling from a high of 2.98 in 1980 to 1.85 in 1982. Mean annual equitability values showed similar declines from 1980 (0.70) through 1982 (0.59). These trends indicate that the ben-thic community at Transect H may have reached a growth plateau and that 4

environmental conditions in the subimpoundment are becoming less favor-able to some organisms.

Monticello Reservoir j 1982 Data. The average density for total benthic macroinvertebrates, obtained from the mean densities of all seven sampling locations, 2 in January / February to 1588/m 2 ranged from 1858/m in July. Mean densities for the individual transects sampled ranged from a low of 271/m2 at Transect J in July to a high of 4329/m 2 at Transect'L in i May (Table 2.7.1). Transect L had the highest mean annual density (2692/m 2 ) for the year, while Transect J had the lowest (1390/m2 )

t i .(Table 2.7.2).

I i 2.7-7

c Dipterans represerted 45 percent of the benthic community collected from Monticello Reservoir, and were the most abundant macroinverte-brates obtained during the January / February sampling effort; oligo-chaetes comprised 33 percent of the samples and were the second most numerous group. By May, the average dipteran population among the seven stations sampled had declined by a factor of 3.5, probably due to spring emergence of adults. The average size of the oligochaete com-munity had grown to 56 percent of the total organisms sampled, making this the most numerous benthic class collected from Monticello Reser-voir during the spring sampling. The overall bivalve population also increased substantially between January / February and May, from 16 to 28 percent of the total population sampled, primarily at Stations L and M.

Through July, the average percentage of oligochaetes in Monticello Reservoir continued to increase in numbers, representing 65 percent of the total benthic community, while the bivalve and dipteran communities decreased to 26 percent and 7 percent of the total collection, respec-tively. Between July and October, the oligochaete community in Monticello Reservoir experienced a substantial decline (to 39 percent of the total community) while the dipteran community increased by a factor of five. As a result, the average oligochaete and dipteran communities at the Monticello Reservoir transects sampled were very similar in density during October.

The major benthic taxa collected from Monticello Reservoir were rela-t l tively well-distributed among the transects sampled during all of the sampling periods. The Asian clam Corbicula manilensis, the dipteran Glyptotendipes, and naidid worms, and tubificid worms were among the most common benthic organisms collected from Monticello Reservoir.

Other dipterans such as Coelotanypus sp., Dicrotendipes sp., Chironomus sp., and Pseudochironomus sp. were also well distributed within the

! reservoir but were generally present in smaller numbers. The mayfly Hexagenia limbata was the most common ephemeropteran identified and, l although present in relatively small numbers, was evenly distributed among the stations sampled.

2.7-8

The transect with the highest mean annual number of taxa was J (15.0);

the next highest was Transect I with 14.5 taxa. Transects M (11.8) and O (12.0) had the least number of taxa. Mean annual taxonomic diversity (3) figures indicated that the most diverse benthic community occurred at Transects I (3.06) and J (3.02), wh!1e the lowest taxonomic diversities occurred at Transects L and M, 2.26 and 2.16, respectively (Table 2.7.2). Equitability values were between 0.61 and 0.81, with Transect I being highest and Transect M the lowest (Table 2.7.2).

Eenthic biomass in Monticello Reservoir increased substantially at all Transects (I-0) during 1982. This increase was predominantly due to the incresse in size and nu:nbers of the Asian clam. The transect with 2

the highest mean annual biomass was M (141.16 g/m ) with the next highest being Transect L (58.66 g/m2 ). The transect with the lowest mean annual biomass was K (26.70 g/m2 ). The transect that showed the greatest increase was Transect I, which showed a 22 fold increase over 1981 data.

Historical Trends. Mean annual benthic macroinvertebrate densities at Transects I, L, and O have increased every year since 1979 (Table 2.7.3). The 1978 data were not compared to other years since sampling was performed for only three seasons instead of four as in subsequent t years. Transects M and N showed increasing densities from 1979 through 1981 (982/m2 and 545/m2 to 2084/m2 and 1460/m 2 , respectively),

and then the benthic populations stabilized, at least temporarily in 1982 (2012/m 2 and 1462/m 2 , respectively). There have been no con-l l sistent year-to year trends in community density at Transects J and K; however, benthic macroinvertebrate numbers have increased dramatically, as at the other Monticello Reservoir transects, since 1979.

l The number of taxa collected has increased annually since 1979 only at l

Transect I (1978 data have not been used for comparative purposes since j

samples were collected only during three quarters in that year); how-ever. the ncuber of taxa declined only in 1982 since the preoperational j monitoring studies began in 1978 at Transects K, N, and O. The number l

2.7-9

i of taxa collected at Transects J, L, and M were similar in decreasing between 1979 and 1980, increasing in 1981, and then remaining stable (Transect J) or decreasing (Transects L and M) in 1982. Although some Monticello Reservoir stations have shown decreased numbers of taxa during certain years, the overall trend at all transects is toward a greater number of taxa.

Mean species diversity has increased annually since 1979 only at Transect J, and showed a slight decrease only during 1982 at Transect O. Trends in species diversity at Transects K, L, M, and N have been the same since 1979, decreasing between 1979 and 1980, then increasing in 1981 only to decrease in 1982. A similar trend is evident at Transect I except that diversity increased there between 1981 (2.79) and 1982 (3.06). As with taxa numbers, the overall trend which is evi-dent at all of the transects during the past five years has been toward greater diversity.

Transects L, M, N, and 0 have shown the same trends in equitability since 1979, while the other three transects show no consistent year-to-year pattern. Unlike density

• taxa numbers, and diversity, equitabil-ity has not increased during the 1979-1982 period at all of the tran-sects sampled. Equitability measurements at all transects, except Transect J, have declined during that period of time.

2.7.3 Discussion i

Several important observations may be made by comparing the data col-1ected during the past four years. (Data collected in 1978 have not been used for comparative purposes since samplee were collected for only three seasons during that year.) These observations reflect the overall characteristics of the aquatic environment in which the benthic communities have been developing since the construction of Monticello Reservoir and the subimpoundment.

2.7-10

Five trends are apparent from a review of the benthic macroinvertebrate data collected from Parr and Monticello Reservoirs, the subimpoundment, and the control station at Neal Shoals. These trends have been ob-served through objective evaluations of both short and long term changes in benthic macroinvertebrate community components. These trends may be characterized as: 1) reduced diversity of taxa at Tran-sect B accompanied by increased density as compared to other transects in Parr Reservoir; 2) maintenance of a stable benthic component at Neal Shoals Dam, Transects C and D in Parr Reservoir, and Transects I, L, M, and N in Monticello Reservoir; 3) increasing benthic community diver-sity at Transect J in Monticello Reservoir; 4) increasing taxonomic diversity in Monticello Reservoir at Transects K and 0 until 1982 when a slight reversal occurred; and 5) declining taxonomic diversity at Transect H since 1980, accompanied by very high densities throughout the study program.

Transect B in Parr Reservoir has typically shown considerably lower ecological stability and a more simplified community structure than any of the other transects sampled since 1979. This characteristic has been recognized in previous Dames & Moore reports (1978, 1979, 1979a, 1980, 1981) and is evidenced by lower community diversity and fewer taxa, illustrative of a simplified community structure. Although mean annual values of these indicators remain much lower than at the other transects sampled (excent Transect H in 1982), a trend toward an increase in these indicators has been apparent since 1981.

A trend towards maintenance of ecological stability and complexity between 1979 and 1982 is apparent at Neal Shoals Dam, Parr Reservoir Transects C and D, and for Transects I, L, M, and N in Monticello Reservoir. Although Transect C showed a slight decline in the overall complexity of the macroinvertebrate community in 1981, it was attri-buted primarily to natural variation (Dames & Moore, 1981). This assumption was borne out by the 1982 data, which showed diversity values at Transect C similar to those of 1980. It is anticipated that 2.7-11

the decrease in mean annual diversity experienced at Transects D, L, M, and N in 1982 will similarly be found to be the result of natural variation once the 1983 data are collected and evaluated. Therefore, the benthic communities at these transects are considered to be stable.

Transect J has experienced an increased mean annual number of taxa and diversity since 1979; the equitability at this station has remained stable. These characteristics indicate continuing Laprovements of benthic community stability at this transect. Increases in benthic community complexity and stability at Transects K and 0 were also evident through 1981, but slight declines in the mean annual number of taxa and diversity occurred in 1982. These declines may be the result of natural variation, but they may also signal a plates" in community stability and complexity at these transects.

For the first time since 1979, the mean annual benthic density at Transect H declined in 1982, although only slightly. The mean annual number of taxa present and benthic diversity have been declining since 1980; equitability decreased between 1980 and 1981 and remained near 1981 levels during 1982. These data, together with the species com-position at this transect, indicate that the nutrient enrichment pro-gram in the subimpoundment (which began in April 1978) has resulted in relatively eutrophic, unstable conditions at Transect H.

l l

2.7.4 Summary The benthic macroinvertebrate data obtained from 1982 were similar in many respects to that recorded during earlier surveys of the four major study areas. As previously noted, Transect B in Parr Reservoir con-I tinues to show a lower ecological stability and complexity than any other transect in Parr or Monticello Reservoirs (excluding the subim-poundment). During 1981 and 1982, however, the difference in these l

l parameters at Transect B and the other transects had moderated some-2.7-12

what. However, the relative level of physical stress due to the sta-tion's close proximity to the FPSF was still evident. The remaining transects in Parr Reservoir (C and D) continue to have diverse benthic macroinvertebrate communities, illustrative of ecological stability and complexity.

The macroinvertebrate communities in Monticello Reservoir except at Transect J exhibited relatively stable mean annual values for density, taxonomic composition and diversity, equitability, and biomass.

Transect J was the only station in Monticello Reservoir which has shown consistent increases in parameters measured.

For the first time since 1979, the benthic community in the subimpound-ment (Transect H) showed a decrease in density; it has continued to show a lower number of taxa and reduced diversity since the 1981 sur-vey. This trend is expected to continue as long as intensive fertili-zation continues. The subimpoundment is the only area sampled to date in which the Asiatic clam has still not been reported.

2.7-13

Table 2.7.1 Summary of banthic macroinvertebrate data collected frvm twelve stations during the 1982 monlioring program."

Page I of 4 Neal Sub-Area Parr Reservoir Shoals impoundment M>nticello Reservoir Station B C D P H I J K L M' N O JANUARY /

FEBRUARY Taxonomic Category Coelenterata 531 - - - -- -- - -- --

Turbellaria - - - -

g- 14 14 -- - 14 -- 14 Nematoda -- --

14 28 -- -- - 14 -

14 -- E Ollgochaeta 57 270 300 889 1,564 258 57 186 1, 521 315 201 1,722 Hirud inea -- -- -

43 -- -- - -

14 - -- --

Gastropoda 14 - - - - -- -

p Bivalvia 847 803 115 918 -- 661 288 144 201 574 58 158 1,721 y Diptera - 271 543 2,256 5,465 1,144 1,090 286 787 445 372 E Ephemeroptera 28 632 258 28 14 144 29 187 I4 201 29 43 Megaloptera - 14 - 14 -- - --

Trichoptera -- - 29 -- - -- -

14 -

Plecoptera 14 -- 29 - - - -

l Hydracarina - 14 14 - -e 14 - -- -

Insecta - - - - - - 14 - -

TOTAL 1,491 2,004 1,273 4,205 7,043 2,235 1,492 817 2,551 1,563 660 3,687 4

" Numbers are organisms /m .

I i

I Table 2.7.1 (Cbntinued) Page 2 of 4 Neal Sub-Area Parr Reservoir Shoals impoundment M>nticello Reservoir B C D P H I J K L M N O Station MAY l Taw >nomic Category 43 - - - - 14 - -

14 -

Nematoda 14 -

1,118 919 273 2,569 29 1,421 1,135 2,927 345 1,147 244 01Igochaeta 157 Bivalvia 2,784 85 86 - - 158 301 43 1,076 1,636 158 287 143 830 1,147 199 686 143 269 28 126 199 Diptera 70 71 Ephemeroptera 14 57 14 72 -- 14 29 57 57 -

43 57 Megaloptera - -- - 28 - -- --

Tricho ptera - 14 -

- 14 - -

Hydracarina - - - - -

e" 4,000 384 t,205 1,203 3,716 400 2,4 51 1,392 4,329 2,009 1,488 787 Y TOTAL 0;

Table 2.7.1 (Cbntinued) Page 3 of 4 Neal Sub-Area Parr Reservoir Shoals impoundment 2nticello Reservoir P" I J K L 'M N O Station B C -

D H - -

JULY Tam nomic Category Coelenterata 14 - - - -- -- --

g- ; --

14 '29 - -t - --

/ Turbellaria - - - - 29 , - -

Nematod e 29 - - -- -- -- 14 - 14 [ - -

602 1,119 1,249 245 215 817 1,307 991 2,024 1,622 Gl lgochaeta 287 -

i. 9  :

Bivalvla 158 43 215, - - 215 14 216 875 1,tJ3 ,

158 330 Diptera 56 - 1,865 171 14 70 100 57 228 . ' 185 d ,

Ephemere ptera 14 29 14 -- -- 114 - 28 -- , 14 - -

p g

M t 2,095 2,410 2,137 1,160 2,2%

g TOTAL 502 674 1,404 -- 3,143 745 271

• Samples were not collected at this station in July.

1

.i 4

l i

l I

Table 2.7.1 (Cb ntinued) Page 4 of 4 Neal Sub-Area Parr Rosarvoir Shoals impoundment h nticello Reservoir Station B C D P H I J K L M N O

~

OCTOBER Ta m nomic Category Bryo ma -

14 - -

Turbellaria - - - - 416 -- -- 373 - - - --

Nematoda 258 43 28 - -- 14 43 29 14 - - --

01Igochasta 28 258 646 258 10,042 330 258 1,148 991 1,190 661- 143 Hirudinea - -- - 14 - - -

Blvalvia 158 215 57 14 -

517 172 216 100 746 172 57 Diptera 731 400 157 457 5,752 1,248 716 658 458 257 413 658 Ephemeruptera -

273 43 - 402 115 129 -

28 187 28 -

.N Megaloptera -

14 29 - - - --

N Odonata - - - - 14 --

Tricho ptera 86 - -- -- -- -- 29 43 - -- --

29

- -- - - 14 -

Hydracarina - -- - -- - --

TOTAL 1,261 1,217 %0 74 3 16,626 2,224 1,347 2,467 1,591 2,380 1,288 887

Table 2.7.2 Summary of mean annual values for benthic macroinvertebrates obtained during the 1982 nonitoring program.

Neal Sub-Area Parr Reservoir Shoals impoundment b nticello Reservoir Station B C D P* H I J K L M N 1 Density Jan/Feb 1491 2004 1273 4205 7043 2235 1492 817 2551 1563 660 3687 May 4000 384 1205 1203 3716 400 2451 ~1392 4329 2009 1488 787 No/m2 July 502 674 1404 -

3143 745 271 1160 2296 2095 '2410 2137 Oct 1261 1217 960 743 16626 2224 1347 2467 1591 2380 1288 887 i

Mean Annual 1814 1070 1211 2050 7632 1401 1390 1459 2692 2012 1462 1875 Blomass Jan/Feb 68.16 3.92 54.19 5.72 0.72 9.93 19.79 22.78 4 5.80 73.58 8.82 20.28 May 398.43 3.69 23.80 0.78 0.42 0.07 31.55 10.65 54.78 186.64 30.98 50.69 g/m 2

July 41.47 2.06 17.13 -

0.13 21.20 5.00 33.66 103.91 210.51 41.43 71.33 Oct 33.64 16.16 13.61 0.16 1.06 90.46 59.50 39.71 30.16 93.89 31.83 22.71 Mean Annual 133.18 6.46 27.18 2.22 0.58 30.42 28.96 26.'s0 58.66 141.16 28.27 41.25 13 23 17 14 14 18 9 16 P Number Jan/Feb 6 20 21 19 21 10 17 6 13 10 w of Taxa May 12 10 10 14 10 12

,L July 6 4 8 -

5 11 7 10 7 8 11 9 12 12 15 18 13 15 16 13 00 Oct 10 18 10 11 Mean Annual 8.5 13,0 12.3 15.0 9.8 14.5 15.0 13.0 12.8 11.8 12.3 12.0 Mean Jan/Feb 1.41 2.62 3.70 3.01 1.93 3.67 3.25 3.27 2.33 3.25 2.80 2.93 Species May 1.56 2.98 2.56 2.99 2.58 2.88 3.04 1.78 2.17 0.99 1.87 2.52 Diversity (3) July 1.67 1.17 1.72 -- 1.47 2.82 2.17 1.83 1.98 1.94 1.75 1.98 Oct 2.59 3.36 2.46 3.22 1.41 2.86 3.62 3.00 2.56 2.46 2.84 3.10 Mean Annual 1.81 2.53 2.61 3.07 1.85 3.06 3.02 2.47 2.26 2.16 2.32 2.63 4

Equi ta- Jan/Feb 0.54 0.61 0.84 0.71 0.52 0.81 0.79 0.86 0.61 0.78 0.88 0.73 bility (e) May 0.44 0.90 0.77 0.78 0.78 0.80 0.69 0.54 0.53 0.38 0.50 0.76 July 0.65 0.59 0.57 -- 0.63 0.82 0.77 0.55 0.71 0.65 0.51 0.62 Oct 0.78 0.81 0.74 0.90 0.41 0.80 0.93 0.72 0.69 0.63 0.71 0.84 Mean Annual 0.60 0.73 0.73 0.80 0.59 0.81 0.80 0.67 0.64 0.61 0.65 0.74

" Samples were not collected at this station in July.

• 4

Tabl e 2.7.3 Summary of mean annual values for benthic macroinvertebrates obtained during nonlioring programs from 1978 through 1982.

Neal Sub-Area Parr Reservoir Shoals impoundment mnticello Reservoir Station B C D P H I J K L M N O Density 1978 407 354 384 286 347 255 920 458 124 76 257 143 1979 395 1724 1609 2087 3343 415 1750 1373 732 982 545 236 No/m 2

1980 871 1985 1630 1572 5833 640 1175 1228 %7 1034 1200 867 1981 882 1817 1204 1786 8201 917 1182 1770 2180 2084 1460 til5 r 1982 1814 1070 1211 2050 7632 1401 1390 145E 2692 2012 1462 1875 B lomass 1978 52.02 6.28 81.51 5.70 1.71 1.37 13.64 2.10 1.40 1.40 2.65 1.21 1979 3.92 2.75 11.71 0.32 0.34 0.05 0.20 0.06 0.43 2.69 0.04 0.02 g/m 2 1980 27.99 1.54 17.87 0.90 0.92 0.36 0.22 0.09 2.45 42.30 0.28 4.44 1981 44.49 12.78 26.94 0.89 1.26 1.39 4.43 10.67 37.% 6 8.84 7.94 6.48 1982 133.18 6.46 27.18 2.22 0.58 30.42 28.% 26.70 58.66 141.16 28.27 41.25 N Number 1978 10.0 13.7 14.6 7.3 8.0 6.0 9.0 9.7 5.7 5.0 8.3 6.0 11.3 11.3 9.5 10.5 11.5 9.8 7.5 L of Taxa 1979 5.0 16.8 15.0 13.2 16.3 16.5 13.5 19.0 11.2 10.0 10.5 9.5 8.2 10.2 12.2

. 8 1980 3.7 15.5 17.0 14.3 15.3 13.8 14.8 15.8 15.0 14.5 13.0 14.5 C 1981 6.5 11 5 14.5 15.0 13.0 12.8 11.8 12.3 12.0 1982 8.5 13.0 12.3 15.0 9.8 Mean Species 1978 2.49 2.73 3.05 1.90 1.84 1.53 1.58 2.26 1.77 1.81 2.13 1.49 Diversity 1979 1.37 3.07 2.70 2.77 2.59 3.02 2.34 2.37 2.55 2.79 2.66 2.45 1980 0.% 2.54 2.56 3.16 2.98 2.81 2.46 2.36 2.18 1.70 2.13 2.72 1981 1.31 1.99 3.35 2.61 2.15 2.79 2.76 2.75 2.88 2.58 2.61 2.86 1982 1.81 2.53 2.61 3.07 1.85 3.06 3.02 2.47 2.26 2.16 2.32 2.63 Equita- 1978 0.76 0.78 0.79 0.65 0.60 0.61 0.50 0.74 0.57 0.85 0.73 0.58 bliIty 1979 0.65 0.76 0.69 0.69 0.70 0.91 0.72 0.69 0.76 0.80 0.89 0.86 1980 0.50 0.65 0.69 0.78 0.70 0.82 0.77 0.71 0.70 0.58 0.67 0.75 1981 0.48 0.58 0.83 0.69 0.54 0.78 0.72 0.69 0.74 0.67 0.71 0.77 1982 0.60 0.73 0.73 0.80 0.59 0.81 0.80 0.67 0.64 0.61 0.65 0.74

2.8 FISH-2.8.1 Introduction Fish are important and visible components of the aquatic ecosystem.

Fish rank high as a source of foed and recreation 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 their sensitivity to changes in their environment, many species nay be useful indicators of stress in the aquatic ecosystem.

%e purpose of this investigation was to characterize the fish com-munity in the water bodies of the study area according to: species

. composition and relative abundance, standing crop, diet, growth, condition factor, and age distribution. Relative abundance for a species was expressed as the percent of the total annual fish catch-from al.1. of the stations in a particular reservoir.

Mean condition factors -and fish lengths at annulus formation were calculated - for dominant species (those that comprised five percent or more of the total 1982 catch) . The condition factor (K) is a means of comparing the relative well being of a fish. The heavier a fish is for

( a given length, the larger the factor and, by implication, the better the " condition" of the fish. The factor is expressed in the form K =

W x 105 fg3 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.

For growth determinations the scale (spine in catfish) radius and fish length data were fitted by linear regression using log-transformed (log 10) data. The Monastyrsky method of back calculation (Lagler, l 1969) was used to estimate total body length at each annulus. The formula for the back-calculation of lengths using the Monastyrsky method is L = bSS where L represents the total length of the fish in 2.8-1 l

, - - . , - , . - , . , - - , - _ - - - .,_ ,,c.,-,,,... . . _ - . . - , ..

mm and S represents the scale (or spine) radius; m and b are constants derived from the data.

2.8.2 Findings and Discussion A total of 35 species were collected from all the stations during the 1982 sampling periods, utilizing gill nets and a boom electrofisher.

The most numerous group of fish collected from all impoundments was the centrarchid family (sunfish), which was represented by several species, among them bluegill, largemouth bass, and crappie. The next most abundant group was the clupeid (shad) family, represented exclusively by one species, gizzard shad, which occurred in all the impoundments.

Ictalurids (cattish), cyprinids (minnows), and catastomids (suckers) were found in all of the impoundments in varying degrees of abundance.

Species composition of 1982 collections was similar to observations in previous years (Dames & Moore; 1978, 1979, 1979a, 1980, 1981), with minor exceptions. A bowfin captured at Neal Shoals Dam was the first collected from any of the sampling stations. A tesselated darter, last collected in 1978, reappeared in Parr Reservoir samples; this darter was found at Station M in Monticello Reservoir in 1981, however.

A detailed description of the adult fish investigation follows and is presented by water body. Species composition, relative abundance, condition factors, growth, diet, and age distribution are described for the combined 1982 sampling periods.

i Parr Reservoir Species Composition and Relative Abundance. A total of 29 species were collected in Parr Reservoir with gill nets and a boom electrofisher (Table 2.8.1). During 1982, the centrarchid (sunfish) family was the dominant group. It-made up 53 percent of the total catch and was represented by nine species, of which the bluegill (28 percent) was

(

2.8-2

.y-i most numerous. The next most abundant group was the clupeid (shad) family. This group comprised 30 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:

six members of the catostomid (sucker) family, b percent; five members of the ictalurid (catfish) family, 5 percent; four members of the cyprinid (minnow) family, 3 percent; and one member of the lepisosteid (gar) family, 2 percent. Whitefin shiner and white bass, waich were first collected.from Parr Reservoir in 1981, were again present in i

small numbers in 1982.

The fish composition of Parr Reservoir has changed little since 1978 (Table 2.8.2). Of 34 species collected since 1978, 19 have been cap-tured in at least 4 of the 5 sampling years. Species at apparently low population levels, including shorthead redhorse, yellow bullhead, and flat bullhead, were infrequently collected. Three species -- creek chubsucker, tadpole madtom, and swamp darter -- have not been collected since 1978. Three other species -- snail bullhead, flier, and tesse-lated darter -- had not been collected since 1978 but appeared in 1982 s ample s. All three of these species are present in Monticello Reser-voir (Table 2.8.2) and their occurrence in Parr Reservoir suggests movement through the penstocks of the FPSF.

Condition Factors and Growth. Condition factors and lengths at annulus formation (based on the Monastyrsky method) for gizzard shad, bluegill, and largemouth bass were:

Mean Mean Length (mm) at Condition Annulus Formation

. Species Factor 1 2 3 4 5 6 7 Gizzard shad 0.847 106 176 215 251 270 Bluegill 1.675 51 95 122 147 185 -

Largemouth bass 1.424 93 177 238 311 369 440 426 2.8-3

Gizzard shad in Parr Reservoir exhibited slightly slower growth than gizzard shad from other southeastern waters (Carlander,1969). The gizzard shad condition factor was lower than that reported by Jester and Jensen (1971) and Carlander (1969) for other southern populations.

In general, bluegill growth in Parr Reservoir was slower than bluegill growth in other southeastern reservoirs (Carlander,1977). The condi-tion factor of bluegill was average when compared to data from other bluegill populations (Carlander,1977). For the average largemouth bass from rarr Reservoir, recruitment into the sport fishery, at ap-proximately 305 mm (12 in, body length), occurred during the fourth year of life. Growth of Parr Reservoir largemouth bass appeared to be slower than that seen in other southeastern populations (Carlander, 1977). The mean condition factor was average when compared to other largemouth bass populations in the southeast (Carlander,1977). The bluegill stomachs contained mostly larval insect remains, although there were some fish remains found. The largemouth bass stomachs contained primarily fish remains.

Standing Crop Estimate. The standing crop is the weight of fish pre-sent in a body of water at any given time. Standing crop estimates at Station C were made by block netting .an area of 0.13 ha (hectare) and

. applying liquid rotenone. The results are shown in Table 2.8.3. A total of 19.0 kg/ha of fish, represented by seven species, were ob-tained at' this cove in 1982, as compared to 142.8 kg/ha and 17 species in 1978; 11.3 kg/ha and 4 species in 1979; 54.9 kg/ha and 15 species in 1980; and 5.3 kg/ha, and 3 species in 1981 (Dames & Moore; 1978, 1979, 1979a, 1980, 1981). Largemouth bass and gizzard shad accounted for the greatest biomass, with 8.1 and 6.1 kg/ha, respectively. The Parr Res-ervoir standing crop estimate was much higher than that obtained in 1981, and was more comparable with estimates from previous years.

l 2.8-4

Neal Shoals Dam Species Composition and Relative Abundance. A total of 16 fish species were collected from Neal Shoals Dam with an electrofisher during 1982 (Table 2.8.1). The centrarchid family was the dominant group numer-ically, making up 72 percent of all fish collected. Six centrarchid species were captured, with bluegill most abundant (31 percent of the total catch) . 'Ihe clupeid family, represented only by gizzard shad, was the second most numerous group (13 percent of the total catch) .

The species composition of fish collections from Neal Shoals Dam has generally been cor.sistent since 1978 (Table 2.8.2). Of 26 species collected from Neal Shoals,12 have been captured in at least four of the last five years. A number of species - shorthead redhorse, creek chubsucker, white catfish, and pumpkinseed -- have been collected infrequently. Others, including silver redhorse, yellow bullhead, black bullhead, mosquitofish, and yellow perch, have not been collected since 1978. A single bowfin, a species native to the Broad River drainage but never before collected in this study, was captured in 1982.

a Condition Factors and Growth. Condition factors and mean fish lengths at annulus formation for dominant species in the 1982 collection are presented below:

Mean Mean Length (mm) at Condition Annulus Formation Species Factor 1 2 3 4 5 6 l

! Gizzard shad 0.897 131 188 200 243

, Bluegill 1.782 44 85 114 135 137 l Redear sunfish 1.636 45 89 125 150 159 173 l

Black crappie 1.198 63 109 143 174 193 253 l

l l

l 2.8-5

4

. Growth of Neal Shoals bluegill was slow. Typically, bluegill- from the i

southeast reach a harvestable size of 152 mm (6 in) by their fourth growing season (Carlander,1977), but the average bluegill from Neal j Shoals Dam will not reach a harvestable size until-its sixth or seventh

- growing season. Growth .of gizzard shad was also slow compared to other populations in the southeast (Carlander,1969). The condition factor of gizzard shad was comparable to those reported by Jester and Jensen (1971). The bluegill condition factor was average when compared to i other southeastern populations (Carlander,1977). Growth and condition factors of black crappie were poor when compared to crappie from similar habitats (Carlander,1977). Growth of redear sunfish was poor, but condition factor average, when compared to redear from other areas

. of the southeast (Carlander, .1977).

The bluegill fed primarily on insect larvae. The stomachs of the redear sunfish contained inorganic and organic debris. The black I crappie stomachs examined contained a wide variety of food materials j

including fish, organic materials, insect parts and plant remains.

j Standing Crop Estimate. The standing crop estimates from Neal Shoals were made by block' netting an area of 0.12 ha and applying rotenone. A

complete kill was assumed and results are presented in Table 2.8.3. A 1-total of 10.5 kg/ha of fish were obtained, represented by four species.

Gizzard shad made up the bulk of the biomass (7.9 kg/ha). S tanding crop estimates were considerably lower than those obtained in previous years (Dames & Moore; 1978, 1979, 1979a, 1980, 1981). The low biomass and species diversity observed at Station P may have resulted from the complete draining of the study area by SCE&G during July, August, and part of September 1982. Recolonization by fishes was probably not yet complete at the time of the rotenone application. ,

2.8-6 I

~ . . - , . - , _ , , _ ~ . , . . . - - . _ _ , . - . . . _ . _ . - _ . _ . . . _ . . --.m... ,. ,..-. ,__... ......_., . . . _ , - _ _ _ - - . . - - , -_-

Subimpoundment Species Composition and Relative Abundance. A total of eleven species were collected with gill nets and electrofisher in the subimpoundment

, during the 1982 collecting periods (Table 2.8.1). The centrarchid family, which ccmprised 82 percent of all fish collected, was the dominant group. This family was represented by seven species, bluegill being most abundant (56 percent of all fich collected).

The clupeid family, represented by gizzard shad, was second in number; it made up some 12 percent of the fish collected. Brown bullhead, of the ictalurid family, ranked third in abundance (6 percent of total).

Eleven of 20 species collected in the subimpoundment since 1978 have been captured in at least four of five collecting years (Table 2.8.2).

Black crappie, white crappie, black bullhead, and silvery minnow have been collected infrequently and are probably at low population levels.

Three species -- redfin pickerel, lake chubsucker, and white catfish --

have not been collected since 1978.

Condition Factors and Growth. Mean condition factors and mean fish lengths at annulus formation (Monastyrsky method) for the dominant species in the 1982 collections are presented below:

Mean Mean Length (mm) at I

Condition Annulus Formation

! Species Factor 1 2 3 4 5 6 Gizzard shad 0.975 238 286 286 308 Bluegill 1.657 43 100 129 146 173 Largemouth bass 1.340 99 199 271 334 Growth of gizzard shad was faster than that descr bed by Carlander (1969) and Jester and Jensea (1971) for U.S. populations in southern latitudes. The growth pattern vf bluegill in the subimpoundment was similar to that of bluegill in Parr Reservoir, with fish reaching harvestable size 152 mm (6 in.) in their fourth or fif th growing season. Bluegill growth in the subimpoundment appeared to be slower than bluegill growth in other southeastern lakes and reservoirs 2.8-7

- ( Carlander , 1977) . The mean condition factor for subimpoundment bluegill was similar to that of Parr Reservoir bluegill and was within the range of values for bluegill from similar habitats (Carlander, 1977). The stomach contents of the bluegill consisted of organic material and larval insect pieces.

No largemouth bass older than age four was collected from the sub-impoundment in 1982. Growth of largemouth bass was more rapid than that seen in previous years, with fish reaching a harvestable size 305 mm (12 in.) by their fourth growing season. The mean condition factor of largemouth bass was also higher than in previous years, and was typical of other southern populations (Carlander,1977). The diet of the largemouth bass consisted primarily of fish, i

The higher condition factor for gizzard shad may be attributed to the fertilization program being carried out by the South Carolina Wildlife and Marine Resources Department. Primary productivity is increased in the subimpoundment as a result of the added nutrients; this has a direct affect on the gizzard shad since they are primarily plankti-vorous filter feeders.

Monticello Reservoir f

Species Composition and Relative Abundance. A total of 29 species were collected from Monticello Reservoir, using gill nets and a boom elec-trofisher during the 1982 sampling periods (Table 2.8.1). For all stations and collecting periods the centrarchid family was the dominant group; it was represented by nine species and comprised 45 percent of the fish captured. Bluegill was the most abundant centrarchid species ,

making up 33 percent of the fish captured. The clupeid family, repre-sented by gizzard shad (39 percent) was the second most abundant group.

Other groups collected, along with percent of total catch, included:

f six members of the ictalurid (catfish) family, 9 percent; six members of the catastomid (sucker) family, 5 percent; and four members of the .

cyprinid (minnow) family, 2 percent. Percids (yellow perch) and 2.8-8 l

l e -- . - . _ - , .---7, . - , , - - - , , - - , - , . ,. ,----, - ~.---

percichthyids (white bass) were present in low numbers, each less than 1 percent of the total.

The fish composition of Monticello Reservoir has changed little since 1978 (Table 2.8.2). Of 38 species collected since 1978, 24 have been captured in at least four or five sampling years. Redfin pickerel and longear sunfish have not been collected from the reservoir since 1978.

Three species -- lake chubsucker, green sunfish, and the margined madtom were found only in 1979. A number of other species including shorthead redhorse, yellow perch, tesselated darter, and sandbar shiner were infrequently collected.

Condition Factors and Growth. Condition factors and lengths at annulus formation (based on the Moc9s yrsky method) for gizzard shad, bluegill, and largemouth bass were:

Mean Mean Length (mm) at Condition Annulus Formation Species Factor 1 2 3 4 5 _ 6_, 7 Gizzard shad 0.791 120 190 235 258 309 Bluegill 1.627 44 86 114 150 155 151 Largemouth bass 1.424 89 174 238 277 315 319 270 Growth of Monticello Reservoir gizzard shad was slow relative to other southeastern populations (Carlander,1969), but comparable to gizzard I

j shad growth in Parr Reservoir and Neal Shoals. The mean condition factor of gizzard shad was low compared to gizzard shad in other south-l eastern reservoirs (Carlander, 1969), and lower than that recorded for Parr Reservoir, Neal Shoals, and the subimpoundment. The diet of the gizzard shad consisted of organic and inorganic material. Bluegill growth rates were similar to those in Parr Reservoir and are slightly lower than the southeastern average (Carlander, 1977). The bluegill's l diet consisted primarily of insects and plants; some of the stomachs examined contained fish remains. Largemouth bass growth was relatively slow, with the average fish being recruited into the sport fishery in 1

i its fifth year of life. The mean condition factor of Monticello 2.8-9 l

Reservoir largemouth bass was average when compared to other southeastern populations (Carlander,1977) . The diet of the largemouth bass consisted of fish.

Standing _ Crop Estimate. Standing crop estimates from coves near Stations I and K were made by block netting areas of 0.13 ha (I) and 0.11 ha (K) and applying rotenone; a complete kill was assumed.

Results are present in Table 2.8.3. A total of 79.6 kg/ha was obtained at the cove near Station I and 78.7 kg/ha at the cove near Station K.

Gizzard shad, channel catfish, and bluegill ranked first, second, and third in biomass at both stations; at Station K, white catfish also ranked third in biomass with the bluegill.

Standing crop estimates for 1982 were considerably higher than those obtained in 1981, and approached those of 1978, when Stations I and K produced 83.5 and 84.5 kg/ha, respectively. The 1982 data suggest that fish were using the littoral zone more than in previous years (Dames &

Moore; 1978, 1979, 1979a, 1980, 1981).

Summary I

The fish community of Parr Reservoir was primarily composed of centrar-chids and gizzard shad. Gizzard shad was the-most abundant species, l

with bluegill second in number. Five year classes of gizzard shad were l found, but most fish were either two or three years old. Five year classes of bluegill were also captured, with most of the fish from one

! to four years of age. Growth of both species, determined from back-calculated lengths, was slightly slower than other populations in the southeast. There is some evidence of parasites in the 1-2 year age classes of bream populations in Parr Reservoir. This has been noticed during the past few years and is particularly noticeable in the smaller (30-50 mm length) size classes.

2.8-10 1

I i

The fish data from Neal Shoals Dam indicated that centrarchids and clupeids (gizzard shad) were the numerically dominant groups. Bluegill were the most abundant of six centrarchid species. Gizzard shad was the second most abundant species. Four year classes of gizzard shad and five year classes of bluegill were represented in samples. Growth of both species was slower than that reported for other southeastern populations. -

The fish community of the subimpoundment was dominated by centrarchid species and gizzard shad. Bluegill was the most numerous of seven centrarchid species collected. Four year classes of gizzard shad and five year classes of bluegill were found. Gizzard shad grew faster

1. than shad in other southeastern impoundments, and bluegill growth was relatively slow. Largemouth bass growth appeared to be more rapid than in previous years of the study.

The fish community in Monticello Reservoir was also comprised primarily of centrarchids and gizzard shad. Nine centrarchid species were collected and bluegill was the most numerous. Bluegill ranked second to gizzard shad in abundance. Five gizzard shad year classes were found, with two and three year old fish most numerous by far. Six bluegill year classes were present, but most fish were one to four years old. Growth of both species was slower than that reported for other southeastern populations.

l I

i l

r 2.8-11

- - - - - - - - - - a n ----g., ,-,----,-en-- - - - - - - - - > - . - - - - < - - - - - - - - - - - - - , , , , , -

I Table 2.8.1 Numbers of fish and their percent abundance'(%), collected by electrofisher and gill nets during the 1982 sampling program.  ;

i Pge l of 4 i Neal. Sub-Area Parr Reservoir' Shoals impoundment M>ntIcello Reserw)ir Stat ion B C D . P H I J K L M N O-Conanon Name Scientific Name

{ Gar Lepisosteldae 5 7 12 (0.14) 1 j Longnose gar Lepisosteus osseus (5) (1.6) (2.0) (4.3)

) Llowfin Ami ldae 1

Dowlin Amia calva (%) -(0.4) i j Shad Cl upeidae 121 76 91 30 67 158 232 110 83 547 4 58 1 10 i Gizzard shad (brosoma cepedianum (%) (37.8) (21.2) (32.3) (13.2) (11.5) (34.2) (52.8) (33.3)' (12.0) ( 51.4) 869.2) (15.0) i Minnows Cyprinidae 5 5 4 2 4 1 i Carp Cyprinus carpio ($) (1.4) (1.8) (1.8) (0.46) (0.38) (0.14) l Silvery minnow Hybonnathus nuchalls 3 2 1 7 i

(%) (1.3) (0.4) (0.30) ( 0.% )

4.

!ct -Golden shiner tbtemigonus crysoleucas 1 6 13 2 1 1 1 j) (%) (0.3) (1.7) (5.7) (0.3) (0.30) (0.09) (0.14) ,

M: Whitefin shiner Notropis niveus 4 24 ' 2 5 1 4 8 2 *

(%) (1.3) (5.205 *0.46) (1.52) (0.15) (0.38) (1.21) (0.27) i j Spottail shiner hudsonius 4

-N.

i

(%) (1.3) l Sucker Catostomidae 2 9 14 3 13 12 40 2 39 26 12 Quillback carp- Carpiodes cyprinus (%) (0.6) (2.5) (5.0) ( 1.3) , (2.81) (2.73) (12.1) (0.30) (3.66) (3.9) _ (1.64)

sucker i

i River corpsucker -C. carpio 3 1 1 l (%) (0.8) (0.4) (0.09)

I 2 i Highfin carpsucker -C. velifer 5

(%) (1.8) (0.19)

)

1 .

1 i

i l

4 I

I

(Continued) - Page 2 of 4 '

Table 2.8.1 Neal Sutr Area Parr Reservoir Shoals impoundment M>nticello Reserwolr Stat ion B C D P H I J K L M N O' Common Name Scientific Name M)w>stoma anisurum 5 4 5 45 11 2 Silver redhorse

($) (1.6) (1.4) (1.14) (4.23) (1.66) (0.27) macrclepidotum 2 2 Shorthead redhorse -M. (0.19)

(J) (0.6)

Creek chubsucker Frlmyaon oblongus 1 1 2 1

(%) (0.4) (0.2) (0.43) (0.2)

Laks chubsucker -E. succeta 1 (5) (0.3)

Catfish letaluridae Catfish, unknown 1

($) (0.3) 34 15 14 45 27 8 20 White catfish letalurus catus 12 10 1 (7.36) (3.42) (4.24) (6.52) (2.54)- (1.21) (2.73);

(5) (3.7) (2.8) (0.4)

• 1 i 1 3 co Yellow bullhead -I. natalls (0.23) (0.14 5) (0.09) (0.41)

($)

4 3 6 32 23 2 7 1 14 I 1 Brown bullhead -I. nebulosus 1

(%) (0.3) (1.1) (1.1) (2.6) (5.5) (4.98) (0.46) (2.12) (0.15) (1.32) .'(0.15) (0.14) l 5 8 6 7 5 5 20 8 9 Chann;si catfish -I. punctatus 1 1

(%) (0.3) (1.4) (2.8) (0.4) (1.30) (1.60) (1.52) (0.73) (1.88) (1.21) (1.23) n Flat bullhead 1. platycephalus (5) (0 3) (0 4) (1 16) ( 03) (1 51)

Snalt bullhead I. brunneus 2

{g) {o 6) (0 22) (0 23) (0 30)  ! 70) ( 35) (178)i

i (Continued)

Page 3 of 4 Trble 2.8.1 Neal Sub-Area Parr Reservoir Shoals impoundment k nticello Reserwir Station B C D P H I J K L M N O Comnon Name Scientific Name Temperate bass Percichthyldae mrone chrysops 10 1 I I 2 22 2 White bass 1

(%) (3.1) (0.41 (0.22) (0.23) (0.30) (0.29) (2.07) (0.30)

Sunfish Centrarchidae Centrarchus macropterus 1 I 2 1 Flier (5) (0.3) (0.15) (0.19) (0.151 7 1 4 19 6 2 9 Redbreast Lepomis auritus 14 1

(%) (4.41 (0.4) (l.2) (0.22) (0.91) (2.75) (0.56) (0.30) (l.23[

." 20 2 6 32 18 17 3 16 gulosus 2 1

? Warnuuth L_.

(3.4) (0.43) (1.37) (9.70) (2.61) (1.57) (0.45) (2.19{

g (%) (0.6) (0.4) 89 326 108 104 66 382 212 91 486 Blusgill L. macrochirus 58 125 71

(%) (18.1) (34.9) (31.1) (31.1) (55.8) (23.4) (23.7) (20.0) (55.4) (19.2) (13.75) (66.4)

Lepomis 1 I I I 1 Hybrid sunfish (5) (0.4) (0.22) (0.15) (0.09) (0.141 L. gibbosus 20 43 15 25 19 12 25 17 12 12 6 Pumpkinseed (5) (6.3) (12.0) (5.3) (4.3) (4.11) (2.73) (7.58) (2.46) (1.13) (1.81) (0.82) 4 21 6 44 2 1 2 7 3 8 4 3 Redear sunfish L. microlophus (5.9) (0.3) (0.22) (0.46) (2.12) (0.44) (0.7 5) (0.60) (0.41)

(%) (1.3) (2.1) (19.3) 39 22 15 5 99 54 29 15 38 41 16 28 Largennuth bass Micropterus sainnides (5) (12.2) (6.1) (5.3) (2.2) (17.0) (11.7) (6.61) (4.55) (5.51) (3.85) (2.42) (3.83>

Table 2.8.1 (Cont inued ) ' Page 4 of 4' Neal 'Sub-Area Parr Reserwolr- Shoals impoundment mnticello Reserwir Station B C D P H I J K L M N _1 Conson Name Scientific Name White crapple Fbnoxis annularis 6 14 3 10

(%) (3.9) (1.1) (4.4) ,

Black crapple P. nigromaculatus 8 2 5 34 3 5 3 1 1 (5) (2.5) (0.6) .(1.8) (14.9) (0.5) (1.08) ( 0.44 ) (0.09) (0.14)

Perch Percidae Yetlow perch Perca fIavescens 1 3 6 2

(%) (0.3) (0.8) (1.30) (0.46)

Tessellated darter Etheostoma olmstedi 3

1. (%) (1.0)

I t

4 1

4 1

1

[

1 i.

.-.T

_ . __ __ _ _ _ _ . - _ . _ _ . . _ _ ~ . . - _ _ . _ _. __ . . - - m , ,

Table 2.8.2 Fish species collected in 1978, 1979, 1980, 1981, and 1982. . Page .1 of 3 i Parr M>nticello Area Reservoir Neal Shoals Dam Subispoundment Reservoir

<J Year 78 79 80 81 82 78 79 80 81 82 78 79 80 81 82 78 79 80 81 82 I Common Name Scientific Name

't Gar Lepisosteidae Longnose gar Lepisosteus osseus x x x x x x x x x i Bowfin AmiIdae Dowfin Amia calva x Shad Clupeldae Gizzard shad Dorosoma cepedianum x x x x x x x x x x x x x x x .x x x x x 1 Pickerel Esocidae Redfin pickerel Esox americanus x x i

j Mi nnows Cyprinidae

Carp Cyprinus carpio x x x x x x x x x x x x x x w

j

• Silvery minnow Hybognathus nuchalls x x x x x x x x x x x x x

! 8 Golden shiner Notomigonus crysoleucas x x x x x x x x x x x x x x x x x x x x l g i x i Whitefin shiner tbtropis niveus x x x x I

i Sandbar shiner N. scepticus x Spo tta ll shiner hud so ni us x l

N_.

i Sucker Catostomidae 1 Quillback carp- Carplodes cyprinus x x x x x x x x x- x j sucker i x x j River carpsucker C. carpio x x x x x x x x x x 1

Hightin carpsucker x x x x x x x j C_. vellfer i

Silver rudturse ibxostoma anisurum x x x x x x x x x x x j

l x x Shorthead redhor se M. macrolepidotum x x x x x t j

I Lake chubsucker Erimyzon sucetta x x x x Creek chubsucker E. oblongus x x x x x x x x x x x x 4

i o -

1 f I

l 2 x x x x x x x x x x x x x x 8

3 1 x x x x x x x x x x x x x x f lori 8

_ o lev o 2 cr 0 x .x x x x x x x x x x x x ie 8 a ts g ne a oR x x x x x x P M 9 7

x x x x x x x x x x 8 x x x x x x x x x x x x x x 7

2 x x x x x x 8

t x x n 1 x x x x x x e 8 m

d n x u 0 x x x x x x x o

p 8

s i

b 9 x x x x x x x x u 7 S

8 x x x x x x x x x x 7

2 x x x x x x 3

m a x x x x D 1 8

. l s

a x x x x o 0 x x x h 8 S

l a 9 x x x x x x e 7 N

8 x x x x x x x x x x 7

2 x x x x x x x x x x x x

_. 8 1 x x x x x x x x x 8

r i

ro rv 0 x x x x x x x x ar 8 Pe

, s e x x x x x R 9 7

x x x x x 8 x x x x x x x x x x x x x 7

s u

r e

t p

o r

s s s s u i i s c s e u l n n p a u s s m t a g i e os m t u u a a s s h i f a e i r h p

s s u

- N c u u p s s f d y as r i s i .

e s s t e u n s a l r du u s h u o t l p c as i o a c e i u e y h ih a u c s l o l e

s i

du l l t y n s n aa h c hc s o o o r

l a n s f i r a u c t n a s i di t cr s o r b g a i ru t b n a u t u r i s h e ra i l c b c i t ul a e u r e r y l u c n ar m u a ig i e y m a lp u o g m m m c o n

c ro n n p b m g ib i rt ie lat t cm

. ea r o t n ne p

e . . . . . e p

) t c . . o .

L_

d e S c lei 1 1 1 1 I 1 N N P

oG P

e M C

eC L L L L L L L u

n i

t n h o d h m C

( h a

e ad i s

d d

a a d

t o mo s h

s i s

h h

s s h e f a e

e eh d a

t h s

s a

i f n i s i f

i l h t h d a B s 4 f n u n

_ 2 o f l l a h l l m ri t e u s f

n u m t u l c l l l m ef s t 8 a a c

b u l u

u u d e e ro et a b s a

h l s s r

u s

s 2

H h w b l e b b b n l at ei a h e t

u ig ni r a l

d se o n n o bu r ot srie r o k a e gn e

n o it l w n t l

i k

c ig p q e i b n r

e u

p e n

e ibr e

a a na r e p m d ih fi l o a d fl d l

b m th e r h l l a a v m h nI e a l B

u e oL r G H y

a o aW Y B C F S O M T e W uF R W P R T C C L T S N.0 0

~4 4 ;i ] *  ! ,4 fijII{Il!,#i1l!jjijl i:1f ,1jjiik4 1

1 I

j Table 2.8.2 (Continued) Pag ^s 3 of 3 Parr Mont Icel lo .

Reservoir Neal Shoals Dan Subispoundment Reservoir

]8, ]!, E E E 3 )), E 8,,,1,, ,8,2, H H E E p2,, H ]?,.. g g . 32,, .

Comnon Name Scientific Name i

j Larg(mouth bass Micropterus salnoldes x x x x x x x x x x x x x x x x x x .x- -x

! White crappie Fbnoxis annularis x x x v x x x x x x x x x x l Black crapple P. nigromaculatus x x x x x x x x x x x x x x x x x Percidae Percidae

Yellow perch Perca flavescens x x x x x i

. Swamp darter Etheostoma f usiforme x I

l Tessol lstud darter _E. o l msted i _x _ _ _ _x _ _ _ _ ____ _ ___ _ _x _

! To tal Number of Species 28 22 20 22 29 19 14 16 12 16 15 13 13 13 11 27 31 25 30 29 I

i ro ,

e l' 1 i

.i r

i 1

i f

i

)

1 i

i f

4 1

1 1

f

Table 2.8.3 Standing crop (kg/ha) estimates of fishes from Parr and Monticello Reservoirs and the Neal Shoals Dam,1982a, Monticello Neal Reservoir Parr Reservoir Shoals Stations I K C P Common Name Gizzard shad 30.7 56.0 6.1 7.9 Whitefin shiner 0.02 1.1 Spottail shiner 0.4 Shorthead redhorse 0.5 White catfish 0.8 3.7 Yellow bullhead 0.2 Brown bullhead 1.0 2.7 Channel catfish 19.2 11.4 Flat bullhead 0.9 0.04 Snail bullhead 0.3 0.06 White bass 0.5 Warmouth 0.7 Bluegill 16.7 3.7 0.5 1.0 Pumpkinseed 0.3 1.5 1.3 Redear sunfich 1.2 0.1 Largemouth bass 2.8 0.2 8.1 Black crappie 3.3 0.2 0.7 Yellow perch 1.0 0.9 Swamp darter 0.01 Tesselated darter 0.02 l Piedmont darter 0.04 Tota 19 79.6 78.7 19.0 10.5 a Fish collections made by rotenone in a 0.13 ha area.

l l

l 2.8-19

3.0 TERRESTRIAL SURVEY 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 very little change occurred in land use patterns from April 1981 to May 1982. Only three areas (Numbered 1-3) within the study area evidenced changes in vegetative cover (Figure 3.1.1). The lettered areas (A-G) represent land use changes prior to 1981. The largest affected area was located on the western shore of Lake Monticello south of the recreation area dam (Area 1, Figure 3.1.1). This approximately 80 acre area was selectively cut, a common timber management practice in the southeastern United States. Trees suitable for use as timber are removed while smaller trees are not disturbed. This practice results in a more open canopy and allows the development of a brushy understory which becomes good wildlife habi-tat.

The other areas in which changes in vegetative cover had occurred were much smaller in size than Area 1. Area 2 (Figure 3.1.1) consisted of I

approximately 4 acres which was cleared and planted by the South Carolina Department of Wildlife to provide food for the Canada geese that were introduced by this agency.

j The third area (Area 3, Figure 3.1.1) is about 10 acres in size and was cleared for the construction of the nuclear training facility. P Construction of the facility was completed by December 1982.

A comparison of the 1982 photographs with those taken in earlier years l

f did not indicate any change in or loss of vigor by the vegetation.

1 t

3.1-1

\A \ \

/ w ,

g = ..... =

g3g/

s

/ \x  :

't./ e -

g-d i D, g%\q

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f2

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n k%  ! 4(

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GGO t i D s , t suuren 1 '

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wariom rentsr --

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i \ b c ~o g i

c.,<. q'h, i- a

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k;i 'Q

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m * = c.,  % ,/ V

' 0"h'.' !?.""l",,

/

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1

$ / i C' .....

a\j\ m Q

p.~,r,g a 'rar=o Q CLEARCUT AREAS 3

g I( y settetivE CUT AREAS Figure 3.1-1. Land Modification in Study Area from 1981 to 1982.

3.2 BIRDS 3.2.1 Avian Auto Survey 3.2.1.1 Introduction 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 was located around the perimeter of Monticello Reservoir, near the areas of influence of the generating facilities (Routes ABC = Test Route), while the other was located away from this area (Route D =

Control Route). The land use along the two routes was superficially similar with approximately equal amounts of wooded versus open land occurring on the routes. Route D is more urbanized than Routes ABC and numerous single-family houses occur along the route; therefore 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 summer survey was timed to coincide with the U.S. Fish and Wildlife Service's Game Bicd Call Count. All birds seen or heard at designated stops were counted; a separate count of bobwhite and mourning dove was made for the Game Bird Call Count during the summer survey.

3.2.1.2 Findings and Discussion A list of species observed in the summer and winter auto surveys is presented in Tables 3.2.1 and 3.2.2. The numbers of birds along both the control and test routes were quite similar to those recorded in 1981 (Figure 3.2.2 ). An average of 7.5 birds per stop per day was recorded on the test route in 1982 as compared to 8.4 birds per stop per day in 1981. The control route averaged 6.4 birds per stop per day in 1982 as compared to 5.4 in 1981. As has been noted since 1973 there were more birds along the test route than along the control route.

3.2-1

Standard X2 calculations on the number of individuals of certain indicator species were performed to determine if the observed

~

differences on the two routes were significant. The indicator species which were abundant enough to allow these calculations to be performed were the mockingbird, eastern meadowlark, cardinal, chickadee, pine warbler, rufous-sided towhee,.and mourning dove. Three of the X2 values indicated that the meadowlark, towhee, and chickadee were significantly more abundant (at the 5 percent level) on the test route than on the control in the summer. The X2 values for the other species were not. significant at the 5 percent level; however, except for cardinals in the summer, there were more individuals observed along the test route than along_the control route.

A similar relationship between the test and control routes was observed during the winter survey. The test route averaged 24.0 birds per stop per day w'hile the. control route averaged 18.2. These numbers are substantially higher than observed during the summer survey and occur because.of the large numbers of migrant birds present during the winter. Large, mono-specific flocks of such species as red-winged blackbirds and cedar waxwings are common and tend to greatly inflate the number of birds observed.

The indicator species which were present in sufficient numbers to allow aX2 analysis to be conducted included mockingbirds, meadowlarks, cardinals, pine warblers, rufous-sided towhees, and chickadees. Only the X2 for meadowlarks was significant (at the 5 percent level) and indicated that more meadowlarks occurred along the test route than the control. ' Although the other X2 tests were not significant, in all cases the number of individuals observed along the test route exceeded the number along the control route.

Nineteen 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 recorded along the control route (Figure 3.2.3). A comparison of the 1982 data with historical information from 3.2-2

previous years indicates that the bobwhite populations along both routes have remained fairly stable since 1977. However, for the first time more bobwhite were recorded along the control route than along the test route. This small difference in numbers, however, indicates that within the study area the habitats are similar and are approaching the same degree of suitability for quail.

More mourning doves were recorded along the two routes than in previous years during the Game Bird Call Count (Figure 3.2.3). Seventeen mourn-ing doves were recorded along the test route while nine were recorded along the control route. Since 1977 the test route has consistently had higher numbers of mourning doves than the control route. There are more areas of open fields and fewer houses along the test route and the habitat is much more suitable fer doves.

3.2.2 Waterfowl Survey 3.2.2.1 Introduction Waterfowl surveys were conducted on bbaticello Reservoir and on Parr Reservoir and its tributaries, the tailrace canal and Cannons Creek.

Observations were made of all ducks and other waterfowl, wading birds, t and shorebirds which utilized these areas during the winter, summer, l and fall seasons of 1982.

3.2.2.2 Findings and Discussion t

The waterfowl observed during the 1982 surveys are listed in Table 3.2.3. The summer waterfowl survey was performed to document the occurrence of resident species of waterfowl and shorebirds. The fall and winter surveys documented the occurrence of migratory waterfowl using the aquatic habitats of the study area as temporary resting and feeding areas.

3.2-3

Ducks were fairly abundant in Parr Reservoir and the tailrace canal during the fall survey. Mallards and blue-winged teal accounted for over 80 percent of all individuals seen. The great blue heron was by far the most common wading bird seen, with at least 48 individuals being observed in Parr Reservoir and its tributaries during the fall survey. A flock of ever 100 Canada geese was also present in the Can-nons Creek section of the study area. These geese, a portion of the flock which was established on .onticello Reservoir, have apparently become permanently established in this area and form a separate popula-tion of geese from the Monticello Reservoir flock.

The fall waterfowl survey of Monticello Reservoir found the large resi-dent flock of Can'ada geese to be present; other than that the only com-mon migrating species was the mallard. Numerous gulls, great blue herons and 8 common loons were also observed during this survey.

The winter waterfowl survey on Parr Reservoir and its tributaries found mallards to be abundant in both the reservoir and the dredge spoil area south of the tailrace canal on the east bank of the reservoir. Great blue herons and gulls were also common in these areas.

The winter survey of Monticello Reservoir found many more ducks present

(> 1,000) than on Parr Reservoir. These were mostly mallards and black ducks in a ratio of 3 mallards to one black duck. In addition to these ducks nearly 400 gulls were observed on Monticello Reservoir during this winter period. The results were somewhat different from 1981 when many more ducks were present on Parr Reservoir than on Monticello Res-ervoir. However, in 1981 Monticello Reservoir seemed to be avoided by ducks because of high winds during the survey. In 1982 the winds were not strong and ducks seemed to prefer Fonticello Reservoir. It appears therefore that the Ibnticello-Parr Reservoir system provides very good waterfowl habitat.

3.2-4

t The summer survey censused resident species that occurred in the area.

The wood duck is the only duck that can be expected to regularly breed there, although mallards will occasionally occur in the region. No wood ducks were seen in Parr or Monticello Reservoir during the surveys. 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 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, and wood ducks have probably moved to more stable areas of the Broad River. The only other aquatic birds seen in Parr Reservoir during the summer survey were four great blue herons.

Other than the transplanted geese, the only species seen in Monticello Reservoir were 13 double-crested cormorants, 2 common loons, and a single gull.

3.2.3 Strip Census 3.2.3.1 Introduction Avian strip censuses were conducted at six sites in the study area during the winter and summer of 1982. Three sites were designated as test sites and were located within an area of possible influence of the generating facilities; the other three sites were designated as con-trols, and were located outside of any area of influence (Figure 3.2.1). A survey test and control site were located in each of the following habitats 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 1982 surveys (Table 3.2.4). Twenty-nine species were recorded on the control sites during the same surveys (Table 3.2.5) . A graphic presentation of avian density in birds per acre on test and control 3.2-5

sites is provided in Figure 3.2.4. Avian diversity in number of species per site is depicted in Figure 3.2.5.

The pine habitat exhibited an increase in both diversity and density of species during the winter 1982 survey as compared to the winter 1981 survey. The increase was only evident on the test site (Transect SB) where the presence of numerous chickadees and pine warblers resulted in the highest density recorded in any habitat during the course of the '

entire study. The density on the control site (Transect 1) showed a ~

slight decline from the 1981 levels. Diversity was nearly equal and fairly high on both test and control sites.

During the summer survey in the pine habitat, the density of birds on the test site was much higher than in 1981 and greatly exceeded the number observed on the control site in 1982. Bird density on the pine control site in 1982 was only half that of the test site. Diversity  !

was also somewhat higher on the test site than on the control site, and this was the first year in which test site diversity exceeded that of the control site.

~

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 ,

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 pine-dominated sites.

The density of birds on the control, selectively-cut pine stands during winter 1982 was much higher than that reported in the winter of 1981 and resembled levels recorded in the winter 1980 survey. This density 3.2-6

l was due mainly to relatively large flocks of chickadees and yellow-rumped warblers observed here. During this time of year localized occurrencea of large flocks of these two species are common occur-rences. The bird density on the selectively-cut test site during winter 1982 was the lowest since the initiation of the avian surveys.

Diversity of species in the selectively-cut pines was similar on the test and control transects and was not greatly different from previous years.

The summer surveys in the selectively-cut pine habitats resulted in similar densities on the test and control sites and these levels .,

declined from those recorded in previous years. Diversity followed the same pattern, and declined slightly.

The deciduous control site was located in a heavily wooded stream bot-tom while the test site was located in an area adjacent to a transmis-sion line that was constructed 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.

The winter community observed on the deciduous control site was higher in density and diversity compared to the levels recorded in 1981, and was also the highest recorded since the initiation of the surveys. No particularly large flocks of birds were seen, but a number of species were present in small groups. The bird populations on the test site were somewhat higher in density and lower in diversity than the control site, but were at levels comparable to those observed in the past.

During 1981 species density was very low on the test site, but diversity was comparable to previous years; the 1982 survey indicated that this was only a chance occurrence and that the populations are similar to those observed during winter surveys for the past three years.

3.2-7

l l

The summer bird populations on the deciduous control site were similar in both density and diversity to those observed in previous years. No one species was particularly common. The deciduous test site, however, showed a greatly reduced density when compared to data from 1979 and 1980. In 1981 this site documented a reduced density of species and the same results were seen in 1982. Diversity was also somewhat reduced. These reductions in numbers cannot be attributed to the operation of the generating facilities and no real explanation is available at the present time.

3.2.4 Unusual Observations s

• During 1982 surveys, the bald eagle, a species listed as endangered by the U.S. Department of the Interior, was observed within the study region. Two bald eagles were seen during both winter and fall surveys.

The birds seen in the winter were immature individuals but the two seen during the fall survey were both mature, so at least four individual birds were observed. 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.

3.2.5 Sumnary Avian populations along both the control and test auto survey routes were both high in density and aiversity as compared to the 1981 find-ings. The test route was higher in avian density than the control route, a situation which has existed since 1973. The somewhat lower numbers of birds along the control route apparently relates to the greater degree of urbanization along this route than along the test route. The habitat along the test route is less patchy and is not so subject to human disturbance, thus accounting for the higher population levels.

3.2-8

The Game Bird Call Counts demonstrated that bobwhite quail populations along both routes are similar in size and have remained relatively stable since 1977. The mourning dove populations tend to fluctuate more widely than the quail, due mainly to the migratory nature of mourning doves. This year the highest mourning dove levels seen during the entire study were recorded.

The waterfowl survey indice' ad 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 win'er, 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 appeared to be as common in 1982 as in previous studies and may have increased in numbers. Species such as gulls, killdeer, and loons, which first appeared after construction was completed, were still present. The ef forts to establish a resident population of Canada geese seems to have been very successful, and breeding and nesting have ,

been observed.

In general, the bird populations surveyed in the strip counts demon-strated little change from the 1981 surveys. The test strips still have more birds than do the control strips in most areas, but no substantive changes from previous years were evident.

Both immature and mature bald eagles were seen during the fall and winter surveys. The Monticello-Parr Reservoir systems have proven to be quite attractive to eagles during their yearly migrations.

s 3.2-9

l e

Table 3.2.1 Birds observed during the auto survey - summer 1982.

Page 1 of 2 Route Where Observeda ,

ABC D_ Status Common Name Scientific Name Eastern bluebird Sialia sialis X X P Red-shouldered hawk Buteo lineatus X P Mourning dove Zenaida macroura X X P Yellow-billed cuckoo Coccyzus americanus X X S Chimney swift Chaetura pelagica X X 3 Common flicker Colaptes auratus X X P Red-bellied woodpecker Melanerpes carolinus X X P Eastern kingbird Tyrannus tyrannus X S Great crested fly-catcher Myiarchus crinitus X S Barn swallow Hirundo rustica X X S Purple martin Progne subis X X S Blue jay Cyanocitta cristata X X P Common crow Corvus brachyrhynchos X X P Carolina chicladee Parus carolinensis X X P Tuf ted 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 American redstart Setophaga ruticilla X S Common yellowthroat Geothlypis trichas X X P Mockingbird Mimus polyglottos X X P Robin Turdus migratorius X X P Wood thrush dylocichla mustelina X X S Carolina wren Thryothoru ludovicianus X X P Turkey vulture Cathartes aura X P Black vulture Coragyps atratus X P 3.2-10 .

- _ -----______.___m_ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _

Table 3.2.1 (Continued) Page 2 of 2 Route Where Observeda ABC -

D Status" Common Name Scientific Name House sparrow Passer domesticus X P Fish crow Corvus osaifragus X P Osprey Pandion haliaetus X S Bobwhite quail Colinus virginianus X X P Starling Sturnus vulgaris X P White-eyed vireo Vireo griseus X X S Pine warbler Dendroica pinus X X P Prairie warbler Dendroica discolor X X S Yellow-breasted chat _I_cteria virens X X S Sturnella magna X X P Eastern meadowlark Red-winged blackbird Agelaius phoeniceus X X P Common grackle Quiscalus quiscula X X P Bluegray gnatcatcher Polioptila caerulea X S Summer tanager Piranga rubra X X S Cardinal Cardinalis cardinalis X X P Blue grosbeak Guiraca caerulea X S Indigo bunting Passerina cyanea X X S Parula warbler Parula americana X S Eastern phoebe Sayornis phoebe X P Black and white warbler Mniotilta varia X X S Rufous-sided towhee Pipilo erythrophthalmus X X P Powee Contopus virens X S Total Number of Species 38 42 a Routes are illus: rated in Figure 3.2.1 b

P = Permanent Resident S = Summer Resident 3.2-11

Table 3.2.2 Birds observed during the auto survey - winter 1982.

Page 1 of 2 Route Where Observeda ABC -

D Status D Common Name Scientific Name Turkey vulture Cathartes aura X P Red-tailed hawk _Buteo jamaicensis X X P Red-winged blackbird Agelaius phoeniceus X X P Common flicker Colaptes auratus X P Starling Sternus vulgaris X X P Red-bellied woodpecker Melanerpes carolinus X X P Downy woodpecker Picoides pubeseens X X P Bluejay Cyanocitta cristata X X P Common crow Corvus brachyrhynchos X X P Carolina chickadee Parus carolinensis X X P Tufted titmouse Parus bicolor X X P Yellow-rumped warbler Dendroica coronata X X W Marsh hawk Circus cyaneus X W Red-shouldered hawk Buteo lineatus X P Mockingbird Mimus polyglottos X X P Robin Turdus migratorius X X P Hermit thrush Catharus guttatus X X W Gray catbird Dumetella carolinensis X P English sparrow Passer domesticus X X P Eastern meadowlark Sturnella magna X X P Common grackle Quiscalus quiscula X P Cardinal Cardinalis cardinalis X X P Rufous-sided toahee Pipilo erythrophthalmus X X P Chipping sparrow Spizella passerina X X P White-throated sparrow Zonotrichia albicollis X X W Purple finch Carpadaeus purpureus X X W Brown-headed nuthatch Sitta pusilla X X P Great blue heron Ardea herodias X P Belted kingfisher Megaceryle alcyon X X P Eastern phoebe Sayornis phoebe ' X P Ruby-crowned kinglet Regulus calendula X X W American kestrel Falco sparverius- X X P Mourning dove Zenaida macroura X P Carolina wren Thryothorus ludovicianus X X P Pine warbler Dendroica pinus X X P 3.2-12

Table 3.2.2 (Continued) Page 2 of 2 Route Where Observeda ABC D Status" Common Name Sc?entific Name Yellow-bellied Sphyrapicus varius X P sapsucker Evening grosbeak Hesperiphona vespertina X W Pileated woodpecker Pryocopus pileatus X P Song sparrow Melospiza melodia X P Cedar waxwing Bombycilla cedrorum X X W Wild Turkey Meleagris gallopavo X P Eastern bluebird Sialia sialis X X P Total Number of Species 36 34 a Routes are illustrated in Figure 3.2.1 b P = Permanent Resident S = Summer Resident W = Winter Resident 3.2-13

Table 3.2. 3 Results of 1982 waterfowl surveys.

Dredge Spoil /

Tailrace Canal Cannons Creek Parr Reservoir Monticello Reservoir Winter Summer Fall Winter Summer Fall Winter Summer Fall Winter Summer Fall Common Name 353 25 965 88 Mallard 93 289 6 2 305 6 Black duck 4 49 3

Greater scaup 4 6 11 Pintail 4 l

Shoveler 2 13 l

220 20 5 Blue-winged teal 2 l

2 8 Common loon 2 1

2 Pied-bil. led grebe 2 22 22 1 11 1 15 Great blue heron 19 3 2 6 1

Belted kingfisher 1 13 4 1

F Double-crested cormorant 15 15 387 1 28 y Gull (ring-billed / herring) 1 16 1 10 4

Bufflehead 0 0 0 365 0 47 1299 0 111 Total Ducks 109 0 558 Total Shore Bird s/ 12 16 0 33 391 16 68 Wading Birds 20 3 40 2 2 2 12 381 0 80 1690 16 179 Total Individuals 129 3 598 2 2 5 0 7 9 3 9 8 1 6 2 2 Tbtal Species

Table 3.2.4 Results of avian strip census conducted in different habitats on test sites during winter and summer of 1982.

Selectively Pine Cut Pine Deciduous Statiun 5B Station 4 Station SC Common Name Winter Summer Winter Summer Winter Summer Cardinal 1 1 3 2 1 Rufous-sided towhee 2 1 1 1 L Blue jay 1 Tuf ted titmouse 1 1 1 1 1 Carolina chickadee 10 3 1 2 2 1 Common crow 3 Mourning dove 1 Wood thrush 1 White-eyed vireo 1 1 2 Downy woodpecker 1 1 Red-bellied woodpecker i Brown-headed nuthatch 1 1 2 Prairie warbler 1 1 Pine warbler 9 2 2 1 3 Yellow-rumped warbier 4 Red-winged blackbird 1 Purple ficeh 3 Ruby-crowned kinglet 2 1 Black-billed cuckoo 2 Yellow-breasted chat 1 Numbers of Individuals 36 14 5 12 13 8 Number of Species 10 10 4 9 8 7 3.2-15

Table 3.2.5 Results of avian strip census conducted in different habitats on control sites during winter and summer 1982.

Selectively fine Cut Pine Deciduous Station 1 Station 7 Station 8 Common Name Winter Summer Winter Summer Winter Summer Cardinal 2 1 1 1 3 Rufous-sided towhee 1 1 1 1 Blue jay 1 2 Tuf ted titmouse 1 2 Carolina chickadee 4 1 9 1 3 2 Robin 2 Mourning dove 1 He rmit thrush 1 Wood thrush 1 1 Summer tanager 1 White-eyed vireo 4 Whi p-poo r-will 1 Red-shouldered hawk 1 Brown creeper 1 Pine warbler 1 2 4 1 Red-bellied woodpecker 1 Downy woodpecker 2 1 i White-throated sparrow 1 Eastern phoebe 1 Parula warbler 1 Brown-headed nuthatch 2 Common flicker 1 Ruby-crowned kinglet 3 4 Carolina wren 2 Yellow-rumped warbler 10 2 Golden-crowned kinglet 1 1 Red-winged blackbird 1 Bobwhite quail 1 2 Evening grosbeak 2 Number of Individuals 16 8 22 9 26 18 Number of Species 9 7 5 7 14 10 3.2-16

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4.0 REFERENCES

Battelle, 1974. Battelle Laboratories, Inc., Environmental impact monitoring of nuclear power plants-source book. Atomic Industrial Fo rum , Inc . August 1974, 810 pp.

Carlander, K.C., 1977. Handbook of freshwater fishery biology, Volume 2. Iowa State University Press, Ames, Iowa. 431 pp.

, 1969. Handbook of freshwater fishery biology, Volume 1.

Iowa State University Press, Ames, Iowa. 752 pp.

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 workshop on freshwater larval fishes. Knoxville, Tennessee , February 21-22, 1978. Tennessee ,

Valley Authority, Division of Forestry, Fisheries, and Wildlife Development, Norris, Tennessee. 241 pp.

Conner, J.V. , 197 9. Identification of larval sunfishes (Centrarchidae:

Elassomidae) from southern Louisiana, in R.D. Hoyt (ed.), Proceed-ings of the third symposium on larval fish, February 20-21, 1979, Bowling Green, Kentucky. Western Kentucky University. 236 pp. -

Dames & Moore, 1978; Environmental monitoring report June 1978 - c December 1978. For the Federal Energy Regulatory Commission project license number 1.894 and the South Carolina Department of Health and Environmental Control.

, 1979. Environmental monitoring report Jaauary 1979-June 1979. For South Carolina Department of Health and Environmental Control.

, 1979a. Environmental monitoring report July 1979 -

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 South Carolina Department of Health and Environmental Control.

, 1981. Environmental monitoring report January 1981 -

December 1981 for the Federal Energy Regulatory Commission Project License Number 1894 and the South Carolina Department of Health and Environmental Control.

Hutchinson, G.E. , 1957. A treatise on limnology. Vol. I. John Wiley & Sons, Inc. New York. 1015 pp.

4.0-1 -

Jester, D.B. and B.L. Jensen, 1971. Life history and ecology of the gizzard shad, Dorosema cepedianum (Le Sueur) with reference to Elephant Butte Lake. Agricultural Experiment Stations Research Report 218. New Mexico State University. 56 pp.

Knight, C.B., 1965. Basic concepts of ecology. Macmillan Co. ,

Toronto. 468 pp.

Koo, T.S.Y. and M.L. Johnston,1978. Larva deformity in striped bass, Morone saxatilis (Walbaum), and blueback herring, Alosa aestivalis (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 . ,

Dubuque. 421 pp.

Marcy, B.C. , Jr. , 1971. Survival of young fish in the discharge canal of a nuclear power plant, J. Fish. Res. Bd. Canada 28:

1057-1060.

, 1973. Vulnerability and survival of young Connecticut River fish entrained at a nuclear power plant. J. Fish. Res .

Board Can. 30: 1195-1203.

Pennak, Robert W., 1978. Freshwater invertebrates of the United States, 2nd ed. John Wiley and Sons, New York, 803 pp.

Pickering, Q.H. and C. Henderson, 1966. The acute toxicity of some heavy metals to different species of warm water fishes.

International Journa_ !,1r and Water Pollution. Vol. X, pp. 453.

Document EPA-440/9-76-023. USSPA, Washington, DC 501. p.

Schubel, J.R., C.C. Coutant and P.M.J. " 4, 1978. Thermal ef fects of entrainment, ir! J.F. Schubel an.. Marcy, Jr. (eds.), Power Plant Entrainment, a Biol.ogical Asse n;t. Academic Press , New York, New York.

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 Starage Reservoir near Holtwood, Pennsylvania. M.S. Thesis.

Cornell University, Ithaca, New York. 209 pp.

South Carolina Department of Health and Environmental Control,1981.

Water classification standards system for the state of South Carolina. 15 p.

Stemberger, R.S., 1979. A guide to rotifers of the Laurentian Great Lake s . 186 pp. E PA-600/4-79-021.

U.S. Environmental Protec tion Agency,1976. Quality criteria for wa ter. Document EPA-440/9-76-023. USEPA, Wa shington, DC 501 p.

4.0-2

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.

The schedule for monthly and quarterly p'.tysical measurements and water quality sampling is given 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 ,

Model 51 dissolved oxygen meter, pH with an AMl Model 107 pH meter, and conductivity with a GLI Model 708 conductivity meter. All instruments were given time to stabilize before the readings were recorded at each depth. Transparency was determined using a Secchi disc. Appropriate calibrations of all instruments were carried out several times curing each sampling day.

Surface water samples were collected in plastic bottles for determina-tion of select chemical parameters. - The samples were preserved in the field according to approved procedures and shipped on ice to the analytical laboratory.

The methods used for chemical analysis of water samples are listed in J

Table A-4. Inspection for oil and grease residue and unusual odor was conducted daily below Parr Dam (Station 5A) by SCE6G personnel. .

l h

A-1

l Table A-1 Water quality sampling locations and sampling dates for the Summer /

I Fairfield Environmental }bnitoring Program, January 1982 through December 1982.

^ LOCATION AREA NM R 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 Dcm 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 20 Monticello Reservoir Eastern Section SAMPLING DATES January 12-13, 1982 February 16-17, 1982 bbrch 9-10, 1982 April 13-14, 1982 May 11-12, 1982 June 15-16, 1982 July 13-14, 1982 August 10-11, 1982 September 14-15, 1982 October 12-13, 1982

- November 9-10, 1982 December 14-15, 1982 A-2

Table A-2. Monthly sampling schedule for the Summer /Fairfield water quality study.

Station Number: 1 2 5A 11 12 14 15 1. 6 18 A. LABORATORY ANALYSES (surface sample only)

Sodium Hardness x x x x x x x x h1 Calcium Hardness x x x x x x x x NR Magnesium x x x x x x x x NR Chloride x x x x x x x x NR Sulfate (SO4 ) x x x x x x x x NR TDS x x x x x x x x NR TSS x x x x x NR NR NR NR M0-Alkalinity x x x x x x x x NR P-Alkalinity (CACO 3) x x x x x x x x NR Ammonia (NH3 ) x x x x x x x x NR BOD x x x x x x x x NR Cadmium x x x x x x x x NR C0D x x x x x x x x NR Total Chromium x x x x x x x x NR Copper x x x x x x x x NR Total Hardness (CACO3 ) x x x x x x x x NR Total Iron x x x x x x x x NR Lead x x x x x x x x NR Mercury x x x x x x x x h3 Nitrate (NO3 ) x x x x x x x x NR Ortho-Phosphate x x x x x x x x NR Total Phosphate x x x ., x x x x x NR Silica (SiO2) x x x x x x x x NR Turbidity x x x x x x x x NR Zinc x x x x x x x x NR Carbon Dioxide x x x x x x x x NR Kjeldahl Nitrogen NR NR NR NR NR NR NR NR NR Boron NR NR NR NR NR NR NR NR NR NR: Not Required B. IN SITU MEASUREMENTS (1 Meter Intervals Surface to Bottom)

Temperature Dissolved Oxygen Stations 1, 2, 2W, 5A, 11, 12, 13, 14, 15, pH 16, 17, 20 Conductivity C. IN SITU MEASUREMENT (Surface)

Transparency (Secchi Disc) Stations 1, 2, 2W, 5A, 11, 12, 13, 14, 13, 16, 17, 20 A-3

l Table A-3. Quarterly sampling schedule for the Summer /Fairfield water quality study.

Station Number: 1 2 SA 11 12 14 15 16 18 A. LABORATORY ANALYSES (surface sample only)

Sodium Hardness x x x x x x x x NR .

Calcium Hardness x x x x x x x x NR Magnesium x x x x x x x x NR Chloride x x x x x x x x NR Sulfate (SO4 ) x x x x x x x x NR TDS x x x x x x x x x TSS x x x x x x x x x MO-Alkalinity x x x x x x x x x P-Alkalinity (CACO3) x x x x x x  :: x x Ammonia (NH3 ) x x x x x x x x x BOD x x x x x x x x x Cadmium x x x x x x x x x C0D x x x x x x x x NR Total Chromium x x x x x x x x x Copper x x x x x x x x x Total Hardness (CACO3 ) x x x x x x x x x

- Total Iron x x x x x x x x NR Lead x x x x x x x x x Mercury x x x x x x x x x Nitrate (NO3 ) x x x x x x x x x Ortho-Phosphate x x x x x x x x x Total Phosphate x x x x x x x x x Silica (SiO2 ) x x x x x x x x NR Turbidity x x x x x x x x x Zinc x x x x x x x x NR Carbon Dioxide x x x x x x x x NR Kjeldahl Nitrogen NR NR NR NR x x x x NR Boron x x x x x x NR x x NR: Not Required B. IN SITU MEASUREMENTS (1 Meter Intervals Surface to Bottom)

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, 5A, 11, 12, 13, 14, 15, 16, 17, 20 A-4

Table A-4 Procedures used in chemical analysis of water quality samples taken between January 1982 and December 1982 for the Environ-mental Monitoring Program.

Parameter Detection Limits Procedurea Sodium 0.01 mg/ liter AA - SM Calcium 0.08 mg/ liter ASTM D1126-67B Magnesium 0.5 mg/ liter ASTM D1126-67B Chloride 0.4 mg/ liter SM Sulfate (SO4 ) 1 mg/ liter ASTM D516-68B Total Dissolved Solids 1 mg/ liter ASTM D1887-67A Total Suspended Solids 1 mg/ liter ASTM D1888-67A MO-Alk 2 mg/ liter ASTM D1057-70C P-Alk (CACO3 ) 2 mg/lt er ASTM D1067-74B Ammonia (NH3 ) 0.1 mg/ liter ASTM D1426-74B 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 (CACO3 ) 2 mg/ liter ASTM D1126-67B Total Iron 0.02 mg/ liter EPA Lead 0.05 mg/ liter EPA Mercury (pg/1) 0.2 mg/ liter EPA Nitrate (NO3 ) 0.2 mg/ liter SM 419-D Ortho-Phosphate (PO4 ) 0.01 mg/ liter ASTM D-515-72B Total Phosphate 0.01 mg/ liter ASTM D-515-72B Silica (SiO2) 0.04 mg/ liter ASTM D859-68D Turbidity NTU 0.01 NTU ASTM D1889-71 Zinc 0.01 mg/ liter EPA Carbon Dioxide 1 mg/ liter SM-407-A Kjeldahl N 1 mg/ liter EPA Boron 0.2 mg/ liter SM 107B Analysis Procedures taken from:

SM - Standard Methods for the Examination of Water and Wastewater, 1976, 14th ed. Publ. by American Publ. Health Assoc., Amer.

Water Works Assn., 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 A-5

-^^ _ _ _ _ _ _

SOUTH CAROLINA ELF 4C,TRIC & GAS COMPANY Post oppica g COLUMBIA. south CARQuNA 29218 C. W. OlXON. JR.

v.ca Passioe~r February 2, 1984 Nucts AR OranATioNs Mr. Harold R. Denton, Director Office of Nuclear Reactor Regulation g U.S. Nuclear Regulatory Commission Washington, D.C. 20555

Subject:

Virgil C. Summer Nuclear Station Docket No. 50/395 Operating License No. NPF-12 1

Environmental Monitoring Repcit

Dear Mr. Denton:

South Carolina Electric and Gas Company hereby submits one (1) copy of the 1982 Annual Environmental Monitoring Report for the Virgil C. Summer Nuclear Station for your information. The report serves as a final preoperational report for the requirements of the National Pollution Discharge Elimination System (NPDES) permit for the Virgil C. Summer Nuclear Station issued by the South Carolina Department of Health and Environmental Control.

If you have any questions, please contact us at your convenience.

er t ly yours, A

W&

Dixon, Jr.

AM:OWD/fjc

Attachment:

cc: V. C. Summer T. C. Nichols, Jr./O. W. Dixon, Jr.

E. H. Crews, Jr.

E. C. Roberts W. A. Williams, Jr.

D. A. Nauman H. R. Denton J. P. O'Reilly Group Managers O. S. Bradham C. A. Price C. L. Ligon (NSRC)

G. J. Braddick D. J. Richards NRC Resident Inspector J. B. Knotts, Jr.

NPCF sE:13

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