ML20246J994
| ML20246J994 | |
| Person / Time | |
|---|---|
| Site: | McGuire, Mcguire  |
| Issue date: | 05/31/1989 |
| From: | DUKE POWER CO. |
| To: | |
| Shared Package | |
| ML20246J984 | List: |
| References | |
| NUDOCS 8909050323 | |
| Download: ML20246J994 (159) | |
Text
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LAKE NORMAN: 1988
SUMMARY
MAINTENANCE MONITORING PROGRAM, McGuire Nuclear Station: NPDES No. NC0024392
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Duke Power Company i Production Environmental Services, TTC/ASC ,,
Route 4, Box 531 Huntersville, North Carolina 28078 4
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May, 1989
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LAKE NORMAN: 1988
SUMMARY
. Page EXECUTIVE
SUMMARY
........... ....... ........ .................. i ~
MNS OPERATIONAL DATA Introduction................... ........................... I 1988 0peration............................................. 2 Discharge Temperatures....... .... ........................ 3 WATER CHEMISTRY Introduction......... .......... .......................... 6 Methods and Materials........... . .. .. .................. 7 Results and Discussion......................... ........... 9 Summary....................... . ....... .................. 19 ,
Literature Cited................ .......... . ............ 21 j Tables and Figures................. ... . ................. 22 THERMAL PLUME SURVEYS l
Introduction...................... . ... ................. 66 Methods and Materials....................... .............. 66 Results and Discussion........ . ......................... 67 Figures. ..... ......... .. ................. ........... 69 PHYTOPLANKTON Introduction........... ......... ...... .................. 73 Methods and Materials........... ....... ...... ........... 73 Results and Discussion............ ........................ 74 Summary........ ............. ................ ..... . ... 77 Literature Cited. ............ . ..... .... ...... ...... 79 l Tables and Figures.... ....... ...... . .. .......... .... 80 1
ZOOPLANKTON Introduction.... ..................... .... ............ . 98 Methods and Materials..... .... . ............... ........ 98 Results and Discussion....... ... ........ ............... 99 Summary....................... .. . .. .. .......... .... 103 Literature Cited...................... ........ .......... 105 Tables and Figures................. .. .. ... ....... .. 106 FISHERIES Introduction... ........................ ................. 112 Methods and Materials..................................... 113 Results and Discussion.. .................................. 117 Future Studies......................... ....... ... ...... 125 S umm a ry . . . . . . . . . . ............. ... .... ..... ........... 126 Literature Cited.................. .. ......... .......... 129 Tables and Figures. ............. . . ..... . . ...... . 133 J
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EXECUTIVE
SUMMARY
This report summa.r.izes the 1988 results of the Lake Norman ao.uatic environment mainter.ance monitoring program, as required by NPDES Permit No. NC0024392, for McGuire Nuclear Station. The overall capacity factor for McGuire during 1988 was 77.9%.
Epilimnion temperatures in 1988 in the mixing zone were slightly (<2 C) higher from February to October than during prior years; the highest temperature occurred in August at the discharge location. The minimum oxygen level at the discharge location in August was 4.9 mg/L. Higher dissolved oxygen was noted in the hypolimnion of the mixing zone as a result of earlier turnover. The thermal and oxygen dynamics of Lake Norman were similar to other southeastern reservoirs of comparable size and trophic status. Drought conditions and continuing basin development are believed to be responsible for increases over preoperational levels for pH, alkalinity, conductivity, chloride, sodium, and potassium.
Duke was granted a one-time authorization by NCDEM to discharge at a monthly average of 97 F during August 1988. Plume mapping on 11 August, with a discharge temperature of 35.1 C, measured a 2.8 C-above-background plume of 47 ha, and a 32.2 C plume of 146 ha. Plume mapping on 24 August, with a discharge temperature of 37.4 C, measured a 2.8 C-above-background plume of 314 ha, and a 32.2 C plume of 676 ha.
Phytoplankton chlorophyll a and standing crop values generally increased from downlake to uplake, as in previous years. Phytoplankton taxonomic composition was similar to previous years, with diatoms, cryptophytes, golden-brown algae, and green algae being the most abundant.
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Zooplankton densities in 1988 were generally within the ranges observed during the same months in prior years, and standing crops usually tended to increase from downlake to uplake locations, as with phytoplankton. Rotifera dominated the zooplankton community, followed in importance by Copepoda and Cladocera.
Densities were higher in the top 10 m than in bottom to surface tows, and were highest in May and lowest in February.
Cove rotenone sampling in August 1988 yielded a total of 26 fish species, and standing stocks (of total and of sport fish) were within the ranges estimated in previous years at the discharge and control location. Fish densities were estimated with hydroacoustic gear: Densities were highest in the discharge l
l area in early summer and in fall, while some fish avoided the discharge area during late summer periods of peak discharge temperature. Suitable habitat for striped bass was depleted in August, as has happeneo in prior years and in other southeastern reservoirs; four observed mortalities from June through September were not considered significant. Largemouth bass studies reflect no l
i adverse effects in or near McGuire's mixing zone. Hydroacoustics studies will be repeated in 1989, to assess the abundance and distribution of fish, in conjunction with vertical temperature and oxygen profiles.
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MCGUIRE NUCLEAR STATION INTRODUCTION Duke Power Company and NCDEM representatives met on January 14, 1988, at Duke's Applied Science Center, for a presentation and overview of Duke's objectives associated with modifying the NPDES pertit. Duke subsequently submitted a S request to NCDEM, dated May 20, 1988, for a NPDES permit modification to increase the July - September monthly average from 95 F to 99 F. In effect, another 316(a) was proposed to NCDEM for McGuire so it could discharge at k
greater than current NPDES limits. '
On July 8,1988, NCDEM was called by Nuclear Environmental Complianc' requesting permission to increase the discharge temperature of MNS on a monthly basis from 95 F to 97 F. Mr. Steve Tedder returned the call a short time 1ater with confirmation that Duke had a one-time authorization to discharge at a monthly average of 97 F, for the month of August 1988.
For reference purposes, some key historical datas are presented below:
Key Dates August 9, 1985 -- 316(a) submitted l
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October 18,1985 -- 316 (a) Variance granted i
August 8, 1987 -- Lake Norman Maintenance Monitoring begun May 20, 1988 -- Permit modification submitted for increasing average monthly discharge from 95 F to 99 F. ,
OPERATIONAL CHARACTERISTICS--1988
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During 1988, the overall capacity factor (CF) for McGuire was 77.9%. Unit l's CF was 74.8% and Unit 2's CF was 81.3% (Table 1). The CF for the station for the months of June, July, and August was 62.8%. Most noteworthy was the CF for Unit 1 during that time (31.7%). The Low Level Intake (LLI) for McGuire operated during the month of August 1988 to keep the Condenser Cooling Water (CCW) discharge temperature below a 97 F monthly average (Figure 1). Verbal permission was obtained from NCDEM to discharge at a greater temperature than the 95 F required in the NPDES permit. The July 8,1988 request to DEM did not ask for an increase to 99 F as requested in the permit modification application for the following reasons:
- 1. A major fire damaged Marshall Steam Station's Units 3 and 4. This resulted in these units being off line for several months; therefore, Units 3 and 4 did not operate during the spring. With these fossil units off-line, less Lake Norman hypolimnetic volume was used by Marshall for condenser cooling. With more hypolimnetic volume available during the summer of 1988 than has normally been available, the need for requesting a 99 F discharge temperature was mitigated.
- 2. Based on experience from previous years of managing the hypolimnion and the relatively cold winter of 1987-88, resulting in more cool Eg>
hypolimnetic water, it was estimated that a 97 F monthly average i
s 2
discharge temperature for August would provide adequate cool water volume to comply with both the NRC Technical Specification require-mentsa$dtheNPDESmonthlydischargetemperaturerequirements.
MCGUIRE DISCHARGE TEMPERATURE - 1988 The LLI pumps operated for 17 days during August 1988. The average monthly discharge temperature for August 1988 was 96.8 F (Figure 1). Figure 1 indicates that the running average temperature decreased disproportionately with LLI pumping during early September. This was due to the running monthly average being reset for the beginning of the month. The highest daily average discharge temperature for August was 102.4 F.
The LLI pumps were not needed during September to comply with the NPDES monthly average of 95 F.
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Table 1. Monthl/ capacity factors (%) for McGuire Nuclear Station during 1988.
MdMTH UNIT 1 UNIT 2 STATION JAN 95.2 95.2 95.2 FEB 98.4 101.8 100.1 MAR 94.6 101.6 98.1 APRIL 95.9 101.5 98.7 MAY 99.6 77.8 88.7 JUNE 90.9 0.0 45.2 JULY 95.1 5.0 50.0 AUG 96.5 90.0 93.3 SEPT 97.4 100.6 99.0 OCT 33.8 100.7 67.3 NOV 0.0 99.4 49.4 DEC 0.0 101.9 50.2 AVG 74.8 81.3 77.9 NET GENERATION X 100 = DAILY CAPACITY FACTOR PER UNIT (24 hrs / day) (1129 MW/ unit)
NET GENERATION (UNIT 1 + UNIT 2) X 100 = STATION DAILY (24 hrs / day) (2258 MW/ station) AVERAGE CAPACITY FACTOR i
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LAKE NORMAN WATER CHEMISTRY
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INTRODUCTION This chapter of the report covers the water chemistry portion of the 1988 monitoring program. The objectives are to:
- 1) maintain continuity with Lake Norman's historic data base at critical locations;
- 2) detect any significant impacts from Duke's operations;
- 3) document any long-term natural changes in the chemistry of Lake Norman, which might affect plant operations;
- 4) characterize the reservoir-wide thermal and dissolved oxygen regimes of Lake Norman; and
- 5) compare, where appropriate, these data to other impoundments in the Southeast.
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4 METHODS AND MATERIALS .
The complete water chemistry monitoring program, including specific variables, ,
locations, depths, and frequencies, is outlined in Tables 1 and 2. Sampling locations are identified in Figure 1. The specific chemical methodologies for 1988, along with the appropriate references, are presented in Table 3. In 1988, the method for calculating detection limits was revised to obtain more a
realistic and appropriate limits, based on guidelines by EPA, APHA, and the chemical industry. Graphs of data may reflect lower or higher limits for past data, however most data are above current and previous detection limits.
e Data were analyzed using two approaches. The first was similar to that used in the 316(a) report, where the reservoir was partitioned into mixing, background, and discharge zones, and comparisons were made among -
preoperational and operational years. The discharge is Location 4.0; the >
mixing zone includes Locations 1.0, 2.0, 3.0, 4.5, 5. 0, 6. 0, 7.5; the background zone includes Locations 8.0, 11.0, 15.0. The preoperational period in this report extends from 1977 through 1981. The operational years include:
J a) the first full year of 2-unit operations at MNS, September 1983 through August 1984, and l b) all of 1988.
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The second approach, used principally for temperature and dissolved oxygen data, erphasized a much broader lake-wide investigation for 1988 and /
encompassed the plotting of monthly isotherms and iscoleths, the determination 7 ,
of the hypolimnetic oxygen deficit, and the calculation of specific
' quantitative' thermal parameters such as the maximum heat content and the Birgean heat budget.
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1 RESULTS AND DISCUSSION Temperature and Dissolved Oxygen Historic Comparisons Temperature and dissolved oxygen data collected in 1988 were generally at or within the historic ranges observed for each of the specified zones in Lake Norman (Figures 2, 3, 4, 5, 6). Temperatures were greater than historic values (preoperational period through first year operational period, September 1983 - August 1984) in the mixing zone in February, March, April, May, August, September and October (Figure 2). Generally, these increases over historic levels were 5 2*C and occurred primarily in the upper 10 m of the water column. The greatest increase over historic values (2.1 C) occurred in August at a depth of three meters. Temperatures greater than historic values were observed throughout the entire water column only in October, as the lake {
cooled and mixed.
Temperature data for 1988 in the background zone exceeded historic values in February, June, August, and October and were generally of the same magnitude as changes observed in the mixing zone, i.e., 52 C (Figure 3). The greatest increase over historic values (2.3*C) occurred in February at a depth of two meters. At the discharge location, 1988 temperatures were generally within the historic range in February, June, July, November and December, and greater than historic values in the remaining months (Figure 4). The warmest discharge temperatures were measured in August (34.8 C) and September (34.3'C), and were 4.2 C and 1.5 C, respectively, warmer than maximum historic temperatures.
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Seasonal and spatial patterns of dissolved oxygen (DO) in 1988 were similar to -
historic patterns in both the mixing and background zones (Figures 5 and 6).
In the mixing zone, 00 values were slightly lower (by 51.0 mg/1) than historic values in April, August, September, and October (Figure 5). For the most part, these differences were restricted to the upper water column. The .
lone exception to this occurred in April when DO concentrations ranged from 0.1 to 0.9 mg/l less than historic values throughout the lower two-thirds of -
the water column. The greatest change in DO concentrations, as compared to historic values, occurred in August at the surface and measured 1.0 mg/l less than observed in the operational year. D0 values slightly higher than .
historic values (range = 0.4 to 8.0 mg/l higher) were also measured in the , ,
mixing zone, and occurred predominantly in the bottom waters during late-fall (November) and early-winter (December).
D0 concentrations in the background zone in 1988 were slightly lower (by 50.5 mg/1) than historic values in April, June, July, and September (Figure 6). As was observed in the mixing zone, these differences occurred primarily in the upper water column except in April when they were observed throughout the ..
lower two-thirds (below 10 m) of the water column. Slightly higher DO concentrations, as compared to historic values, were observed in the background zone in September (1.0 mg/l at 10 m) and in the bottom waters in '
November (1.0 mg/1), and December (2.0 mg/1).
DO concentrations in 1988 at the discharge location were at or within the historic range from October through March, and lower than the historic minimum from May through September. The lowest DO concentration at the discharge .
10 3
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location wFs observed in August and measured 4.9 mg/1. This was 1.3 mg/l less than observed in, August of 1984.
Reservoir-Wide Comparisons The monthly reservoir-wide temperature and dissolved nxygen data for 1988 are presented in Figures 7 and 8. For the most part, the temporal and spatial distributional patterns of both temperature and dissolved oxygen are similar.
to other cooling impoundments and hydropower reservoirs in the Southeast.
nd During the winter cooling and mixing period, vertical rather than horigd<htal homogeneity in temperature predominated, with the shallower uplake ' riverine' zone exhibiting slightly cooler temperatures than the deeper downlake
' lacustrine' zone (Figure 7). These longitudinal differences in temperatures were clearly illustrated in January and February. As is the case in other reservoirs, the principal factors influencing this gradient in Lake Norman are morphometric (depth) differences within the reservoir and advective inputs from upstream.
As more heat was gained at the water's surface during the day than was lost at night, signalling the beginning of the lake's heating period, buoyancy forces
' smoothed out' the horizontal differences in temperature while enhancing the vertical. Because the lake was at a period of vertical ' instability' during these times (e.g., March, April), warming occurred throughout the water column. Eventually, differential heating at the surface leo to the formation of the classical epilimnion, metalimnion, and hypolimnion zones that were clearly ' identifiable in July. In contrast tr. most natural lakes, but not unlike many reservoirs in the Southeasb a distinct thermocline within the metalimnion was not observed in Lake Norman in 1988. Rather, the metalimnion l
11 u--________ . _ _ _ _ _
was more or less continuous with respect to vertical density differences within the lower water column, and even showed signs of merging with the hypolimnion in August (Figure 7).
Cooling of the wate.- olumn began in early September as illustrated by decreases in surface tempet stures compared to August data. Concurrent with decreases in surface temperatures were an increase in the- depth of the epilimnion (caused by convective mixing) and a' disruptbn of. the horizontal homogeneity in epilimnion temperatures (caused by reservoir-wide differential heating and cooling, and advective inputs from upstream). Continuation of these differential vertical and horizontal processes led to even more pronounced thermal differences within the reservoir. For example, by October the uplake riverine zone had already ' turned over' while the downlake l lacustrine zone was still strongly stratified. Not until early Dember was Lake Norman completely mixed vertically throughout the reservoir.
l Distributional patterns of dissolved oxygen in 1988 were similar to but not l
i identical to temperature (Figure 8). Generally, dissolved oxygen l
l concentrations were greatest during the winter cooling and mixing period when biological respiration was at a minimum and atmospheric reaeration was at a maximum. The highest reservoir-wide mean concentration of dissolved oxygen (11.3 mg/l) occurred in March when the reservoir exhibited a temperature of 9.0'C (Figure 7). Unlike the thermal regime, no major longitudinal differences existed in dissolved oxygen within the reservoir during the winter. Not until the lake became stratified, thereby isolating the metalimnion and hypolimnion from atmospheric reaeration, were uplake-to-downlake gradients in dissolved oxygen observed. Longitudinal gradients in 12 L - - - - - - _ _ _ _ _ _ _ _ _ _ _ _ _ . _ _ _ _ _ _ _ _ _ __
+ .
metalimnetic. and hypolimnetic dissolved oxygen in 1988 were first observed in
-May. Differential dissolved oxygen depletion and eventual. anoxia were first observed in the transitional zone (Locations 15 through 62) where hypolimnetic volume is small, water column and sediment organic matter high, and advective mixing minimal. A metalimnetic oxygen minimum, also known as a negative heterograde oxygen profile, was also first observed in June in the transitional ' zone. By August, the complete hypolimnion throughout the reservoir below elevation 217 m was anoxic. This represents approximately 18%
of the entire volume of the lake at full pond.
Reaeration of the water column started in September concomitantly with the cooling'and mixing of the reservoir. Decreasing air temperatures cooled the surface waters resulting in a convective deepening, aided by wind-induced mixing, of the epilimnion. As the oxygenated epilimnion eroded progressively deeper into the water column, the width of the anoxic zone decreased.
Longitudinal differences in reaeration were also observed and apparently were related to differential mixing caused by McGuire Nuclear Station (MNS) and Marshall Steam Station (MSS), upstream advective inputs, and horizontal gradients in photosynthesis (Table 1 Plankton section). Reaeration was complete, reservoir-wide, by early November.
Heat and Dissolved Oxygen Calculations Table 4 presents some common quantitative limnological calculations for the thermal environment in Lake Norman. Few comparable calculations exist in the literature for reservoirs, but these data are generally within the 'ballpark' 13
of those presented by Hutchinson (1957) for natural lakes at similar latitudes throughout the world.
Table 5 presents the 1988 areal hypolimnetic oxygen deficit (AHOD) for Lake Norman compared to similar estimates for 18 TVA reservoirs. The data illustrate that Lake Norman exhibits an AHOD that is similar to other Southeastern reservoirs of comparable depth, chlorphyll a status, and secchi depth.
Alkalinity and pH Mean total alklainity values in Lake Norman during 1988 ranged from 12 to 16 mg-CACO 3 /1 (Figure 9). February and August values throughout the reservoir, and November values in the discharge, were comparnble to the maximum historic values. The remainder of the 1988 mean alkalinity values were within the historic range. The high alkalinity values in 1988 were generally observed throughout the reservoir and are probably not related to MNS operations.
During the preoperational and first year operational periods, bicarbonate represented the major anion (followed by chloride) in the discharge and background zones (Figure 10). During these periods, bicarbonate was approximately equal to chloride in the mixing zone. In 1988, bicarbonate was the major anion throughout the reservoir.
Mean pH values in Lake Norman during 1988 ranged from 6.6 to 7.6, with higher values observed uplake and on the bottom (Figure 11). The February pH values in each zone were equal to or higher than historic values. The pH values for the other months were within the historic range throughtat the reservoir. As l
with alkalinity, the high February pH values were observed throughout the 14
( j.
-l reservoir, especially in the background zone, and are probably not related to MNS operations.
l The higher alkalinity and pH values observed in Lake Norman during 1988 were probably the result of drought conditions, i.e., increased infiltration of ,
groundwater (relative to surface and runoff) which has relatively high-alkalinity and dissolved solids concentrations because it has reached near solid-solution equilibria (Hem 1985, Stumm and Morgan 1981).
Specific Conductance and Turbidity Mean specific conductance values in Lake Norman during 1988 ranged from 50 to 72'umho/cm (Figure 12). Mean 1988 values exceeded the maximum historic values by 4 to 19 umho/cm throughout the reservoir in February and August, and by 13 umho/cm in the discharge in November. The greatest difference between maximum historic values - and 1988 values (17 to 19 umho/cm) was observed in the discharge and mixing zones. The low lake levels (3 to 8 feet below full pond) during the drought of 1986,1987, and 1988 may have been partly responsible for the high conductivity values, as well as an increased proportion of groundwater infiltration (relative to mface runoff) with high dissolved solids concentrations (Hem 1985, Stumm and Morgan 1981). However, conductivity appears to be increasing slightly (Rho .5 to .7, p<0.01) over time throughout the reservoir (Figure 13), but especially in the more
-populated and rapidly developing lower end. This trend has also been observed in most of the reservoirs in the Catawba River basin (Clawson et al. 1984).
Mean turbidity values in Lake Norman ranged from 2 to 8 NTU in 1988, and were comparable to or less than historic values at all zones (Figure 14). Drought 15
conditions are probably responsible for reduced inflow, and thus suspended material, from the tributaries and upstream reservoir, and subsequently lower turbidity levels in Lake Norman in 1988. The higher 1988 veiues and greater historic variability were generally observed uplake in the more riverine conditions.
Nutrients Mean nitrate plus nitrite and ammonia concentrations throughout Lake Norman in 1988 were generally lower than corresponding historic values (Figures 15 and
'16). In 1988, the mean nitrate plus nitrient concentrations ranged from 0.073 to 0.22 mg-N/1, and mean ammonia concentrations ranged from 50.050 to 0.092 mg-N/1-. Mean orthophosphate concentrations throughout the reservoir were generally comparable to historic values in February, and were less than or equal to the detection limit of 0.010 mg-P/1 in May, August, and November.
(Figure 17). ~ Mean total phosphorus concentrations in 1988 in all zones were.
either within the historic range or less than the detection limit (Figure 18).
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1 Silica and Chloride Mean silica concentrations throughout Lake Norman in 1988 ranged from 2.4 to 3.7 mg-Si/l (Figure 19). February silica values were lower throughout the reservoir than historic values, while values during the other months were within the historic range. Mean chloride concentrations in 1988 ranged from 5.8 to 7.2 mg/l throughout the reservoir (Figure 20). Chloride concentrations were comparable to or higher than maximum historic values in all zones and months except in the mixing zone in May and November, which were within the historic range. The high chloride concentrations in 1988 followed a pattern similar to that observed with conductivity (Figure 21), possibly re flecting drought conditions as well as population growth (more industrial wastes) in the Catawba River Basin (Clawson et al. 1984).
Minerals Sodium is the dominant cation in all zones and time periods in Lake Norman, followed by calcium (Figure 10). Mean sodium concentrations in Lake Norman during 1988 ranged from 5.5 to 7.3 mg-Na/1 in February and from 6.5 to 6.8 mg-Na/l in August (Figure 22). Mean sodium concentrations in all zones in 1988 were considerably higher (by 1.0 to 3.2 mg-Na/l) than historic values, except in the mixing zone in August which was within the historic range. The high concentrations of sodium in 1988 may be associated with water table declines because sodium is removed from the less permeable strata as the more dilute water in the more permeable strata are depleted during drought conditions (Hem 1985).
Mean calcium and magnesium concentrations in 1988 in all zones and depths were comparable to historic values (Figures 23 and 24). Mean potassium 17
concentrations in 1988 were equal to or slightly higher than historic values in May and August at all zones (Figure 25). Mean iron and manganese concentrations in February 1988 were comparable to or lower than historic values throughout the lake (Figures 26 and 27).
l 18
l SLM4ARY
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Temperature and dissolved oxygen data collected in 1988 were generally similar thoughout the lake to data collected during the preoperational and first year operational periods of MNS. However, some differences from historic values were observed in both parameters in space and time. Epilimnion temperatures in 1988 in the mixing zone were slightly higher (<2 C) over the period February to October than observed during the preoperational and first year operational period. The greatest increase in temperature over historic levels (4.2 C) occurred in August at the discharge location where a maximum temperature of 34.3 C was measured. The greatest decrease in dissolved oxygen, as compared to historic values, occurred at the discharge location in August where a minimum oxygen concentration of 4.9 mg/l was measured, or 1.3 mg/l less than recorded in August 1984. The greatest increase in dissolved oxygen over historic values (0.4 to 8.0 mg/1) occurred in the hypolimnion of the mixing zone and resulted from an earlier " turnover". Reservoir-wide isotherm and isopleth information for 1988, coupled with heat content and hypolimnetic oxygen depletion data, illustrated that Lake Norman exhibited thermal and oxygen dynamics similar to other Southeastern reservoirs of comparable size and trophic status.
Alkalinity values throughout Lake Norman in 1988 were generally within the range of historic values in May and November, and comparable to the maximum historic values in February and August. The pH values were generally higher than historic values in February, and comparable to historic values during the other months. The higher pH and alkalinity values are probably related to drought conditions (the infiltration of high alkalinity, high dissolved solids 19
groundwater, relative to surface runoff). Specific conductance values exceeded the maximum historic values during much of 1988, probably because of both drought conditions and the general trends of increasing conductivity (over time) throughout most of the Catawba River reservoirs. Chloride l
concentrations in 1988 were comparable to or higher than maximum historic values and, like conductivity, probably reflect both drought conditions and population growth in the Catawba Basin. Sodium concentrations were considerably higher, and potassium concentrations were slightly higher, than historic values, probably due to increased groundwater infiltration (relative to more dilute surface runoff) during the drought conditions of 1988.
Calcium, magnesium, iron, and manganese concentrations were generally comparable to historic values.
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FUTURE STUDIES t Th'e 1989 water chemistry program will continue unchanged from the 1988 program.
LITERATURE CITED Clawson, P. A., C. W. Harden, R. N. Keener, and T. J. Bowling. 1984.
Evaluation of historical data on 12 reservoirs in the Piedmont Carolinas with respect to acid rain considerations. PES /84-21. Duke Power Company, NC.
Hem ~ John D. 1985. Study and interpretation of the chemical characteristics.
of natural water, Thi"d edition. U.S. Geological Survey Water-Supply Paper 2254. U.S. Government Printing Office, Alexandria, VA.
Higgins, J. M. and B. R. Kim. 1981. Phosphorus retention models for Tennessee Valley Authority reservoirs. Water Resour. Res., 17:571-576.
Higgins, J. M., W. L. Poppe, and M. L. Iwanski. 1981. Eutrophication analysis of TVA reservoirs. In: Surface Water Impoundments. H. G.
Stefan, Ed. Am. Soc. Civ. Eng., NY, pp. 404-412.
Hutchinson, G. E. 1957. A Treatise on Limnology, Volume I. Geography, Physics and Chemistry. John Wiley & Sons, NY.
Stumm, W. and J. J. Morgan. 1981. Aquatic chemistry: an introduction emphasizing chemical equilibria in natural waters. John Wiley & Sons, NY.
21
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Table 4. Heat content calculations for the thermal regime in Lake Norman in 1988.
-2 Maximum areal heat content 27,191 g. cal .cm Maximum hypolimnetic (below 11.5m) -2 areal heat content 12,807 g. cal .cm
-2 Birgean heat budget 20,119 g. cal. cm
~I Epilimnion (above 11.5m) heating rate 0.117'C day
-I Hypolimnion (below 11.5m) heating rate 0.074 C day 25
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< L .,
DXSCHARGE (LOCATION 4)- j
! ALK %LINITY - (mg-COCO 3/1) .
40- 'PREDPERATIONAL MAXIMUM O-
' 30 -
-. PREDPERAT!DNAL MINIMUM O
20 - PREDPERATIONAL
-a D 8 10 O U O 6 FIRST YEAR DPER MEAN' A
0 FEB- MAY AUG NOV . MIXING ZONE (LOCATIONS 1, 2, 3 4.5, 5, 6, 7.5) ALKALINITY (mg-COCO 3/1) 40 - PREDPERATIONAL
. MAX MUM g
'30 -
PREDPERATIONAL MINIMUM O 20 ' PREDPERATIONAL O O o MEAN "QL ~ n 10 o
.O o FIRST YEAR
- o. &m MUN a
D.FEB MAY AUG NOV BACKGROUND ZONE (LOCATIONS 8, 11, 15) ALKALINITY (mg-COCO 3/1) 40 - PREDPERATIONAL MAXIMUM O 30 - O PREDPERATIONAL MINIMUM O 20 - g PREDPERATIONAL 9 ,,. MEAN
" L a 10 g$ O o o FIRST' YEAR DPER MEAN A
-FEB MAY AUG NOV Figure 9. Temporal and spatial variations in quarterly mean (of water column) alkalinity for discharge, mixing. and background zones during the preoperational period (1977-1981). first year operational period (9/83-8/84), and 1988.
47
6 Figure 10. Ionic composition for discharge (Loc. 4), mixing (Loc. 1.2.3'.4.5.6. 7.5), and background (Loc. 8.11.15) zones during the preoperational period (1977-1981). first year operational period (9/83-8/84), and 1988. , UEQA.
*~
500 - DISCHARGE @x 450 - Gwa
'=
- #x f -
N - 2* -
! l i!!!!!$
f ! !!!!!!h
!= -
! j :i:i:i.i:
5 l ! O p&h# ps @\,$s # pe cGhe # sso
$k 500 .
MIXING 4so - @m 4= - gwa. 250 -
._ I BACKGROUND @K
.so . EE 4= -
% h% swa. ,
l i . l11a0- ~ . ..- *8 __ -_ - -____0
E OfSCHARGE (LOCATION 4) PH
- 9. 0
- PREDPERATIONAL-MAXIMLN n O-
' B. 0 -
PREDPERAT!DNAL 0 0 MINIM'A' () . u O
, 7. 0 "
n n PREDPERATIDNAL o- .MEAN. O b
- 6. 0 -
FIRST YEAR. DPER MEAN a FEB MAY AUG NOV 1998 EAN l MIXING ZONE CLDCATIONS 1. 2. 3. 4.5. 5. 6 7.5) PH -
- 9. 0 -
PREDPERATIDNA,L
,. O MAXIM!.M
'O
- 8. 0 -
Q PREDPERATIDNAL
-MINIMUM O O O
.- 7. 0 U 25 PREDPERAT!DNAL
' j, - -
n MEAN A h O
- 6. 0 FIRST YEAR O DPER MEAN-O a
o FEB MAY AUG NOV 1968 MEAN BACKGROUND ZONE (LOCATIONS 8. 11. 15) PH
- 9. 0 '
PREDPERATIDNAL O MAXIMJM O O B. 0 - PREDPERATIDNAL
- MINIM'JM O u g 0
- 7. 0 -
p PREDPERATIDNAL 2- McAN 6
- 6. 0 O o FIRST YEAR g DPER MEAN A
- 5. 0 FEB MAY AUG NOV 1988 MEAN Figure 11. Temporal and spatial variations in quarterly mean (of water column) i pH for discharge, mixing and background zones during the first year operational period p(reoperational period 9/83-8/84), and 1988.(1977-1981).
49 f
DISCHARGE (LOCATfDN 4) L SPECIFIC CONDUCTANCE (UMHD/CM) 110- PREDPERATIDNAL 100 -
"A "#
90 - r PREDPERAT!DNAL 80 - "I"IM# O 70 -
- PREDPERATIONAL
- MEAN 60
- O 50 h a h
FIRST YEAR 40 0 6 O DPER MEAN
- @-- g 30 FEB MAY AUG NOV MIXING ZDNE
- (LDCATIONS 1. 2, 3. 4.5. 5. 6. 7. 5) l SPECIFIC CONDUCTANCE .(UMHD/CM) 110- PREDPERATIONAL '
100 , o MAX MW 90 - PREDPERATIONAL 80 , MINIMW O 70 -
- PREDPERATIONAL
- h MEAN 60 -
, 50 - h b - FIRST YEAR l DPER MEAN 40 O O , 6 O A FEB MAY AUG NOV 4 L BACKGROUND ZDNE (LOCATIONS 8. 11. 15) l< SPECIFIC CONDUCTANCE (UMHD/CM) 110 - PREDPERATIONAL 100 - M^*hM# 90 - PREDPERATIONAL 80 - MIN MW 70 - PREDPERATIDNAL SD
- O n MEAN 50 0 O FIRST YEAR 40 DPER MEAN O
g O FB hay AUG NOV Tigure 12. Temporal and spatial variations in quarterly mean (of water column) specific conductance for discharge, mixing,)and eriod (1977-1981 background
, first year zones during the operational period (9/83-8 preoperational p/84), and 1988.
50
. Figure 13. Surface (0.3 m) specific conductance values over time for discharge (Loc. 4). mixing (Loc. 1.2.3.4.5.6.7.5), and background (Loc.
8.11.15) zones. n;> - CO@ UCTIVITY G M C/OO DISCHARGE oO s0 - 70 - 80 50 - 40 - m - 20 -
-10 -
o g@ g@* g@* \M g@ \M gM g@'gM gM a,M gM 100 MIXING e0 - 40 - 30 - 20 - 10 - 0 g@l spt \p9 \g \g \g \g \p6 gg \g p1 g \g 100 - BACKGROUND 90 - 90 - 70 - 80 - 50 - 40 - 30 - 20 - 10 - g, , , , , g@i g@' g@* gM g@\ g M gM g@' gM gM g@' gM YEAR 51
DTSCHARGE (LOCATf0N 4)
- TURBIDITY (NTU)-
200 - PREDPERATIONAL MAXIMUM 240 O 200 - -- PREDPERATIONAL l. MINIM'JM 160 - 0 PREDPERATIONAL 120 - MEAN BD - FIRST YEAR 1 AD q DPER MEAN 2 Fss g[y gjG NV
.1968 NEAN MIXING ZDNE (LDCATIONS 1, 2, 3, 4. 5, 5, 6, 7.5)
TURBIDITY (NTU) 280- PREDPERATIDNAL MAXIMUM ; 240 - O 200 - PREDPERATIONAL MINIMUM 160 - 0 0 PREDPERATIONAL 120 - MEAN BD - g ' 0 FIRST YEAR 40 0 DPER MEAN o, 0 pyg MY Ag D 1988 MEAN l l i BACKGROUND ZONE I (LOCATIONS 8, 11, 15) TURBIDITY (NTU) 280 - O PREDPERATIDNAL j 240 - O "^ "" I 200 , PREDPERATIONAL MINIM'JM 160 - O PREDPERATIONAL 120 - 0 MEAN f BD - 1 g FIRST YEAR 40 - OPER MEAN ; 3 g a D FB MY AUG N 1988 MEAN Figure 14. Temporal and spatial variations in quarterly mean (of water columin) ! turbidity for discharge, mixing, and background zones during the p(reoperational 9/83-8/84) and period 1988. (1977-1981). first year operational period 52
, DISCHARGE (LDCATION 4)
NITRATE + NITRITE (mg/1) D.700- PREDPERATIDNAL.
.O MAXIMUM 0.600 -
.O 0.500 O PREDPERATIONAL
,.. o grgrgog l 0.400 -
O O PREDPERATIONAL 0.300 - MEAN 0.200 U
-Q U FIRST YEAR 0.100 -
h OPER EAN 0.000 NOV FEB MAY AUG . i MIXING ZDNE (LDCATIONS 1, 2, 3, 4. 5, 5, 6, 7. 5) NITRATE + NITRITE (mg/1) D. 700 ' O PREDPERATIONAL "A " 0.600 - O O O O 0.500 - PREDPERATIONAL MINIM'JM 0, 400 - PREDPERATIDNAL D.300 - 2* MEAN 0.200 " h b i FIRST YEAR D.100 0 " TER EAN n o ., D.000 NOV FEB MAY AUG BACKGROUND ZONE (LDCATIONS 8,' 11, 15) N8TRATE + NITRITE (mg/1) D. 700 - g gg MAXIMUM 0.600 o O O PREDPERATIONAL 0.500 - O MINIgus 0,400 - PREDPERATIDNAL 0,300
-u a MEAN
^
0.200 6 x a 2 FIRST YEAR 0.100 - O x u PER EAN n - 0.000 AUG NOV FEB MAY gy Figure 15. Temporal and spatial variations in quarterly mean and (of water background column) zones nitrate + nitrite for discharge, mixing,981), eriodand (1977-1 first year during the preoperational 3perational period (9/83-8 p/84), 1988. 53
DISCHARGE
-(LOCAT10N 4)
- AMMONIA (mg/1)
PREDPERATIONAL 1.200 - MAXIMUM' O 1.000 -
-. PREDPERATIONAL
-D.800 MIN MW O .
0.600 . O PREDPERATIONAL MEAN
- 0. 400 -
O FIRST YEAR 0.200 'O DPER MEAN FB MXY ALG NV 1998 MEAN 4 MIXING ZONE (LOCATIONS-1. 2. 3. 4. 5. 5. 6. 7. 5) AMMONI A (mg/1) PREDPERATIDNAL 1.200 - MAXIMUM l O 1.000 - 0 0 PREDPERATIONAL 0.800 - MINIMW l O 0.600 . PREDPERATIDNAL MEAN 0.400 - O~ n FIRST YEAR 0.200 - DPER MEAN I- n U O M O FEB MXY AUG NOV 1998 MEAN 4 l' l I BACKGROUND' ZONE (LOCATIONS 8 11. 15) AMMONI A (mg/1) PREDPERATIONAL 1.200 - MAXIMUM O 1.000 ' PREDPERATIONAL 0.800 - MINhMUM 0.600 . O PREDPERATIONAL O MEAN 0.400 - 0 0 FIRST YEAR 0.200 - DPER MEAN
~
;9 MXY AhG NOV gg s
Figure 16. Temporal and spatial variations in quarterly mean (of water column) ammonia for discharge, mixing, and background zones during the first year operational period p(reoperational period 9/83-8/84). and 1988. (1977-1981), 54
g
.DTSCHARGE (LOCATION 4)-
.'ORTHOPHOSPHATE : Cmg/1) ~
PREDPERATIONAL MAXIMUM i' '
.. PREDPE TIDNAL MINIhdM 0.015 -
o .- l PREDPERATIDNAL l O. 010 - (*) MEAN D.005 0 0 0 0 FIRST YEAR DPER MEAN a
- 0. 0%
FEB MAY AUG NOV L MIXING ZDNE (LOCATIONS 1, 2, 3, 4. 5, 5, 6, 7. 5) ORTHOPHOSPHATE (mg/1) PREDPERATIDNAL O- o MAXIMUM
-D.020 '
O PREOPERATIONAL
.41NIMUM 0.015 -
0 0' PREDPERATIDNAL 0.010 - b " " "^ 0.005 O .. : :; FIRST YEAR DPER MEAN a
- 0. MO NOV FEB MAY AUG BACKGROUND ZDNE (LOCATIONS B, 11, 15)
ORTHOPHOSPHATE (mg/1) PREDPERATIONAL MAXIMUM D.020 O 0 0 PREDPERATIDNAL MINIMUM 0.015 - O n O PREDPERATIDNAL 0.010 " Jr; 8 MEAN 22 0.005 0 0 ;; h FIRST YEAR DPER MEAN A D. 0% NOV FEB MAY AUG ae Figure 17. Temporal and spatial variations in quarterly mean (of water column) orthophosphate for dischar the preoperational period e, mixing), and 1977-1981 background
. first zones during year operational period (9/83-8/84). and 19 8.
55 . _ _ _ _ _ _ _ _ _ _ _ . _ _ _ _ _ _ _ _ _ _ _ _ =
j DISCHARGE (LOCAT!ON 4)- .j TOTAL PHOSPHORUS (mg/1) ! D. 090 - PREDPERATIONAL l MAXIMUM j 0.075 - O
~-
PREDPERATIONAL 0.060 - MINIMUM 1 0 D.045 - PREDPERATIONAL MEAN O.030 - O 0.015 - " FIRST YEAR 'l
$ g g OPER MEAN !
.b e w o A 1 l 0.000 FEB MAY AUG NOV l 1988 MEAN i
- l i
l j MIXING ZONE (LOCATIONS 1, 2. 3, 4. 5. 5. 6, 7. 5) TOTAL PHOSPHORUS (mg/1) D.090- PREDPERATIONAL O 'l MAXIMUM D.075 - O PREOPERATIONAL 0.060 ' MINIMUM O
- 0. 045 -
.O o PREOPERATIONAL O
MEAN 0.030 - u ! r FIRST YEAR -1 0.015 " E J o .OPER MEAN D O D U A ! FEB MAY AUG NOV 1986 MEAN i BACKGROUND ZDNE (LOCATIONS 8, 11, 15) TOTAL PHOSPHORUS (mg/1) O.090- PREOPERATIONAL O MAXIMUM 0.075 - O PREDPERATIONAL 0.060 o MINIMUM O 0.045 - o PREOPERATIONAL 0.030 - 0
' ^
0.015 ' E jl [ERMEAN O O O O A 0.000 FEB MAY AUG NOV 1968 MEAN Figure 18. Temporal and spatial variations in quarterly mean (of water column) total phosphorus for discharge, mixin the preoperational period (1977-1981)g, and
, background first year operational zones during period (9/83-8/84), and 1988.
56
- - . _ _ - _ _ . -- - - - -. = - _ - _ _
~
- l. . .
L 'D8SCHARGE q ! (LOCATf0M 4) 1 SILICA' (mg/1) L 7. 0 - PREDPERATIONAL MAXIMUM i 6. 0 - O l -- PREDPERATIDNAL-
- 5. 0 .
g A- MINIMUM-o - PREDP h!DNAL
- 3. 0 MEAN
- O o 0 '
FIRST YEAR
- 1. 0 -
OPER MEAN A
- 0. 0 NOV FEB HAY AUG I
MIXING ZDNE (LOCATIONS. 1, 2,~ ' 3, 4. 5. 5, 6, 7. 5) SILICA (mg/1)
- 7. 0 -
PREDPERATIDNAL MAXIMUM
.S0 -
O 5- o PREOPERATIDNAL
' p, g o a mINIMuu
- 4. 0 -
3, p' O PREDPERATIONAL
- 3. 0 0- O MEAN
- O U
- 2. 0 -
FIRST YEAR
- 1. 0 -
DPER MEAN a
- 0. 0 NOV FEB MnY AUG BACKGROUND ZDNE (LOCATIONS 8, 11, 15)
SILICA (mg/1)
- 7. 0 -
PREDPERATIDNAL MAXIM'JM
- 6. 0 -
O "O PREDPERATIONAL 0
'f p* p MINIMUM
- 4. 0 - j lc O PREDPERATIDNAL 3.00 0 MEAN O
2* O ' FIRST YEAR
- 1. 0 - DPER MEAN A
0 NOV FEB MAY AUG Figure 19. Temporal and spatial variations in quarterly mean (of water column) silica for discharge, mixin and background zones during the first year operational period p(reoperational 9/83-8/84), and 1988. period (1977 g,981). 1 57 4
r. DISCHARGE (LOCATf0N 4) CHLDRIDE (mg/1) - 10.0-PREDPERATIONAL MAXIMUM
- 8. 0 ,
O
..
- PREDPERATIONAL
- 6. 0
- O """
O l -R O u PREDPERATIONAL l' 4. 0 ' y MEAN
. 2. 0 -
FIRST YEAR OPER MEAN
.0 FEB MAY AUG NOV 1986 MEAN l MIXING ZONE (LOCATIONS 1, 2. 3, 4. 5. 5. 6, 7. 5)
CHLDRIDE (mg/1) 10.0 - O PREDPERATIONAL-MAXIMUM B. 0 . O O O u PREDPERATIONAL
. 6. D O MINIMUM O
n . PREDPERATIONAL
- 4. 0 -
MEAN o O O O I 2. 0 - FIRST YEAR i DPER MEAN ' . ' O. 0 FEB MAY AUG NOV 1988 MEAN BACKGROUND ZONE (LOCATIONS 8. 11, 15) CHLORIDE (mg/1) 10.0- PREDPERATIONAL MAXIMUM
- 8. 0 .
O g O PREDPERATIDNAL
- 6. 0 g O MIN MUM
- l. 'n . PREOPERATIONAL
! 4. 0 o g MEAN O O
- 2. 0 -
FIRST YEAR DPER MEAN A
- 0. 0 l FEB MAY AUG NOV l 1988 MEAN Figure 20. Temporal and spatial variations in quarterly mean (of water column) chloride for discharge, mixing, and background zones during the p(reoperational 9/83-8/84), andperiod 1988. (1977-1981), first year operational period 58
_ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ . _ _ _ _ _ _ _ _ . _ _ _ _ . _ _ _ _ _ . - - . . _ . . - _ _ . . - _ . _ _ _ . _ _ .. I
Figure 21. . Surface (0.3 m) chloride values over time for discharge.(Loc. 4), mixing.(Loc. 1.2.3.4.5,6,7.5), and background (Loc. 8.11,15) zones.
. ounrat oc/o
*~ DISCHARGE e
e - 7 - s - 5 3 . 2 - 1
~
0 g@ g@* g@' gM g@\ $4 sM g@' gM gM gd1 gM 10 e . MIXING e - 7 - 6 - 5 - 4 - 3 - 2 - 1 0 g@' g@' g@' gM g@\ gM gM s@' gM gM g@' gM 3D BACKGROUND e - s - 7-- 6 - 5 - 4 - 3 - 2 - 1 0 g@' g@' g@' gM gM gM gM g@' gM gM g#1 gM YEAR 59 u____-_--__. _ - - _ _ - _ - - _ _ - _ _ _ - _ _ _ _ _ - _ _ _ _ _ _ _ _ _ - _ _ _ _ _ _ _ _ - _ _ _ _ - _ - - ._-_-_ ___-_-___-______-__-_-- _ -____ -
DTSCHARGE-(LOCAT20N 4)
.SDDIUM . (mg/1)
- 8. 0 -
PREDPERATIDNAL
- NAX W
- 7. 0 -
- 6. 0 -
- %. -* PREOPERATIONAL O MINIMUM
- 5. 0
- 4. 0
'h O' O O PREDPERATIONAL
- 3. 0 .O O b' O MEAN
. 2. 0 -
FIRST YEAR
- 1. 0 . OPER MEAN A
FEB MAY AUG NOV MIXING ZONE (LOCATIONS 1 '2. 3, 4. 5, 5, 6, 7. 5) SODIUM (mg/1)
- 8. 0 -
O PREDPERAT10NAL
* "^XIMUM
- 7. 0 -
u o , 6. 0 -
- PREDPERATIONAL O MINIMW
- 5. 0 0
,$ 0
- 4. 0 .
O n O PREDPERATIONAL MEAN
- 3. 0 .
- 2. 0 -
FIRST YEAR OPER MEAN
- 1. 0 .
A
- 0. 0 NCV FEB MAY AUG BACKGROUND ZONE (LOCATIONS 8, 11, 15)
SODIUM (mg/1)
- 8. 0 -
PREDPERATIDNAL
- MAXIMUM
- 7. 0 -
4 o
- 6. 0 *
- PREOPERATIONAL O MIN UM j
- 5. 0 -
o
" ' "^'
[g ,6 o o ""'"$'N
- 2. 0 -
FIRST YEAR OPER MEAN
- 1. 0 ,
h
- 0. 0 AUG NOV FEB MAY Figure 22. Temporal and spatial variations in quarterly mean (of water column) sodium for discharge. mixing. and background zones during the reoperational period (1977-1981), first year operational period 9/83-8/84), and 1988.
60 .
DISCHARGE (LOCATTON 4) CALCIUM (mg/l)
.PREDPERATIDNAL
, 5. 0 - MAXIMUM O 4* 0 -
-- PREDPERATIONAL O MINIMUM
- 3. 0 *O h n O e PREDPERATIDNAL
& T 5 O MEAN
- 2. 0 -
0 FIRST YEAR
- 1. 0 -
DPER MEAN A FEB MAY AUG NOV
.c l
. MIXING ZONE (LOCATIONS 1, 2. 3, 4. 5, 5, 6, 7. 5)
CALCIUM (mg/1) PREDPERATID E
- 5. D -
MAXIMUM O
- 4. 0 .
PREDPERATIONAL O . MINIMUM
- 3. 0 O 9 31 PREDPERATIONAL b 5 "E^"
- 2. 0 FIRST YEAR
- 1. 0 '
DPER MEAN a a0 FEB MAY AUG NOV gg s BACKGROUND ZDNE (LDCATIONS B, 11, 15) CALCIUM (mg/1) PREDPERATIONAL i 5. 0 - O MAXIMUM O g, g , PREDPERATIDNAL 0 MINIMUM
- 3. 0 O u O g __ r-*
PREDPERATIONAL h O o MEAN
- 2. 0 U
FIRST YEAR
- 1. 0 '
DFER MEAN A FEB MAY AUG NOV g Figure 23. Temporal and spatial variations in quarterly mean (of water colwnn) calcius for discharge, mixin p(reoperational 9/83-8/84), and 1988. period1981), (1977 g, and background zones during th first year operational period 61 ,
OfSCHARGE (LOCATION 4) MAGNESIUM (mg/D
- 1. 6 -
PREDPERATIDNAL 4 MAXIMUM o
- O l.
- 1. 2 % ..
" 9-
'" h PREDPERATIDNAL
.f g MINIMUM O O
- 0. 8 -
PREDPERATIONAL-MEAN
- 0. 4 -
FIRST YEAR l DPER MEAN A 0 FEB MAY AUG NOV MIXING ZDNE (LOCATIONS.I. 2. 3. 4. 5. 5. 6. 7. 5) MAGNESIUM' (mg/D
- 1. 6 -
PREDPERATIONAL O p O MAXIMUM o" " 21 0
- 1. 2 m
PREDPERATIDNAL g MINIMUM
@ O- 0
- 0. 0 -
O PREDPERAT'DNAL MEAN
- 0. 4 -
FIRST YEAR DPER MEAN A
- 0. 0 FEB MAY AUG NOV BACKGROUND ZDNE CLOCATIONS (8, 11, 15)
MAGNESICM (mg/D
- 1. 6 -
O PREDPERATIONAL O MAXIMUM n O o O
- 1. 2 " 2'
. PREDPERATIONAL h jg MINIMUM' O
O O
- 0. 9 -
O PREDPERATIONAL MEAN
- 0. 4 '
FIRST YEAR DPER MEAN A 0 FEB MAY AUG NOV Figure 24. Temporal and spatial variations in quarterly mean (of water column) magnesium for discharge, mixing. and background zones during the first year operational period p(reoperational 9/83-8/84). andperiod 1988.(1977-1981). l 62
- t l
DfSCHARGE 1 (LOCAT20N 4) PDTASSIUM (mg/l) PREDPEM T! MAXIMLN
- 1. 5 : -- O -
? h PREDPERATIONAL 8
MINIMUM O O
- 1. D PREDPERATIONAL U.
MEAN
- 0. 5 -
FIRST YEAR DPER MEAN A D. D FEB- MAY AUG NOV MIXING ZONE
.- (LDCATIONS 1, 2, 3. 4. 5, 5, 6, 7. 5)
POTASSIUM (mg/l) PREDPERATIONAL 9 MAXIMUM
- g- 9 O
- 1. 5 3 p 2, 4 PREDPERATIONAL ggggggg 6 g O 'I 1* 0 ,
PREDPERATIDNAL-
- g. )
MEAN D. 5 . FIRST YEAR DPER MEAN ! a ! D. D FEB MAY AUG NOV 1966 MEAN 1
)
i BACKGROUND ZDNE i (LOCATIONS 8, 11, 15) POTASSIUM (mg/1) g PREDPERATIONAL MAXIMUM
- 1. 5
-n O PREDPEMTIONAL MINIMUM j 6 g O !
- 1. D .
PREDPERATIDNAL i g MEAN { D. 5 - MRST YEAR DPER MEAN j A ' O. D FEB MAY AUG NOV 88 6 Figure 25. Temporal and spatial variations in quarterly mean (of water column) potassium for discharg(e, reoperational mixing and first period 1977-1981). background year operational zones during the period p(9/83-8/84), and 1988, 63 f
i DXSCHARGE (LDCATf0N 4) IRON Cmg/1) 15.O FREDPERATIDNAL~ MAXIN!.M
-- PREDP TIDNAL MININOM
- 9. 0 -
o PREDPERATIDNAL
- 6. 0 -
MEAN
- 3. 0 FIRST YEAR
,O DPER MEAN o e m A
- 0. 0 p{g gzy ggg ggy 1988 MEAN MIXING ZONE (LOCATIONS 1. 2. 3. 4. 5. 5. 6. 7. 5)
IRON Cmg/1) 15.0- 0 - PREDPERATIONAL MAXIMUM PREDPERATIDNAL MINIMUM
- 9. 0 -
o PREDPERATIDNAL
- 6. 0 -
MEAN
- 3. 0 O FIRST YEAR O FM MUN is _ a FEB MXY AUG NDV 1988 MEAN BACKGROUND ZONE ,
(LOCATIONS (8, 11, 15) IRON (mg/1) 15.0 PRED8'ERATIONAL MAXIMUM PREDPERATIONAL MINIMUM
- 9. 0 -
O PREDPERATIONAL 1( O 0 H AN 0 FIRST YEAR
- 3. 0 -
g o DPER MEAN n u n A O FEIB M'5Y AUG fiDV Figure 26. Temporal and spatial variations in quarterly mean (of water column) iron for discharge, mixing. and background zones during the first year operational period p(reoperational period 9/83-8/84). and 1988. (1977-1981), 64
08SCHARGE (LOCATION 4) MANGANESE ,(mg/1)-
- 5. DO : PREDPEu TIDE L MAxIMug O
' 4. D0 ! ,,
PREOPERATIDNAL MINIMUM 3.00 i O PRE 3PERATIDNAL 2.00 : 1.00,,: FIRST YEAR DPER MEAN
, a b 100' ppg pjy AUG NDV MIXING ZDNE (LOCATIONS 1. 2. 3. 4. 5. 5. 6. 7. 5)
MANGANESE (mg/1) 5.00 - O PREDPERATIDNAL max!Mug L O
- 4. DO PREDPERATIDNAL MINIMUM 3.00 ! O PREDPERATIDNAL 2.00 i O " ^"
^ FIRST YEAR 1.00 : -
DPER MEAN o P. .. A E UU ,kBF pyy ADG NDV s BACKGROUND ZONE (LDCATIONS 8 11. 15) MANGANESE (mg/1) ,
- 5. 00 : PREDPERATIDNAL gAx1 MUM O O
- 4. DO :
PREDPERATIDNAL MINIMUM
- 3. DD i O PREDPERATIONAL 2.00 '
MEAN O FIRST YEAR 1.00-: n DPER MEAN b b EDD'rie Mky~ ^[1G NV Figure 27. Temporal and spatial variations in quarterly mean (of water column) manganese for discharge. mixing, and background zones during the p(reoperational 9/83-8/84), andperiod 1988. (1977-1961), first year operational period 65 I
MCGUIRE NUCLEAR STATION THERMAL PLUME SURVEY INTRODUCTION During August 1988, two special surveys were made of the thermal plume discharged from MNS into lower Lake Norman. The objective of these surveys was to investigate any effect on the thermal plurre caused by an increase in the MNS maximum monthly average discharge temperature limit, from the normal 35.0'C (95.0'F), to 36.1' C (97.0*F). This increase in the discharge temperature limit was allowed only for the month of August, by special request to state regulators. MATERIALS AND METHODS The surveys were performed August 11 and 24 when the MNS daily average discharge temperatures were 35.1*C (95.2*F) and 37.4*C (99.3*F), respectively. Forty-two locations were sampled in each survey (Figure 1). Temperatures were measured using a Hydrolab model 4041 water . quality analyzer on the first survey and a Digitec 5831 digital ther-mometer on the second. Background temperatures were measured at chem-istry sampling location 9.5. Plume acreages were determinea for areas with surface water temperature greater than 2.8'C (5.0*F) above back-ground temperature and for areas greater than 32.2*C (90.0*F). Plume areas were masured with a Micro-Plan II image analysis system. i l 1 1 66
RESULTS AND DISCUSSION 1 The background temperatures for the 1988 surveys were 30.1*C on August 11 and 30.6*C on August 24. On August 11, when the MNS daily average discharge temperature was 35.1*C, the 2.8'C-above-background and the 32.2*C plumes covered approximately 47 ha (116 ac) and 146 ha (362 ac). respectively (Figure 2). On August 24, when the MNS daily average dis-charge temperature was 37.4*C, the 2.8*C-above-background and the 32.2*C plumes covered approximately 314 ha (775 ac) and 676 ha (1670 ac), respectively (Figure 3). This was an incrense in area of 267 ha (659 a_c) for.the 2.8'C-abose-background plume and 530 ha (1308 ac) for-the 32.2*C plume. The acreages of the plumes determined during the 1988 surveys werc somewhat different than those predicted by mathematical modeling (Duke Power Company 1985) and those measured during a survey conducted on August 30, 1984 (Foric, memo to file,1984) (Table 1). In 1988, the areas of the 2.8*C-above-background . plumes were smaller than those of the 32.2 C plume. That was the reverse of the two examples from previous years. This situation was probably due to the higher background temperatures in 1988 which resulted in the 2.8'C-above-background plume having temperatures higher than 32.2*C. 1hase higher temperatures would normally produce smaller plumes. 67 _.._______.___.2_ a.._________m-__-_.__
t i l LITERATURE CITED
~.
l. Duke Power Company. 1985. McGuire Nuclear Station 316(a). Demonstration. Duke Power Company, Charlotte, NC 1 I l i 68
. 1
________________J
y- a 0 ) 6 6 g* ( 1 3 3 1 a2 ( 6 ( ( 5 r a ( . 8 e2h 0 6 6 9 v3 3 5 4 7 1 o 4 2 1 6 C , n o i t d a n r u t o ) - s r 0 ) ) ) n g 3 1 6 5 o ek) 5 7 1 7 m mcc uaa 1 ( 2 1 7 e ( ( ( D l b( P> 0 0 4 )
. Ca 2 1 7 1 a
' h 6 1 4 3 (
8 6 1 2 3 n n
. )
3
) ) o 3 1 i o d e ) . t i nr) 4 3 8 7 a t uuF 8 8 8 8 t a
S t ot r a gr
"( ( ( ( ( S 0 5 3 6 r k eC a r cp a
e 8 e am' 9 2 2 8 1 3 0 3 i c c l T u c N u N ) ) ) e e ee ) 3 0 1
. i r
r gr) 6 9 5 8 u i ruF 9 8 9 9 G u at* ( ( ( ( c G h a( M c cr 5 8 0 7 M seC p m i 5 1 5 6 o r o D m' e 3 3 3 3 r f f T a s t n a o d d i a 0 8 8 8 t l a L o% 9 9 9 9 i d m n r o e T) ) ) ) ) c h F 6 5 7 4 t a* 1 1 . r d t( ( ( 4 6 e e l eC 9 1 1 m 3 ( ( m r d* u u 8 8 2 1 s s . a 8 9 e e m m e d r r t n e x a s . e nwM 2 2 2 2 d e eoP 3 3 3 3 r t dl G 0 0 0 0 o nFK 2 2 2 2 f c o i C d d e e t r c P i l ) d a a e c ( r 1 i n 4 8 8 p tl o 8 8 8 e y aei / / / l d mdt 0 1 4 b u eoc 3 1 2 ) a t hMi / / / a T S t d 8 8 8 (
. a e M r P
3 8 g
!l)
95 g
? .,
/'
0 4 9 4 M)' y q, L' V r Y eiv
,VI pg # l
. ss :,
a os .m I N 7*
- e x3
*u d
, S J2 4
yvs . . . . ,
~'
Cowans
- . qp Ford intakeg
- Dam 5 c' rt
?
McGuire Nuclear ' discharge Station 3 1 { Figure 1. Sampling locations used during the thermal plume I surveys on August 11 and 24, 1988 for the McGuire Nuclear Station. l 70
.__-____________-_________________________________:___-_-___D
^
~.
O l .. krs a L- _ t , & ' N ./
<d 1
1 2 l
. h N a
(, "'; ' I Cowans Ford intake g Dam 3 u idischarge St& tion Figure 2. Surface isotherms (2.8'C above background (----) and 32.2*C ( )) of the thermal plume from McGuire Nuclear Station on August 11, 1988. 71
~.
# \
e o
;w 3
t i t u c' N o 6 g" j , g f E i S
}
s Q l i U i
/ 9/ '
f
~
Cowans intake - I I rord Dam R
- McGuire t discharge Nuc l e a r' Station Figure 3. Surface isotherms (2.8*C above background (----) and 32.2*C ( )) of the thermal plume from McGuire Nuclear Station on August 24, 1988.
( 72 { \ i
l l
~
PHYTOPLANKTON
~
INTRODUCTION Previous studies on Lake Norman have reported considerable spatial and temporal variability in phytoplankton standing crops and taxonomic composition (Duke Power Company 1976, 1985; Menhinick and Jenson 1974; Rodriguez 1982). Rodriguez (1982) classified the lake as oligo-mesotrophic based on phytoplankton abundance, distribution, and taxonomic composition. The objectives of the Lake Norman Maintenance Monitoring Program are to:
- 1. Describe quarterly patterns of phytoplankton standing crop and species composition throughout Lake Norman, and
- 2. Compare phy toplankton data collected during this study (February, May, August, November 1988) with historical data collected during these months.
METHODS AND MATERIALS Quarterly phytoplankton sampling was conducted at Locations 2.0, 5.0, 8.0, 9.5, 11.0, 13.0, 15.9, and 69.0 (Chemistry, Figure 1). Duplicate composite grabs from 0.3, 4.0, and 8.0 m (i.e., the euphotic zone) were taken at all locations, with the exception of Location 69.0 where grabs from 0.3. 3.0, and 6.0 m were taken due to the shallow depth at 73 . i
- that location. Sampling was conducted on 2 February, 5 May, 4 and 8 August, and 22 November 1988. Standing crop (density and biovolume) and taxonomTc' composition were determined for samples collected at Locations 2.0, S.0, 9.5,11.0, and 15.9; chlorophyll a, concentrations were determined for samples from all locations. Field sampling meth-ods, and laboratory methods used for chlorophyll, standing crop, and taxonomic composition determinations were identical to those used by Rodriguez (1982).
Chlorophyll a data for February, May, August, and November 1988 were compared with historical data beginning in 1975. Derisity and biovolume , data for 1988 were not compared to data prior to 1978 due to signifi-cant changes in sample analysis after 1977. RESULTS AND DISCUSSION Standing Crop Phytoplankton chlorophyll a and standing crop values generally demon-strated a trend of increasing concentrations from downlake to uplake locations, with the exception of biovolume values in August and i November (Tables 1 through 5; Figure 1). Biovolume values during these months showed considerable variability. Similar trends of increasing i standing crop values from downlake to uplake locations have been observed in previcus Duke Power studies (Duke Power Company 1976, 1985; Roriguez 1982). 74
r - - ------ V i l Phytoplankton standing crops during February, May August, and Novem-ber of 1988 were generally within ranges of those observed during these months of previous years (Figures 2 through 5). Density and biovolume values at Locations 11.0 and 15.9 in February 1988 were considerably higher than in previous Februarys. At. Location 15.9, both density and biovolume values were somewhat higher in May 1988 than.in previous Mays. At Locations 11.0 and 15.9 in August 1988, the chloro-phyll concentrations were somewhat lower than in previous Augusts. No specif M treno:: of densities or bio-volumes could be identified at these locations in August due to extreme variability among these parameters during previous years. No long-term trends could be identi-fied at Locations 9.5 and 69.0 due to the paucity of historical data from these locations. Community Composition Ten classes comprising 84 genera and 175 species of phytoplankton have been identified from samples collected on Lake Norman since the Maintenance Monitoring Program was initiated in August 1987. The distribution of species within classes was as follows: Chlorophyceae, 91; Bacillariophyceae, 34; Chrysophyceae, 15; Haptophyceae and Xanthophyceae, 1 each; Cryptophyceae, 4; Myxophyceae, 14; Euglenophyceae, 5; Dinophyceae, 7; and Chloromonadophyceae, 3 (Table 6). Thirty-three taxa have been identified during the Maintenance Monitoring Program which were not recorded during previous studies 75 ______________.m,_ . . - - - - - - . - - - - - -
(Duke Power Company 1976, 1985; Menhinick and Jensen 1974; Rodriguez 1982). The major classes during February, in terms of density, were the Bacillariophyceae (diatoms), Cryptophyccae (cryptophytes), and Chrysophyceae (golden-brown algae). During May, the cryptophytes were most important, followed by the golden-brown algae and the diatoms. In August, the green algae were most abundant, with the Flyxophyceae (blue-green algae) and golden-brown algae ranking second and third, respectively. The diatoms were most abundant in November, followed in importance by cryptophytes and green a'.gte (Table 7). In tenns of biovolume, the diatoms dominated samples during all periods except August, when the Dinophyceae (dinoflagellates) often dominated phytoplankton biovolumes. Similar taxonomic composition was observed during February, May, August, and November of the preoperetional and operational periods. No algae have been recorded as " unknowns" during the Lake Ronnan Maintenance Monitoring Program. Prior " unknowns" have since been identified primarily as members of the Chrysophyceae (i.e., Erkinia, unidentified chrysophytes, etc.). This also accounts, in large part, for the apparent increase in the relative abundance of chrysophytes during the current study. The blue-green algae were more abundant during August 1988 than during previous Augusts, due primari-ly to high densities of blue-greens observed from replicates collected at Location 15.9. Species composition among phytoplankton samples collected during 1988 was generally similar to that observed for samples collected during 76 _.____-.__--_-_._---J
I l the preoperational and operational periods. Rhodomonas, a small cryptophyte, was usually among the most abundant taxa observed at locations on Lake Norman throughout the 1988 monitoring study. Melo-l sira (primarily M. ambigua), a centrate diatom, was often an important constituent of phytoplankton assemblages during all sample periods except August Green algal taxa, primarily Cosmarium asphearosporum v. strigosum, a small desmid, and Dictyospearium pulchellum, a colonial alga, dominated phytoplankton assemblages in August. At Location 15.9 in August, Oscillatoria and Raphidiopsis, filamentous blue-greens, were codominants, accounting for over 25% of the phytoplankton den-sity. Melosira ambigua, which was not reported in previous Duke Power studies (Rodriguez 1982), had been previously identified as M. italica and M. italica v. tennt, ..w . according to Duke Power Company's diatom taxomony consultant, Dr C. W. Reimer of the Philadelphia Academy of Science. There are, as yet, no oW future phytoplankton studies planned for Lake Noman. We will continue to perform quarterly maintenance mon-itoring as described in this report.
SUMMARY
Phytoplankton sampling was conducted at Locations 2.0, 5.0, 8.0, 9.5, 11.0,13.0, h.9, and 59.0 on Lake Norman in February, May, August, and November 1988. Chlorophyll a analyses were performed at all 77 u____mm.________.._____ __.__--
f: L I locations, while standing crops and taxonomic composition were -deter-mined at Locations 2.0, 5.0, 9.5, 11.0, and 15.9. Phytoplankton standing crops generally showed a trend of increasing values from downlake to uplake locations. This trend was also observed during previous studies on Lake Norman. Phytoplankton standing crop values during sampling months of 1988 were usually within ranges of l 1 those observed during these months of previous years, except that densities and biovolumes at Locations 11.0 and 15.9 in February 1988 were considerably higher than in previous Februarys, while chlorophyll concentrations ' at these locations in August 1988 were somewhat lower than in previous Augusts. L Phytoplankton taxonomic composition during sampling months of 1988 was usually similar to that observed during these months of previous studies, with diatoms, cryptophytes, golden-brown algae, and green algae among the l most abundant forms. Diatoms dominated phytoplankton biovolumes in all months but August, when dinoflagellates were dominant. Major species observed during 1988 were similar to those observed during previous studies. Most exceptions were due to recent identifications of unknowns, and new taxonomic information on previously identified species. 78
LITERATURE CITED Duke Power' Company. McGuire Nuclear Station, Units 1-and 2, Environ-mental Report, Operating License Stage. 6th rev. Volume 2. Duke Power Company, Charlotte, NC.1976. Duke Power Company. McGuire Nuclear Station, 316(a) Demonstration.
> ' Duke Power Company, Charlotte, NC.1985.
Menhinick, E. F. and L. D. Jensen. Plankton populations, p. 120-138 3 - L. D. Jensen (ed.). Environmental responses to thermal discharges from Marshall Steam Station, Lake Norman, Noth Carolina. Electric Power Research Institute, Cooling Water Discharge Project (RP-49) Report No.11. Johns Hopkins University, Baltimore, MD. 235 p.; 1974. Rodriguez, M. S. Phytoplankton, p. 154-260 h J. E. Hogan and W. D. Adair (eds.). Lake Norman summary, Technical Report DUKEPWR/82-02 Duke Power Company, Charlotte, NC. 460 p.; 1982. 79 _ _ . _ . _ . _ _ _ . _ _ _ _ . . . . _ _...________m_ _ _ _ . _ _ _ _ _ _ . _ _ _ _ . _ _ _ . _ _ _ _ _ _ _ _ _
Table 1 op Phyj/m}anktontotaldensity(units (mm /ml),andbiovolume
), as well as major class densities and biovolumes, and percent composition (in parenthesis) at each location for samples collected on 2 February 1988.
Locations Parameter 2.0 5.0 9.5 11.0 15.9 Total densi ty 942 1,065 1,184 2,874 3,513 Chlorophyceae 73 151 118 269 539 (7.7) (14.1) (9.9) (9.4) (15.3) Ba cillario- 383 306 392 1,092 + 1,530 phyceae (40.6) (28.7) (33.1) (38.3) (43.5) Chrysophyceae 163 221 307 538 532 (17.3) (20.7) (25.9) (18.8) (15.1) Cryptophyceae 245 314 310 830 757 (26.0) (29.4) (26.1) (29.1) (21.5) Myxophyceae 12 45 12 24 69 ! (1.2) (4.2) (1.0) (0.8) (1.9) Others
- 66 28 45 94 86 (6.9) (2.9) (4.0) (3.3) (2.7)
Total biovolume 1,143 911 933 2,101 2,683 Chlorophyceae 11 17 32 38 89 (0.9) (1.9) (3.3) (1.8) (3.3) Bacillario- 587 640 591 1,155 1,793 phyceae (51.3) (70.2) (63.3) (54.9) (66.8) Chrysophyceae 92 37 68 148 166 (8.0) (4.0) (7.2) (7.0) (6.1) Cryptophyceae 116 117 55 259 298 (10.1) (12.8) (5.9) (12.3) (11.1) Myxophyceae 8 20 9 6 6 (0.7) (2.1) (0.9) (0.2) (0.2) Others 329 80 178 495 331 (28.6) (9.0) (26.9) (23.8) (12.5)
* = Includes primarily the Dinophyceae, which were found at all i locations; and the Haptophycae, which were found at all but l Location 11.0.
( 80 l
Table 2'
'(mm /m}ankton total density (units /ml), and biovolumePhyjop )
and percent composition (in parenthesis) at each location for samples collected on 5 May 1988. Locations Parameter 2.0 5.0 9.5 11.0 15.9 Total density 904 1,198 1,681 1,610 2,524 Chlorophyceae 102 135 63 66 45 (11.2) (11.2) (3.7) (4.0) (1.7)
'Bacillario- 323 '417 340 310 312 phyceae (35.7) (34.8) (20.2) (19.2) (12.3)
Chrysophyceae 129 289 484 611 1.045 (14.2) (24.1) (28.7) (37.9) (41.4) Cryptophyceae 302 331 699 578 1,064 (33.4) (27.6) (41.5) (35.9) (42.1) Myxophyceae- 40- 11 30 4 4 (4.4) (0.9) (1.7) (0.2) (0.1) Others
- 8. 15 65 41 54 (0.8) (1.2) (3.8) (2.8) (2.4)
Total biovolume 673 1,158 943 1,163 1,071 Chlorophyceae 13 32 10 17 7 (1.9) (2.7) (1.0) (1.4) (0.6) Bacillario- 523 855 653 572 403 phyceae (77.7) (73.7) (69.2) (49.1) (37.6) Chrysophyceae 26 57 84 95 162 (3.8) (4.9) (8.9) (8.1) (15.1) Cryptophyceae 79 98 114 103 316 (11.7) (8.4) (12.0) (8.8) (29.5) Myxophyceae 14 il 2 <1 2 (2.1) (60.1) (0.2) (< 0.1 ) (0.2) Others 18 116 80 376 181 i' (2.8) (10.0) (8.7) (32.6) (17.0)
* = Dinophyceae at all locations; Haptophyceae at Locations 9.5,11,0 and 15.9; Chloromonadophyceae at Location 11.0.
I 81
-__s-___ ______ - _ _ _ - - . _ _ _ _ - - _ _ _ _ _ _ _ _ _ _ . _ _ _ . _ _ _ _ _ . _ . . _ . - - - _ _ _ _ _ _ -
l Table 3 - op Phyj/m}ankton (mm ), as welltotal density as major class(units /ml), and densities biovolume and biovolumes and percent composition (in parenthesis) at' each location, for samples collected on 4 and 8 August 1988. Locations parameter 2.0 5.0 9.5 11.0 15.9 Total densi ty - 2,828 2,882 3,138 3,070 8,408 Chlorophyceae 1,078 1,370 1,405 1,555 1,823 (38.1) (47.5) (44.7) (50.6) (21.6) Baci11ario- 408 311 342 280 1.341 phyceae (14.4) (10.7) (10.8) (9.1) (15.9) Chrysophyceae 423 637 693 440 876 (14.9) (22.1) (22.0) (14.3) (10.4) Cryptophyceae 576 258 460 514 870 ' (20.3) (8.9) (14.6) (16.7) (10.3)
'Myxophyceae 251 202 226 226 3.413 (8.8) (7.0) (7.2) (7.3) (40.5)
Others
- 92 104 12 55 85 (3.5) (3.8) (0.7) (2.0) (1.3)
Total biovolume 1,794 2,092 894 1,585 2.275 Chlorophyceae 128 161 190 408 329 (7.1) (7.6) (21.2) (25.7) (14.4) Bac111ario- 437 348 331 169 767 phyceae (24.3) (16.6) (36.9) (10.6) (33.7) Chrysophyceae 86 144 151 82 131 (4.7) (6.8) (16.9) (5.1) (5.7) Cryptophyceae 246 148 158 240 247 (13.6) (7.0) (17.7) (15.1) (10.8) Myxophyceae 47 38 48 90 473 (2.6) (1.8) (5.3) (5.6) (20.7) Others 850 1,253 16 596 328 (47.7) (60.2) (2.0) (37.9) (14.7)
* = Dinophyceae at all locations; Haptophyceae at all but Location 11.0; Euglenophyceae at Location 15.9; Chloromonadophyceae at Location 5.0.
82
--a-m_-___-_-------_---_u__---__ a-__ - - - _ - _ - - -_ - _ _ - - _ - - - - . - - - - - - - - - - - - - - - - - -
Table 4 op Phyg/m}ankton (mm ), as welltotal density as major class (units /ml), and densities andbiovolumebiovolumes - and percent composition (in parenthesis) at each location for samples collected on 22 November 1988. Locations Parameter 2.0 ; .0 9.5 11.0- 15.9 Total. density 1,305 1,035 1,035 1,280 2,551 Chlorophyceae 184 122 175 171 712 (14.0) (11.7) (16.9) (13.3) (27.9) Baci11ario- 627 379 518 510 503 phyceae (48.0) (36.6) (50.0) (39.8) (19.7) Chrysophyceae 110 159 179 122 393 (8.5) (15.3) (17.2) (9.5) (15.4) Cryptophyceae 352 335 151 445 792 (27.0) (32.3) (14.5) (34.7) (31.0) Myxophyceae 24 28 12 24 106 (1.8) (2.7) (1.1) (1.8) (4.1) Others
- 8 12 0 8 45 (0.6) (1.1) (0) (0.6) (1.6)
Total biovolume 2,034 1,252 1,564 1,388 2,001 Chlorophyceae 27 26 49 39 236 (1.3) (2.1) (3.1) (2.8) (11.7) Bac111ario- 1,891 1,060 1,435 1,122 1,041 phyceae (92.9) (84.6) (91.7) (80.7) (52.0)- Chrysophyceae 20 26 28 14 50 (0.9) (2.1) (1.8) (1.0) (2.5) Cryptophyceae 67 88 42 173 318 (3.3) (7.0) (1.8) (12.4) (15.8) Myxophyceae 8 21 10 19 139 (0.4) (1.6) (0.6) (1.3) (6.9) Others 21 31 0 21 217 (1.0) (2.6) (0) (1.5) (11.1)
* = Dinophyceae at all but Location 9.5; Haptophyceae at Location 15.9 83
__m_.____.____m____ _.____. _ _ - _ _ _ _ _ _ _ _ _ _ _ _ _
I Table 5 ' Chlorophyll- a concentrations (ag/m3 ) from samples collected at locations in Lake Norman on 2 February, 5 May, 4 and 8 August, and 22 November 1988. Months locations February May August November 2.0. 2.58 1.68 4.56 3.63 5.0 2.66 2.37 4.40 3.39 8.0 2.58' 2.15 3.96 3.75 9.5 2.58 2.82 3.88 3.71 11.0 4.32 3.11 2.90 3.95-13.0 5.44 2.90 3.63 3.95 15.9 6.74 3.43 3.59 6.03 69.0 4.12 3.91 10.46 6.54 84
Page 1 of 4 Table 6 Phytoplankton taxa identified from Lake Norman samples collected on 4 August, 5 November 1987, 2 February, 2 May, 4 and 8 August, and 22 November 1988 (*= taxon not recorded in previous Lake Norman studies). CHLOROPHYCEAE Actinastrum hantzschii Lagerheim Ankistrodesmus falcatus (Corda) Ralfs A. falcatus v. mirabilis (Corda) Ralfs X. _falcatus v. tumidus (West & West) G. S. West X. spiralis (Turner) Lemmerman Xrthrodesmus incus (Breb.) Hassall
- Ca rteria frizschii Takeda C. spp. Diesing chlamydomonas spp. Ehrenberg Chlorogonium spp. Ehrenberg Closteriopsis longissima v. tropica West & West Closterium incurvum Brebisson Coelestrum cambricum Archer
- Cosmarium angulosum v. _concinnum (Rabenhorst) West & West C. asphearosporum v. strigosum Norstedt
- t, contractum Kirchner
- t. polygonum (Naegeli) Archer
- T. tenue Archer
- t. tinctum Lundell T. spp. Corda trucigenia crucifera (Wolle) Collins C. irregulare Wille T. tetrapedia (Kirchner) West & West Dictyosphearium ehrenbergianum Neageli D. pulchella Wood Elaxatothrix gelatinosa Wille Eauastrum spp. Ehrenberg
- Eudorina elegans Ehrenberg Franceia droescheri (Lemmerman) G. M. Smith F. ovalis (France) Lemmerman 31oeocystis planktonica (West & West) Lemmerman G.
E. gigas (Kuetzing) Lagerheim spp. Neageli Eolenkinia paucispina West & West G. radiata (Chodat) Wille tonium sociale (Dujar.) Warm. Kirchneriella contorta (Schmidle) Buhlin K. lunaris (Kirchner) Moab. K. obesa (W. West) Schmidle R. subsolitaria G. S. West C spp. Schmidle
- Tagerheimia. ciliata (Lagerheim) Chodat L. longiseta (Lemmerman) Printz E. subsala Lentnerman Resostigma viride Lauterborn Micractinium pusillum Fresenius 85
Table 6 (continued) Page 2 of 4 Mougtotia elongatum (Agardh) Wittrock M. spp. (agardh) Wittrock Rephrocytium agardhianum Neageli
- N. limneticum (G. M. Smith) G. M. Smith
- Docystis elly]tica W. West O. lacustris Chodat D. pa rva West & Wes t bdorina charkowiensis Korshikov Pediastrum biradiatum Meyen P. duplex Meyen
- 7. obtusum Lucks P. tetras (Ehrenberg) Ralfs P. tetras v. tetroadon (Corda) Ralfs 71anktospheara gelatinosa G. M. Smith Quadrigula lacustris (Chodat) G. M. Smith Scenedesmus abundans (Kirchner) Chodat
- 5. abundans v. asymetrica (Shroeder) G. M. Smith
- 3. abundans v. brevicauda G. M. Smith
- 3. acuminatus (Lagerheim) Chodat
- 3. annatus v. bicaudatus (Gugliell-Printz) Chodat
- 3. bijuga (Turpin) Lagerheim
- 3. bijuga v. alterans (Reinsch) Hansgirg
- 3. denticulatus Lagerheim
- 3. dimorphus (Turpin) Kuetzing
- 3. incrassulatus
- 3. quadricauda (Turpin) Brebisson Telenastrum minutum (Neageli) Collins
- 5. westii G. M. Smith 3phearocystis schroeteri Chodet Sphearozosma granulata Roy & Bliss Staurastrum americanum (West & West) G. M. Smith
- 5. apiculatum Brebisson
- 3. brevispinum Brebisson
- 3. curvatum v. elongctum G. M. Smith
- 3. cuspidatum Brebisson
- 3. dejectum Brebisson
- 3. dickeii v. rhomboideus West and West
- 3. manfeldtii v. fluminense Schumacher
- 3. megacanthum Lundell
- 3. iaradoxum v. cingulum West & West
- 3. paradoxum v. parvum W. West
- 3. subcruciatum Cooke & Wille
- 3. tetracerum Ralfs
- 3. turc escens Denot
- Tetraec ron arthrodesmiforme v. contorta Woloszynska T. caudatum (Corda) Hansgirg j T caudatum v. longispinum Lemerman i T. minimum (A. Braun) Hansgirg j
- T. muticum (A. Braun) Hansgirg T. regulare v. incus Teiling T. spp. Kuetzing Truebaria setigera (Archer) G. M. Smith Westella linearis G. M. Smith 86
Table 6 (continu:d) Page 3 of 4 BACILLARIOPHYCEAE Achnanthes microcephaly (Kuetzing) Grunow A. spp. Bory Inomoeonisyitrea(Grunow)Ross Asterionella fonnosa Hassall Attheya zachariasi J. Brun Cocconeis placentula Ehrenberg Cyclotella meneghiniana Kuetzing C. pseudostelligera Hustedt C stelligera (Cleve) Van Huerck lymbella turgida Gregory C. spp. Agardh - Tragilaria crotonensis Kitton
- Frustulia rhomboides (Ehrenberg) De7oni
- Melosira ambigua (Grunow) O. Muller M. distans (Ehrenberg) Kuetzing R. granulata (Ehrenberg) Ralfs R. .granulata v. angustissima Mueller R. italica (Ehrenberg) Kuetzing M. spp. Agardh Witzschia acicularis (Kuetzing) W. Smith N. agnita Hustedt R~ holsatica Hustedt
. R. alea (Kuetzing) W. Smith
- W. su nearis Hustedt W.spp. Hassall Whizosolenia spp. Ehrenberg Skeletonema potemos (Weber) Hasle Stephanodiscus spp. Ehrenberg Synedra acus Kuetzing S. planktonica Ehrenberg
- 3. rumpens Kuetzing
- 3. rumpens v. fragilarioides Grunow
- 3. rumpens v. scotica Grunow l
- 3. ulna (Nitzsch) Ehrenberg
- 3. spp. Ehrenberg Tabe11 aria fenestrata (Lyngby) Kuetzing T. flocculosa (Roth) Kuetzing CHRYSOPHYCEAE Chromulina spp. Cienkowski Dinobryon bavaricum Imhof D. sertularia Ehrenberg D. spp. Ehrenberg
- Yrkinf a subaequiciliata Skuja Kephyrion rubi-klaustri Conrad Mallomonas pseudocoronata Prescott M. tonsurata Teiling R spp. Perty Uchromonas spp. Wyssotzki
- Rhizochrysis spp. Pascher Stelexomonas dichotoma Lackey Synura spinosa Korshikov 87 k -.--__.-_-___________w
Table 6 (continued) Page 4 of 4 S. ulvella Ehrenberg l
- Broglenopsis americana (Calk) Lememan HAPTOPHYCEAE Chrysochromulina parva Lackey XANTH 0PHYCEAE Dichotomococcus spp. Korshikpv CRYPTOPHYCEAE Cryp?snonas erosa Ehrenberg C. ovata Ehrenberg
- f. reflexa Skuja Rhodomonas minuta Skuja MYXOPHYCEAE Agmenellum quadriduplicatum Brebisson Anabaena wisconsinense Prescott A. spp. Bory
- throococcus limneticus Lemmerman
- C. minor Kuetzing
- 7. spp. Neageli Eomphosphearia lacustris Chodat Lyngbya spp. Agardh
+ Microcystis aeruginosa Kuetzing Oscillatoria geminata Meneghini
- 0. limnetica Lemerman D. spp. Vaucher i
Thormidium spp. Kuetzing Raphidiopsis curvata Fritsch & Rich EUGLENOPHYCEAE Euglena spp. Ehrenberg
- Lepocinclus spp. Perty l
- Trachelomonas acanthostoma (Stokes) Deflandre T. pulcherrima Playfair l T. volvocina Ehrenberg DINOPHYCEAE Ceratium hirundinella (Mueller) Schrank l
- Glenodinium boroei (Lemmerman) Schillcr i
G. palustre WTTing Teridinium aciculiferum Lemerman P. inconspicuum Lemmerman
- 7. pusillum (Pennard) Lemmerman
- 7. wisconsinense Eddy 1
CHLOR 0 MONAD 0PHYCEAE Gonyostomum depressum (Lauterborne) Lemerman G. latum Iwanoff
- 3. spp. Deising
+=
Not recorded from previous studies, but blooms have been observed uplake outside monitored areas. 88 u_,_,_,_____________----------- -
L' Page 1 of 2 Table 7 List of algal classes observed in samples collected on Lake Norman and their percent composition during part of the-preoperational period (February, May, August, November 1978-1981), the operational period (these months of 1982-84), August / November 1987, and February 1987, and February, May August, and November 1988 (NS .= not sampled). Density Percent Composition Taxon May February 78-81 82-84 1987 1988 .78-81 82-84 1987 1988 Chlorophyceae 22.2 10.6 Ns TE'6 24.3 F Ns Tf Bacillariophyceae 44,0 41.2' 38.8 41.0 22.4 21.5 Ch rysophyceae 1.4 4.6 18.4 2.3 9.4 32.3 Haptophyceae 0 0 0.8 1.1 0 1.2 Xanthophyceae 0 0 0 0.6 0.2 0 Cryptophyceae 19.9 33.2 25.7 19.7 23.5 37.5 Myxophyceae - 0.2 0.3 1.7 3.2 7.6 1.1 Euglenophyceae (0.1 (0.1 0 (0.1 0.2 0 Dinophyceae 0.4 0.8 2.4 1.1 0.8 1.0 Chloromonadophyceae 0 0 0 0 0 (0.1 Unknowns 11.6 9.0 0 6.6 8.2 0~ Biovolume Percent Composition Chlorophyceae 1.4 1.6 2.4 6.4 1.5 1.6 Bacillariophyceae 81.7 55.2 61.3 49.8 23.9 60.0 Chrysophyceae 0.6 0.9 6.6 5.8 14.8 8.5 Haptophyceae 0 0 0.1 0 0 0.2 Xantophyceae (0.1 0 0 0 0.1 0 Cryptophyceae 7.8 15.6 10.9 22.1 44.4 14.2 Myxophyceae 0.9 0.4 0.6 3.7 C.3 0.4 Euglenophyceae 0.2 0.3 0 0 0.6 0 Dinophyceae 5.0 23.3 18.0 6.7 10.0 13.4 Chloromonadophyceae 0 0 0 0 0 1.6 Unknowns 2.2 2.5 0 5.3 4.4 0 89
L Table 7(continued)- pa9e 2 of 2 Density Percent Composition Taxon May Februa ry 78-81 82-84 1987 1988 78-81 82-84 1987 1988 Chlorophyceae 58.7 44.0 66.3 35.6 24.3 i 27.7 28.3 18.9 Baci11ariophyceae 9.6 25.4 15.4 13.2 41.0 22.4 22.9 35.2 Chrysophyceae 3.2 5.0 3.7 15.1 2.3 9.4 16.3 13.2 Ha ptophyceae 0.3 0 0 0.4 1.1 0 2.1 0.3 Xanthophyceae 0 0.1 0 0 0.6 0.2 0.1 0 Cryptophyceae 11.5 10.6 7.0 13.2 19.7 23.5 21.1 28.8 Myxophyceae 6.5 2.7 5.6 21.2 3.2 7.6 8.3 2.7 Euglenophyceae 0.4 0 0 0.3 (0.1 0.2 0.1 0 Dinophyceae 3.4 2.5 2.1 1.0 1.1 0.8 0.3 0.7 Chloromonadophyceae 0 0 (0.1 (0.1 0 0 0.3 0 Unknowns 6.5 9.8 0 0 6.6 8.2 0 0 Biovolume Percent Composition Chlorophyceae 11.2 10.8 20.2 14.1 6.0 6.9 12.3 4.6
' Ba cillariophyceae 8.6 7.7 15.3 23.7 49.4 . 34.2 46.2 79.5 Chrysophyceae 1.3 2.6 1.7 6.9 2.2 13.2 5.9 1.7 Haptophyceae 0.1 0 0 0.1 0.4 0 0.3 X0.1 Xantophyceae 0 (0.1 0 0 (0.1 0.1 (0.1 0 Cryptophyceae 6.6 3.8 8.1 12.0 25.9 15.5 13.6 8.3 Myxophyceae 11.5 3.3 6.7 8.0 1.9 7.8 12.0 2.4 Euglenophyceae 1.8 0 0 1.6 0.2 4.6 0.7 0 Dinophyceae 57.8 70.2 47.6 33.2 12.8 14.7 5.2 3.5 Chloromonadophyceae 0 0 0.4 0.4 0 0 3.7 0 Unknowns 1.1 1.5 0 1.2 0 2.9 0 0 90
I Sarpling Locations Sarpling Locations
,,,i s a s.,s 9.o 13,o iss se,0 2 s e es its is,s os.o ts.s
- : vna ; ; nue
)
{. o
> - - - = m ay ---.m noy
.E a- 8 4
-* .a J.
1 EL ,' a'
@ = - - - - I' o
J __ x-.w,,..- x ,, , . .
", N '
I. x-u 0-12 -- E e g. / o
/
x
= ~
c
.E
>.4 t- _
+
,z . .
a x- - "~ x ~ n. . x ~ , , ,,, . .
- 0-
~'
x a 2 g ,x E ,# E '. , w s y - i, 2 ,'o a y- - . = - - _ _ _ , n
)1 O
> e' 9
m 3 . . . . 0 10 20 30 40 0 10 20 30 40 DISTANCE FROM C0WAN'S FORD DAM (km) Figure 1 Phytoplankton standing crops in Lake Norman during February, May, August, and November 1988. 91 y
LOCATION 2.0 is - to - l s - o LOCATION 5.0 is to -
"E fs -
~
~
01 s d LOCATION 8.0 2 ts - Q. E O g to - u s - r : 3 o LOCATION 9.5 to - s - o e o
- i 76 78 80 82 84 86 86 76 76 B0 82 84 B6 se FEBRUARY MAY figure 2 Lake Norman chlorophyll a concentrations coserved in February and May of each year, when sampling was conducted, from 1975 to 1988.
Values-represent composites of the euphotic zone. 92
LOCATION 11.0 ss r to - 4 0 s - o LOCATION 13.0 is - 7 10 = E N o
= A E s -
- at l
/
d o y LOC ATION 15.9 ts - u ,a . e o LOCATION 69.0 is - to - s - e
, ,,,,,,,,,,,,,, o 78 78 80 82 84 86 88 76 78 80 82 84 46 88 FEBRUARY MAY Figure 2 (continued) 93
\l ~ r
is - LOCATION 2.0 - to - 5 - o'
/
N / is - LOCATION 5.0 E 10 - A E s -
.J J
E'o LOCATIO N 8.0
$ at O
N o to - e-- s - \ o ts - LOCATION 9.5 10 - s - N
/
7s te so as as as as n n so sa at es as AUGUST NOVEMBER Figure 3 1.ake Norman chlorophyll a concentrations observed in August and November of each year, den sampling was conducted, from 1975 to 1988. Values represent composites of the euphotic zone. 94 _ . _ _ _ . _ _ . _ _ _ _ _ _ _ _ _ _ _ . _ _ _ _ . _ _ _ _ _ . _ _ _ _ _ _ __._____ _ _ m
i LOCATION 11.0 is [ to
-i 5
, j 1
0 _ LOf,lATION 13.0 0 10 - E N s- [ at . 0 7 E LOC ATION 15.9
- c. is ,
t u 10 - s *
- 0 is - LOCATION 69.0 e
10 - t O' ' 7s 7e so s2 as as se 7s 7e so s2 s4 as as AUGUST NOVEMBER Figure 3 (continued) 95
*-----* D EN S I TY 5--* Bl0 VOLUME LOCATION 2.0
** - .s
* ~ -
r.
- s. .
o
,, LOCATION 5.0
.s 4 . .
- 2 o 'E ' k # '"~ '
_ -r.. , m
~
es o E E u ," LOCATION 9.5 m - n x - 2 E g2 -
- E - 5- 3 ~
t-m 0 o 3 z LOCATION 11.0 J w a- o o - - 4 > 9 s . m 4- - 2 2 .
.. ~
4-o
- m, N -v'#
D LOCATION 15.9 s . s . x -
=, -
- 2 2 -
s, - n-o ,
,,~, ~
y a w* re so s2 s4 as as 7e 80 s2 s4 se as FEBRUARY MAY Figure 4 1.ake Norman phytoplankton densities and biovolumes observed in February and May of each year, when sampling was conducted, from 1978 to 1988. Values represent composites of the euphotic zone. 96
l W DENSITY .
*--* B10 VOLUME LOCATION 2.0 :
s- - - _4 1
~
~
4 - .
)
,- 2 2 -
/
)- ~
s.-< 0
=%
o i
- s. LOCATION 5.0
~ ~
4 - g g ,w " ~ 2
'I #
2 =
# 5 p . k
~
d 's , =' , E o
.-N o E x
9 LOCATION 9.5 9 x '- - x f ~
\ -
2 E c .
. 'n E 6 .x - '
>- W w 0 I 0
Di 3 z LOCATION 11.0 $ g s-A' - -
-t g
,v' i ", -
5 4 . i , -
/
2 2 -
\'W _
D 0 x LOCATION 15.9 i 14.2 =so' x N. s - i
/ i
_ 4 i f '. 9 ' 4 - i i, _ i < x i .. . d - x- 2 2
" *~~<i
~] x a
k 0 ' ''''' O 78 80 82 84 86 88 78 80 82 84 86 88 AUGUST NOVEMBER l l Figure 5 1.ake Norman phytoplankton densities and biovolumes observed in August and November of each year, when sampling was conducted, from 1978 to 1988. saiues represent composites of the euphotic Zone. 97
- k. _ _ _ . _ _ _ . _ _ _ _ . _ _ _ _ _ _ _
i ZOOPLANKTON l INTRODUCTION , Previous studies on Lake Norman have found that zooplankton popuia-l tions demonstrate a bimodal seasonal distribution with peaks occurring
- in spring and fall. Considerable spatial and year to year variability
! was also observed (Duke Power Company 1976, 1985; Hamme 1982; E Menhinick and Jensen 1974). The objectives c' the Lake Norman Mainte-nance Monitoring Program are to:
- 1. Describe quarterly patterns of zooplankton standing crops at selected locations on Lake Norman, and
- 2. Compare zooplankton data collected during this study (February, May, August, and November 1988) with historical data collected during these months.
METHODS AND MATERIALS Quarterly zooplankton samples were collected at Locations 2.0, 5.0, 9.5,11.0, and 15.9 (Chemistry, Figure 1). Duplicate 10 m to surface and bottom to surface net tows were taken at these locations on 2 Fet rua ry, 5 May, 4 and 8 August, and 22 November 1988. Field and laboratory methods for zooplankton standing crop analysis were report-ed in Hamme (1982). Zooplankton standing crop data from February, May, 98 _-___-_=_________-_---____-___ a
August, and November 1988 were compared with historical data from
.these months since 1978.
RESULTS AND DISCUSSION Standing Crop Zooplankton densities during sampling periods of 1988 were generally higher among 10 m to surface samples than among bottom to surface samples, except 'during February when little difference was observed. This was also the case during previous years (Table 1; Figure 1). Ruttner-Kolisco P.974) reported that zooplankton are capable of maintaining their positions in the water column as a response to the light gradient, which subsequently accounted for higher phytoplankton standing crops in the upper strata. Zooplankton standing crops were highest in May and lowest in February 1988. Hamme (1982) noted that the primary p'ak in zooplankton densi-ties usually occurred during the spring; while minimum zooplankton standing crops were typically observed during the winter. Spatially, zooplankton standing crops usually followed a trend of increasing values from downlake to uplake locations, with the exception of August when zooplankton densities increased uplake to Location 11.0, then declined sharply at Location 15.9 (Table 1; Figure 1). Zooplankton densities during February, May, August, and November 1988 l were generally within ranges of those observed during these montt.: of 99
1 previous' years; however, Location 2.0 had somewhat lower standing crops during May 1988. than during . Mays of previous _ years. -Location 11.0 had higher zooplankton densities in August 1988 than in previous Augusts, and Location 15.9 had higher standing. crops during: November 1988 than during Novembers of previous years. This location has also - shown considerable _ year to year variability among. zooplankton densi-
' ties. No long ter:a trends could be identified at Location 9.5 and, with the exception of August, Location 11.0 due to the paucity of historical data from these locations-(Figure 1).
__ Community Composition Fifty-three zooplankton taxa have been identified in samples collected since the Lake Nonnan maintenance Monitoring' Program was initiated in August _1987 (Table 2). One taxon, Holopedium amazonicum, t;ad not' been recorded in previous studies (Duke Power Company 1976,1985; Hame 1982; Menhinick' and Jensen 1974). The Rotifera dominated zooplankton assemblages during this study, fcillowed in importance by the Copepoda and the Cladocera -(Table 3). This was also the case during previous years. Rotifers dominated zooplankton assen.blages at all locations during 1988. During February 1988, the relative abundance of rotifers was highest at Location 5.0. Location 11.0 had the highest percent compo-sition of rotifers in May and August, while Location 15.9 demonstrated the highest relative abundance t
- rotifers in November (Table 1).
Name (1982) found that highest r, cifer densities generally occurred 100
at uplake locations. The percent composition of rotifers among samples collected during' 1988 was generally higher than in previous years (Table 3). During February 1988, Trichocera dominated rotifer populations at' Locations 2.0 and 5.0; while Polyarthra was the dominant rotifer at Location 11.0, and Keratella was the most abundant rotifer at Location 15.9. Polyarthra dominated rotifer populations in May at all but Location 15.9, where Syncheata was dominant. Dominant rotifer taxa in August were Ptygura and Trichocera, except et Location 15.9, where Conochilus was dominant. During November 1988, major taxa at most locations were Polyarthra and Keratella. These taxa were among the most abundant rotifers observed during previous years (Hame 1982). Copepods were most abundant during May, with lowest densities observed during August. Their relative abundance Sas highest at Location 2.0 in May and November, and in outt9m to surface samples at this location in August. Location 9.5 had the highest relative abundance of copepods in February, while Location 5.0 had the highest relative abundance of copepods in 10 m to surface samples in August (Table 1). Copepods were far less important in tenns of relative abundance during May 1988, August 1987 and 1988, and November 1988 than during these periods of previous years (Table 3). Copepods were dominated by immature forms during all sampling periods of 1988, and adults seldom accounted for more than 10% of copepod densities. Tropocyclops and Cyclops dominated adult populations at 101
i- most locations in February, while Tropocyclops and Mesocyclops were l the predominant adults in May and Augurt. Tropocyclops and Diaptomus dominated adult populations in November. The four taxa listed above were also among the most abundant adult copepods identified by. Hamme - (1982). Cladocerans were most abundant during May, while lowest densities were observed during August. In Februa ry, percent composition of cladocerans was highest at Locations 11.0 and 2.0 in 10 m to surface and bottom to surface samples, respectively. During May, relative abundance was highest at Location 2.0. In August, cladocerans had highest relative abundances. at Locations 9.5 and 2.0 in 10 m to
' surface and ' bottom to surface samples, respectively. Locations 11.0 (10 m to surface) and 5.0 (bottom to surface) had highest relative
{ abundances of cladocerans in November (Table 2). Percent composition values for cladocerans at Lake Norman locations in August and November 1988 were generally lower than in these months of previous years, while February and May 1988 samples had higher proportions than in previous years (Table 3). Bosmina was the most abundant cladoceran observed in samples collected in 1988. During August, Bosminopsis was also an important constituent of cladoceran populations. Hanine (1982) found that Bosmina often dominated cladoceran populatiori throughout the year. Bosminopsis was i not reported as a dominant cladoceran prior to plant operation; ' however, its abundance increased considerably during the operational 1 1 years of 1983-1984 (Duke Power Company 1985). i 102
There are, as yet, no new future zooplankton studies planned for Lake Noman. We will continue to perfonn quarterly maintenance monitoring as described in this report.
SUMMARY
Zooplankton densities were generally higher among 10 m to surface samples than among bottom to surface samples during this study, as during previous studies. Total zooplankton standing crops and standing crops of Copepoda, Cladocera, and Rotifera were highest in May - and lowest in February. In- past studies, primary zooplankton peaks were often observed in the spring, with minima occurring in winter and summer months. Zooplankton densities during 1988 were generally within ranges observed during previous years; however, considerable year to year variability in zooplankton standing crops was observed at most locations. Rotifers dominated zooplankton standing crops throughout the 1988 study, as they have generally done during past years; however, their relative abundance during 1988 was higher than in past years. Major rotifer taxa were Trichocera, Polyarthra, Keratella, Synchaeta, Ptloup, and Conochilus. The Copepoda were much less important among zooplankton assemblages during May 1988, August 1987, 1988, and November 1988 than during these months of previous years. Copepod populations were consistently dominated by immature forms. Major adult taxa during 1988 were Tropo-cyclops, gglops, Mesocyclops, and Diaptomus. 103 __~_______-__________________
I" Cladoceran relative abundance in February and May 1988 was higher than in these months .of previous years, while relative abundance in August l and November 1988 was lower than in these months- of previous years. Bosmina and Bosminopsis were the most abundant cladocerans observed during 1988, as w' ell as during sampling periods of 1987. With the exception of variations in relative abundance values, overall trendt of community composition during this - study were generally similar to those_ of previous studies U.e., Rotifera dominant, fol-lowed in importance by copepods and cladocerans). Most of the major genera identified during 1988 were also listed as among the most abundant taxa during previous years. 104
i LITERATURE CITED Duke Power Company. McGuire Nuclear Station, Units 1 and 2, Environ-mental Report, Operating License Stage. Och rev. Volume 2. Duke Power Company, Charlotte , NC.1976. Duke Power Company. Mcguire Nuclear Station, 316(a) Demonstration. Duke Power Company, Charlotte, NC.1985. Hamme, R. E. Zooplankton, p. 323-353. In J. E. Hogan and W. D. Adair (eds.). Lake Norman summary, Technical Report DUKEPWR/82-02. Duke Power Company, Charlotte, NC. 460 p.; 1982. Menhinick, E. F. and L. D. Jensen. Plankton populations, p. 120-138. In L. D. Jensen (ed.). Environmental responses to thermal dis-charges from Marshall Steam Station, Lake Norman, North Carolina. Electric Power Research Institute, Cooling Water Discharge Re-search Project (RP-49) Report No.11. Johns Hopkins University, Baltimore, MD. 235 p.; 1974. Ruttner-Kolisco. Planktpn rotifers: biology and taxonomy. Die Binnen-gewasser. 24(1) suppliment.146 p.1974. 105
Page 1 of-2 3 Table 1 Total zooplankton densities (no./m ), densities of major zooplankton taxonomic groups, and percent composition in parenthesis) of major taxa in 10 m to surface (10-5) a(nd bottom. to surface (B-S)- net tow samples collected on Lake Nonnan in February, May, August, and November 1988. Sample Locations Date Type Taxon 2.0 5.0 9.5 11.0 15.9 027[i2788 10-5 COPEPODA 8.8 2.9 10.3 22.8 17.8 (22.3) (10.0) (36.2) (29.6) (18.7) CLAD 0CERA 3.2 1.3 2.1 . 10.5 6.6 (8.2) (4.3) (7.5) (13.6) (7.0) ROTIFERA 27.5 25.2 16.0 43.6 70.5 (69.5) (85.7) (56.2) (56.7) (74.3) TOTAL 39.5 29.4 28.4 76.9 94.9 B-5 COPEPODA 8.1 4.1 8.4 19.8 19.2 (depth [m] (20.2) (12.5) (36.5) of tow (25.3) (22.4) for each CLAD 0CERA 3.6 0.6 1.5 6.8 5.5 location: (9.0) (1.9) (6.6) (8.7) (6.4) 2.0=30 5.0=16- ROTIFERA 28.5 28.4 13.1 51.4 61.1 9.5=21 (70.8) (85.6) (56.9) (65.9) (71.2). 11.0=26 - TOTAL 40.2 33.1 23.0- 78.0 85.8 15.9=20) 05/05/88 10-5 COPEPODA 14.2 8.8 10.6 13.0 19.8 i (21.6) (13.7) (6.7) (6.6) (4.6) CLAD 0CERA 5.8 5.8 4.8 1.6 18.4 (8.8) (9.0) (3.1) (0.8) (4.3) ROTIFERA 45.8 49.6 141.7 183.9 388.5 (69.6) (77.3) f9 j0.2 (92.6) (91.0) : TOTAL 65.8 64.1 37.1 198.5 426.7 l l B-S COPEPODA 11.8 20.1 17.1 19.6 25.0 (depth [m] (30.2) (26.8) (15.9) (17.7) of tow (7.8) for each CLAD 0CERA 8.5 9.2 7.9 3.3 42.1 location: (22.0) (12.3) (7.4) (3.0) (13.2) . 2.0=31 I 5.0=19 ROTIFERA 18.6 45.7 82.2 88,0 251.1 ! 9.5=21 (47.7) (60.9) (76.7) (79.4) (78.9) 11.0=26 TOTAL 38.9 75.0 107.2 110.9 318.2 15.9=20) l l l 106 1
Table 1 (continued) Page 2 of 2 Sample . Locations
'Date Type Taxon _-2.0 5.0 9.5- 11.0 15.9 08754787. 10-5 CUPLPUDA 4.6 11./ ~.b J U.1 U.4 (5.7) (10.5) (2.5) (4.2) (16.2)
CLAD 0CERA 2.5 7.2 6.0 3.6 1.1 (3.1) (2.5) (4.2)- (1.9) (2.1) ROTIFERA 73.4 92.3 133.7 183.3 42.1 (91.2) .(83.0)- (93.4) (93.9) (81.4) INSECTA 0 0 0 0 0.1 TOTAL 1 1 1 5-5 COPEPODA 11.9 9.9 2.8 3.0 5.7 (depth [m] (23.2) (13.7) of tow (3.4) (3.5) (18.2) for each CLAD 0CERA 3.1 3.7 3.5 1.4 0.9 location: (6.0) (5.1) (4.3) (1.6) (2.9) 2.0=30
-5.0=19 ROTIFERA 36.3 58.8 75.3 82.2 24.5 9.5=20 (70.6) (81.1) 11.0=26 (92.2) (94.8) (78.0) 15.9=19) INSECTA 0 0.1 0.1 0.1 0.3 TOTAL 11/22/88 10-5 COPEP00A- 12.2 12.5 9.1 18.0 11.8 (17.5) (12.8) (6.6) (11.8) (4.4)
CLAD 0CERA 2.8 1.6 1.8 6.7 3.1 (4.0) (1.6) (1.3) (4.4) (1.2) ROTIFERA 54.5 83.6 125.5 128.3 253.6 (78.5) (85.6) _(92.0) (83.8) (94.4) TOTAL 69.5 97.7 136.4 153.0 268.5 8-5 COPEPODA 16.9 18.1 12.4 22.7 8.8 (depth {m] of tow (24.8) (21.1) (7.8) (15.4) (3.1) for each CLAD 0CERA 6.1 2.1 1.2 9.3 2.6 location: (8.9) (13.6) (0.8) (6.3) (0.9) 2.0=30 5.0=19 ROTIFERA 45.2 65.6 145.6 115.4 277.1 9.5=21 (66.2) (76.4) (91.4) (78.2) (96.0) 11.0=27 TOTAL 68.2 53.7 159.2 147.4 288.5 15.9=21) 107
~
page 1 of 2 Table 2 Zooplankton taxa identifie'd from samples collected on Lake Nonnan on 4 August, 5 November 1987, 2 February, 5 May 4 and 8 August, and 22 November 1988. (*= taxon not recorded in previous Lake Nonnan studies).
' COPEPODA Cyclops thomasi S. A. Forbes C. spp. Fischer Diaptomus bergei Marsh D. mississipaiensis Marsh D. pallidus ierick D. spp.. Marsh Nesocyclops edax (S. A. Forbes)
M. spp. Sars Tropocyclops prasinus (Fischer) T. spp. Kiefer falanoid copepodites Cyclopoid copepodites Nauplii CLAD 0CERA Bosmina longirostris (O. F. Muller) B. spp. Baird losminopsis deitersi Richad I;eriodaphnia spp. Dana. Daphnia ambigua Scourfield , D. parvula Fordyce D. spp. Mullen Diaphanosoma spp. Fischer
- Holopedium amazonicum Stingelin H. spp. Stingelin Teptodora kindtii (Focke)
Ilyocryptus sordidus (Lieven) Sida crystalline 0. F. Mullaer ROTIFERA Anuraeopsis spp. Lauterborne Asplanchna spp. Gosse Brachionus caudata Barrois and Daday B. havanaensis Rousselet
- 1. patulus 0. F. Muller thromogaster spp. Lauterborne Collotheca spp. Harring Conochiloides spp. Hlava Conochilus unicornis (Rousselet)
C spp. Hlava Eastropus spp. Imhof Hexarthra spp. Schmada Kellicotia bostonensis (Rousselet) 108
s Table 2 (continued) page 2 of 2 l- K.. spp. Rouselet Eeratella spp. Bory de St. Vincent Lecane spp. Nitzsch Macrocheatus spp. Perty Monostyla _stenroost (Meissener) M. spp. Ehrenberg Floeosoma truncatum (Levander) P. spp. Herrick Polyarthra euryptera (Weirzeijski) P. vulgaris Carlin P. spp. Ehrenberg Ptygura spp. Ehrenberg Synchaeta spp. Ehrenberg Trichocera capucina (Weireijski) T.. cylindrica (Imhof) T. spp Lamark Unidentified Bdelloidea INSECTA Chaoborus spp. Liechtenstein Table 3 A comparison of the density percent composition of major taxonomic groups during certain years of the preoperational period (1978-1981), the operational period (1982-1984), and the Lake Norman Maintenance Monitoring study (1987 and 1988) (NS = not sampled). February May 78-81 82-84 1987 1988 78-81 82-84 1987 1988 COPEPODA 33.2 28.7 NS 23.1 33.9 18.2 NS 10.2 CLAD 0CERA 6.8 4.5 ' 7.9 5.1 3.9 6.9 ROTIFERA 60.0 66.8 69.0 61.0 78.2 82.9 INSECTA 0 0 0 0 0 0 August November 78-81 82-84 1987 1988 78-81 82-84 19,87 8 1988 COPEPODA 27.4 22.1 8.5 7.7 19.7 26.6 31.9 9.7 CLAD 0CERA 8.0 12.3 7.2 3.7 3.2 6.4 8.9 2.5 ROTIFERA 64.0 65.4 84.2 88.6 77.1 67.1 59.2 87.8 INSECTA 0 0.2 0 0.1 0 0 0.1 0 109 w
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FISHERIES INTRODUCTION In accordance with the NPDES permit for McGuire Nuclear Station, monitoring of specific fish population parameters was continued during 1988. The objectives of the fish monitoring program for Lake Norman during 1988 were to:
- 1. Determine taxonomic composition, standing stock, and density of fish at McGuire Nuclear Station (MNS) discharge and reference locations; compare with past data.
- 2. Determine density and distribution of fish at and near MNS discharge associated with modification of the thermal effluent limitation for MNS from 95 to 97'F during August.
- 3. Determine striped bass habitat lake-wide and note any occurrence of fish mortalities; compare with past data.
- 4. Determine age and growth of striped bass collected from Lake Norman; compare with past data.
- 5. Determine an index of abundance of largemouth bass in the mixing zone of MNS and reference zone; compare with past data.
- 6. Determine age and growth of largemouth bass collected from Lake Norman; compare with past data.
112 i
a, MATERIALS AND METHODS Fish Community Sampling 9 L g Taxonomic composition, standing stock, (Kg ha" ) . and Jensity
~
(numbe: + he ) of fish were determined with cove rotenone samples durin'g August 1988 at MNS discharge Location 4.0 and midlake Location 19.0 (Figure 1). A 1.2-ha area was sampled at each rotenone location as described in Siler et al. (1982). Ictalurids, moronids, and centrarchids were considered sport l fish. Harvestable sport fish standing stock was estimated from cove rotenone snmples. for each location. Harvestable sport fish were defined by the total length criteria of Hayne et al. (1967). Density of fish in the limnetic areas of 'the MNS mixing zone was determined 'with hydroacoustic gear by sampling alt na .0 transects (Figure 2) on 23 June, 3 August, 22 August, ca.d 22 September 1988 after sunset. Acoustic sampling was conducted with a Biosonics - echosounder and a dual-beam ' transducer (Burezynski. et al. 1987) . The acoustic system was set at a frequency of 120 kHz on 23 June and 22 and 31 August, and 420 kHz on 22 September. The acoustic equipment parameters were as
~1 follows: ping rate of 10 sec , pulse width of 0.4 ms, 40 Log R signal threshold of 100 mV for 420 kHz frequency ar 8150 mV 4
113
W l 1: I. for 120 .kHz frequency. The. transducer was mounted in a hydrofoil. towed approximately 1.5 m s ~1 at' O.5 m below the - surface and aimed straight down. Target strength data were procersed in real-time with'a Biosonics echo signal processor. Echo integration'information was recorded and processed in the lab with the echo' signal processor, and scaled with the target strengths to provide densities by location and depth. Fish size was calculated from the target strength of fish tracked using Biosonics tracker software package and converted to lengths with. Love's (1971) equation. Striped Bass Sampling l The availability of suitable adult striped bass habitat in Lake Norman .was determined from water temperature and dis-solved oxygen concentration profiles taken lake-wide during 1988 (Chemistry Chapter). Water with a temperature-526*C and a dissolved oxygen concentration 22 mg.l ~1 .was considered suitable habitat for adult striped bass in Lake Norman. The main channel of Lake Norman was searched for dead and moribund fish in conjuction with physicochemical samples during June, July, August, and September. Additional searches, in the main channel, for stressed fish were also conducted on 20 and 31 July and 5 and 11 August. Dead and moribund fish were identified, and striped bass were measured (nearest mm total length). Scales and ctoliths were removed for age and growth analyses of striped bass, if the fish were not badly decomposed. 114
Fishing tournaments conducted on Lake Norman on 16 and 17 April and 23 and 24 April 1988 by the Lake Norman Striper Swiper Club and Striper Magazine provided data on size and age structure, spatial distribution, food habits, and condition of striped bass. Tournaments started at 0600h and ended at 1200h the next day. Anglers were asked to give the general locatioa of capture, which was assigned a zone number (Figure 1). A total of four striped bass (two each day) could be weighed-in per entrant. Each fish was weighed (g) and measured (nearest mm total length). Fish were filleted and the carcasses were frozen or kept on ice until processed. Scales, otoliths, and stomachs were removed, gall bladders examined, and sex determined for each striped bass processed. A scale sample was removed from the region posterior to the margin of the depressed pectoral fin and below the lateral line of striped bass. Acetate impressions of scales were magnified at 40x with an Eberbach scale projector, and annuli counted and measured. Otoliths were removed, sectioned, and mounted on o; is slides; annuli were counted while viewing through a stereomicroscope at 8-20x magnification. Total length of striped bass at annulus formation was back-calculated from scale measurements with the standard method (Carlander 1969) and an intercept of 50 mm (Hamphreys and Kornegay 1979). Stomach contents were removed, and organisms were identified to the lowest practicable taxon, counted, and weighed to the 115
a nearest 0.1' mg. .These data ~ from each tournament were summarized as percent wet weight of total stomach contents. The condition of the gall bladder of' striped bass collected from tournaments was used as an indicator of stress. A distended gall bladder (completely filled with bile) l indicates reduced capability for digestion (Coutant 1985) 1 and is considered an indication of stress. A flaccid gall bladder is an indir.ation of no stress. Condition factor (k) (Carlander 1969) of each striped bass was also calculated, K , W 10 3 L j where W = weight in grams and L = length in millimeters. Largemouth Bass sampling Largemouth bass were collected at night from Zone 1 (MNS mixing zone included) and reference Zone 2 (Figure 1) from 24 April through 1 May 1988 with boat-mounted electrofishers by Duke Power Company (DPC) and North Carolina Wildlife Resources Commission (NCWRC). The same 1-km shoreline segments sampled for largemouth bass during 1984 by DPC and NCWRC were sampled i (18 segments in Zone 1 and 14 segments in Zone 2). Largemouth i bass were also electrofished at the MNS diccharge canal and i l 116
l1 were . included with ' the ' Zone 1 collections. All largemouth
' bass collected were measured for. total' length (mm). A maximum of, ten bass from each 50-mm size class were weighed,'and scale (samples were taken for age and growth analysis. Scales were pressed 'and read as previously described for striped bass.
.CPUE, catch-per-unit-effort (number per km of shoreline), was used as a index of abundance for largemouth bass for each zone.
RESULTS AND DISCUSSION Fish Community A , total of 26 fish species (22 species from Location .4.0 and 20 species- from Location 19.0) was ' collected with cove rotenone samples during August 1988 (Table 1). Gizzard sn=0 (Dorosoma cepedianum), common carp (Cyprinus carpio),-channel catfish (Ictalurus. punctatus), and bluegill: (Lepomis macrochirus) accounted for more than 80 % of the total standing stock at MNS discharge cove (Location 4.0); bluegill accounted for over 70 % of the total fish density. Gizzard shad, common carp, channel catfish, and bluegill comprised more than 65 % of the total standing stock of fish at Location 19.0; threadfin shad (Dorosoma petenense), whitefin shiner (Notropis niveus), and bluegill accounted for over 65 % of the total fish density. Channel catfish comprised more of 117
I the total standing stock at both locations (over 10 % at each location) than in previous years (less than 5%, Duke Power Company 1986). A subtle change in taxonomic compostion of the fish community downlake was ' first noted during 1984 when channel catfish were first collected in downlake cove rotenone samples (Duke power Company 1985). No other substantial differences in taxonomic composition of the fish community among years were apparent. Total standing stock of fish at Locations 4.0 and 19.0 appeared similar and were within ' the range estimated in prior years (Figure 3). This was also the case for harvestable sport fish standing stock. No differences of critical importance in standing stock and density estimates for representative important fish taxa 1 collected at cove rotenone locations were noted between years before and during operation of MNS (Figures 4 and 5). Some avoidance and attraction to the MNS discharge cove in August by selected taxa may be related to the operation of MNS. I Standing stock and density of gizzard shad and density of yellow perch at the MNS discharge location were slightly lower during than before operation of MNS; bluegill density was slightly higher during than before MNS operation. 118
Young-of-the-year (YOY) of selected fish taxa were collected at MNS discharge Location 4.0 and Location 19.0 in cove rotenone samples during and before MNS operation (Figure 6). Threadfin shad, catfish, largemouth bass and yellow perch YOY were collected in all years sampled at each location. Collection of gizzard' shad, white bass, and crappie YOY was sporadic among years at both locations. Successful reproduction of selected fish taxa was detected before and during MNS operation. Recruitment of YOY fish was evident in hydroacoustic samples taken in the MNS mixing zone from 23 June through 22 September 1988 (Figure 7; Table 2). Mean total fish density
~
increased from 6,650 fish.ha on 23 June to 30,262
~1 ~1 fish ha on 3 August to 31,456 fish *ha on 22 August and decreased to 20,797 fish ha ~1 on 22 September. The majority of fish targets measured were <100 mm total length for all sample dates. More fish targets >100 mm total length were measured on 22 September than on previous sample dates. Very few large fish (>300-mm total length) were detected (<5% of fish measured) in the limnetic area of the MNS mixing zone and immediate discharge area on any of the hydroacoustic sample dates.
Changes in horizontal and vertical distribution of fish in the limnetic area of the MNS mixing zone among hydroacoustic sample dates appeared to be influenced by water temperature 119 _-__-_______-__-____D
and dissolved oxygen concentrations to some degree (Figures 7 through 11). The mean fish density in the limnetic area of the MNS discharge on 23 June (8795 fish ha" ) was slightly higher than that of the main-lake area (7120 fish ha~I) and over twice that of the Ramsey Creek area (3079 fish ha"I). Densities of fish from all three areas of the MNS mixing zone were most abundant from 3 to 5 m below the surface on 23 June, but fish were present at almost all depths. As water temperature at the MNS discharge area increased and the hypolimnion became anoxic from 23 June to 22 August, a shif t in spatial distribution of fish occurred. Mean fish density was highest at the main-lake area (43,261 fish ha' ) followed by 31,532 fish ha ~I at the MNS discharge area and 11,659
~1 fish ha in the Ramsey Creek area on 3 August. Mean fish density in the main-lake area on 22 August . (46,140 fish ha" )
was twice that in the MNS discharge area and Ramsey Creek area (22,420 and 20,913 fish ha'I , respectively). Fish were primarily concentrated from 6 to 10 m and 6 to 9 m below the surface on 3 August and 22 August, respectively,. No fish were detected deeper than 19 m below the surface on 22 August. Water temperatures decreased in the epilimnion and dissolved oxygen concentrations increased in the hypolimnion from 22 August to 22 September, and fish were detected at almost all depths on 22 September. Attraction of fish to the MNS discharge area on 22 September was indicated, as mean fish density was highest at this area (40,041 fish ha~I) followed 120
L by 15,660 ' fish *ha'1 in the Ramsey Creek area, . and 10,212
. fish ha'1 in the main-lake area.
Some fish avoidance of the MNS discharge area was associated with water temperatures >90* and 95* F during August 1988, but such behavior did not appear to have an adverse effect on the fish community. Stauffer et al. (1975) noted that the fish community can maintain its structure and function with the presence of thermal discharges, provided that adequate areas of ambient temperature are available nearby. Such areas I i continued to exist in Lake Norman during August 1988. Striped Bass' Adequate habitat for striped bass in Lake Norman occurred i-lake-wide in all months during 1988,- except August. As the lake stratified, depletion of suitable habitat for adult striped bass (water with a temperature 526' C and a dissolved oxygen concentration 22 mg *1' ) occurred in the main channel j of Lake Norman (Figure 12). Reduction of suitable habitat for adult striped bass occurs to some degres each summer in Lake Norman (Duke Power Company 1985), and appears to be typical of habitat reduction in some southeastern reservoirs (Coutant 1985; Mullis.1984). 121
l' s j A total of four striped bass mortalities was documented from June through September 1988 (Table 3). This was, fewer mortalities than occurred during 1986 or 1987, when reduction - of suitable habitat was more severe . than during 1988. Modification of the thermal limitation for MNS from 95 to 97'F during August 1988 may have contributed to some degree to'the-shorter period of suitable habitat depletion during 1988 than during 1986 and 1987. A total of 49 striped bass sas collected from two striped bass fishing tournaments during April 1988 (Table 4 ). Striped bass were caught in four of the six zones in Lake Norman, with the majority of fish caught in uplake Zone 5, followed by the catch in Zone 4 (near Marshall Steam Station). The majority of striped bass was also caught in Zone 5 during April 1986 and 1987. Ages of striped bass caught in April 1988 ranged from two to seven years, and total length ranged from 474_ to 858 mm (Table 5). Five was the modal age during April.1988. The 1983 year class appears to be a dominant year class, as four and three was the modal age during April 1987 and 1986, respectively. Additional striped bass fingerlings were stocked in Lake Norman during 1983 (a total of 450,000 striped bass fingerlings were stocked, personal communication NCRC) . The NCWRC stocks a minimum of 100,000 striped bass fingerlings in Lake Normam each year. I i 122
1 Mean back-calculated total lengths for striped bass collected from Lake Norman since 1986 indicate that their growth was within the range reported from other reservoirs (Table 6). Female striped bass appear to grow faster than males in Lake Norman. Mean back-calculated total length for one and two year old Lake Nerman striped bass (sexes combined) was greater than that reported previously for striped bass from Lake Norman and other southeastern reservoirs. Striped bass collected from tournaments during April 1988 were almost entirely piscivorous, as was the case in April 1986 and 1987 (Table 7). The diet of striped bass consisted of a wide variety of prey that included gizzard shad, Dorosoma cepedianum, during all years. The condition of striped bass during April 1988 appeared j similar to the condition of striped bass collected during the April 1986 and 1987 tournaments (Table 8). The occurrence of distended gall bladders in striped bass indicates reduced capability for digestion of food to some degree (Coutant 1985). The mean condition factor of striped bass during April 1988 was similar.to that during April Iwo6 and 1987. l l 123
7 , r n: Largemouth Bass Mean CPUE of largemouth bass was greater at Zone 1 (MNS mixing Zone and discharge included) than at Zone 2 (Davidson Creek arm) of Lake Norman during spring 1988 '(Table 9). Mean CPUE of largemouth bass for both zones was lower in 1988 than in past years. Percent occurrer e of largemouth bass by total length groups and ages at each zone was similar among years,
.except in 1983.(Figures 13 and 14). -Largemouth bass that were 301 to 350 mm total length comprised more of the catch during 1983 than in other years, as did age three largemouth bass.
This change may have been-an initial response to the regulation change from a 12-in (305-mm) size limit to a 14-in (356-mm) size limit and able to keep.two bass of any size that l l was effective in January 1982. Mean back-calculated total length of largemouth bass was similar for each age group between Zones 1 and 2 for all years combined and was within the range reported for other southeastern reservoirs (Table 10). No adverse effects on the largemouth bass population in and near the MNS mixing zone were apparent. 124
years. No other differences in taxonomic composition of the fish community or critical changes in standing stock and density estimates of selected fish taxa were apparent am ong years. Recruitment of YOY of selected fish taxa was cove evident in rotenone sa,mples and for fish measured in hydroacoustic samples in 1988. Successful reproduction of fish was detected before and during MF3 operation. Spatial differences of fish density among hydroaconstic e samp that some fish avoidance of the MNS discharge area was associat water temperatures over 90 degrees F or over 95 degrees F, du 1988. An adequate area with ambient water temperatures existed in mixing zone fcr the fish community to utilize. As Lake Norman stratified, depletion of suitable h&itat or f adult striped bass occurred in the main channel during August 19B8. Reduction of suitable habitat in 1988 was less severe than in 1986 or 1987, and fewer striped bass mortalities vere documented in 1988 (four fish) than in 1986 or 1987 (43 and 15 fish, respectively). l 127
t
- 4. Periodic creel surveys to determine changes in u.
n fishermen pressure, success, and harvest of sport fish associated with two-unit operation of MNS and NCWRC management regulations since the last creel survey in 1982. Creel surveys will be scheduled and budgeted cooperatively between DPC and NCWRC.
SUMMARY
The operation of MNS did not appear to have an adverse effect on the fish community of Lake Norr.an. A total.of 22
.and 20' fish species were collected in cove rotenone samples at the MNE discharge and reference locations, respectively.
Total standing stock was similar between locations during August 1988 and was within the range reported for past years. Gizzard shad, common carp, channel catfish, and bluegill comprised over 65 % of the total standing stock of fish; bluegill, threadfin shad, and whitefin shiner accounted for over 65 % of the total fish density at each cove rotenone location sampled in 1988. Channel catfish comprised more of the total standing stock of fish in 1988 than in past 126
i A total of 49 striped bass were caught within four of six zones in Lake Norman during two tournaments held in April 1988. The majority of striped bass were caught in the two uplake Zones (Zones 4 and 5). Zone 4 included the Marshall Steam Station discharge area. The modal age of striped bass caught was five. This yearclass was also the modal group caught in April 1986 and 1987, and corresponded to the highest number of fingerlings stocked (approximately 450,000 fish). Mean back-calculated total length of striped bass from Lake Norman was within the range of total lengths reported from other reservoirs. CpUE of largemouth bass collected with electrofishing was higher in Zone 1 (MNS mining zone included) than Zone 2 during spring 1988. Percent ecmposition of total length groups and ages of largemouth bass was similar between Zone 1 and Zone 2 during 1988, 1984, and 1982. Mean back-calculated total length of largemouth bass was similar for each age group between Zones 1 and 2 for all years combined, and was within the range reported for other southeastern reservoirs. No adverse effects were apparent on the largemouth bass population in or near the MNS mixing zone. 128
I l '-
- l. LITERATURE CITED I
1 Burczynski, J. J.; Michalettz, P. H.; Marrone, G. M.; Hydroacoustic assessment of the abundance and distribution of rainbow smelt in Lake Oahe. North American Journal of Fisheries Management. 7(1):106-116; 1987. Bustle, R.G. . Striped bass population investigations Badin Lake and Lake Norman 1975-1977. North Carolina Wildlife Resources Commission Report. pp. 201-207; 1979. Carlander, K. D. Handbook of freshwater fishery biology.' - The Iowa State University Press, Ames, Iowa. 1969. Coutant, C. C. Striped bass, temperature, and dissolved crygen: a speculative hypothesis for environmental risk. Transactions of the American Fisheries Society 114:31-61;- 1985. Duke Power Company. McGuire Nuclear Station 316(a) demonstration. Duke Power Company, Charlotte,-North Carolina; 1985, 129
l Erickson, K.E. ; Harper, J. ; Mensiriger, G.C. ; Hicks, D. Status and artificial reproduction of striped bass from Keystone Reservoir, Oklahoma. Proc. Annu. Conf. Southeast Assoc. Fish and Game Comm. 25:513-522; 1971. Hayne, D.W.; Hall, G.E.; Nichols, H.M. An evaluation of cove sampling of fish populations in Douglas Reservoir, Tennessee. pp. 244-297. In Reservoir Fishery Resources Symposium. Southern Division, Am. Fish. Soc., Athens, GA. 569 p.; 1967 Humphreys, M.; Kornegay, J.W. An evaluation of the use of bony structures for aging Albemarle sound-Roanoke river striped bass (Morone saxatilis). N. C. Wildl. Resour. Comm. Fed. Aid Proj. F-22; 1979. Love, R.H. Dorsal-aspect target strength of an individual fish. J. Acoust. Soc. Amer. 49:816-823; 1971 Mullis, T. Stripers in hot water. Wildlife in North Carolina. 4B(6):8-9; 1984. Richardson, F.; Ratledge, H.M. Upper Catawba river reservoir and Lake Lure. N. C. Wildl. Resour. Comm. Fed. Aid Project F5R and F6R Job Compl. Rep.; 1:161-231; 1961. l 130
Siler, J.R.; Lewis, R.E.; Baker, B.K.; Vaughan, G.E.; Hansen, R.A. Chapter'20. Fish. D Hogan, J.E. and' W.D. Adair.(eds.). Lake Norman Sumary. Duke Power
* ~
Technical Report No. DUKE PWR/82-02. Duke Power Company, Charlotte, NC. 460 p. plus appendices; 1982. Smith,'W. B. Roanoke R.'er reservoirs. N.C. #ild?..~Res. Comm. Fed. Aid Proj. I1R adn F6R Job Compl. Rep.; 1:75-95; 1961.
.Stauffer,'J.R.; Cherry,'D.S.;'Dickson, K.L.; Cairns, J.Jr.
Laboratory and field temperature preference and avoidance. data of fish related to the establishment of standards. 3: Saila, S. B. (ed.) Fisheries and energy production, a symposium. D.C. Heath and Company, Lexington, Massachusetts; 1975 Stevens, R.E. The striped bass of the Santee-Cooper reservoir. Proc. Arm. Conf. Southeast Assoc. Game and Fish Comm. 11:253-264; 1957. Tatum, B. Yadkin and Lower Catawba River reservoirs. N.C. Wildl. Res. Comm. Fed. Aid Proj. F5R and F6R. Job Compl. Rep. 1:99-158; 1961 131
Van Den Avyle, M.J; Higginbotham, B.J. Growth, survival, and distribution of striped bass stocked into Watts Barr Reservoir, Tennessee. Proc. Ann. Conf. Southeast Assoc. Fish and Wildl. Agencies 33:361-370; 1979. 132
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ll1 f lfhb I Figure 4. Total standing stock (kg ha'I) of selected fish taxa estimated with cove rotenone samples collected during August of years before two-unit operation of McGuire Nuclear Station (before 1984= triangle), baseline year (1978= asterisk), and operational years (after 1983= square) at MNS discharge (Location 4.0) and midlake Location 19.0 on Lake Norman, North Carolina. I 146 _ ____O
MCGUIRE DISCHARliE s LOCATION 4.0 t ! I
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i Figure 5. Total density-(number ha-l) of selected fish taxa estimated with cove rotenone samples collected during August of years before two-unit operation of McGuire Nuclear Station (before 1984= triangle), baseline year (1978= asterisk), and operational years (after 1983= square) at MNS discharge (Location 4.0) and midlake Location 19.0 on Lake Norman, North Carolina. 147
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MCGUIRE WCLEAR Col #NS FORD STATION i HYDRO 23 Jugg gggg i
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COLMNS FORD MCGUIRE MJCLEAR STATION HYDRO 3 AUGUST 1988 82097
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's MCGUIRE NUCLEAR C0lh 5 FORD STATION HY3R0 22 SEPTEMBER 1988 Figure 7. Total density of fish (number.ha-I) estimated at each of ten transects with hydroacoustic gear on 23 June, 3 and 22 August, and 22 September 1988 in the McGuire Nuclear Station mixing zone on Lake Norman, North Carolina.
148
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