ML20198P038
| ML20198P038 | |
| Person / Time | |
|---|---|
| Site: | Mcguire, McGuire  |
| Issue date: | 12/31/1997 |
| From: | DUKE POWER CO. |
| To: | |
| Shared Package | |
| ML20198P037 | List: |
| References | |
| NUDOCS 9801210314 | |
| Download: ML20198P038 (99) | |
Text
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LAKE NORMAN: 1996
SUMMARY
MAINTENANCE MONITORING PROGRAM McGUIRE NUCLEAR STATION: NPDES No. NC0024392
- <a DUKE POWER 13339 HAGERS FERRY ROAD HUNTERSVILLE, NORTH CAROLINA 28078 DECEMBER 1997 O '
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i TABLE OF CONTENTS
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EXECUTIVE
SUMMARY
i LIST OF TABLES y LIST OF FIGURES vi l CHAPTER 1: McOUIRE OPERATIONAL DATA- 1-1 1 Introduction 1-1 l
. Operational data for 1996 1-1 i CHAPTER 2: WATER CHEMISTRY 2-1 J Introduction 2-1 '
Methods and Materials 2-l l Results and Discussion 2-2 :
Future Water Chemistry Studies 2-9
.... Summary 2-10 Literature Cited 2-10 CHAPTER 3: PHYTOPLANKTON 3 Introduction ~ 3-1 Methods and Materials 3-1 Results and Discussion 3-2 Future Phytoplanktan Studies 3-8 Summary 3-8
' O - Literature Cited 3-9 CHAPTER 4: ZOOPLANKTON 4-1 Intmduction 4-1 Methods and Materials 4-1 Results and Discussion 4-2 Future Zooplankton Studies 4-7 Summary 4-7 Literature Cited 4-8 CHAPTER 5: FISHERIES 5-1
. Introduction 5-1 Methods and Materials 5-1 Results and Discussion 5-2 Future Fisheries Studies 5-2
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1 EXECUTIVE
SUMMARY
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As required per the National Pollutant Discharge Elimination System (NPDES) permit number NC0024392 for McGuire Nuclear Station (MNS), the following annual report has l been prepared. 1his report summarizes environmental monitoring of Lake Norman conducted during 1996.
- - OPERATIONAL DATA FOR 1996
) Monthly wity factore of MNS during 1996 averaged over 50% for all months for both
- - units except in April, May and June for Unit 1. The average monthly discharge temperature ,
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was below the permit limit for all months. During July, August, and h;*=ber, when conservation of cool water and discharge temperatures are most critical, the permitted
- thermal limit for MNS increases from a monthly average of 95'F to 99*F. The average
[ monthly discharge temperature was 91.8'F (35.4*C) for July,98.3 F (36.8'C) for August, '
I and 93.4'F (34.18C) for September 1996. Low level intake water was pumped by Unit 1 for additional cooling from September 18 to 29,1996. The volume of cool water in Lake Norman was tracked throughout the year to ensure that si adquate volume was available to
,' comply with both the Nuclear Regulatory Commission Technical Specification requirements
! and the NPDES monthly discharge water temperature limit.
WATER CHEMISTRY DATA l
Temporal and spatial trends in water temperature and dissolved oxygen concentration data collected in 1996 were similar to those observed historically. Reservoir-wide isotherm and isopleth information for 1996, coupled with heat content and hypolimnetic oxygen data, illustrated tisat Lake Norman exhibited thermal and oxygen dynamics characteristic of historic conditions and similar to other Southa==*=n reservoirs of comparable size, depth, flow conditions, and trophic status.
Availability of suitable pelagic habitat for adult striped bass in Lake Norman in 1996 was
, generally similar to historic conditions. Reservoir-wide habitat elimination occurred for about a month in 1996, and was similar to conditions observed in 1995.
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\ All chemical parameters measured in 1996 were witain the concentration ranges previously reported for the lake during both MNS preoperational and operational years. As has been observed historically, mangmese concentrations in the bottom waters in the summer and fall of 1996 oAen exceeded the North Carolina water quality standard. This is characteristic of -
waterbodies that experience hypolimnetic deoxygenation during the summer.
PHYTOPLANKTON DATA The maximum chlorophyll a concentration of 16.82 mg/m3 was well below the North Carolina Water Quality standard of 40 mg/m2 . Chlorophyll a concentrations at locations during 1996 were generally within ranges reported during previous years, and considerable spatial variability was observed.
Total phytoplankton densities and biovolumes observed in 1996 were within ranges of those observed during previous years. 'Ihe maximum density and biovolume were below state standards of 10,000 units /ml and 5,000 mm2 /m3, respectively, and no bloom conditions vwe g
recorded at times of sampling. ~1he lowest lakewide mean density occurred in February, and the highest in May; while the minimum mean biovolume was in August and the maximum occurred in February. As was the case with chlorophyll, considerable spatial variability was noted during each sampling period.
Seston dry weights showed more variability during 1996 than during 1995, and downlake to uptake differences were more pronounced. Maximum dry and ash free dry weight were most often observed at the riverine location (69.0); while minima were most often noted in the mixing zone (2.0 and 5.0) and at LW 8.0. The proportion of ash free dry weights to dry weights were much lower in 1996 than in 1995, indicating proportionally less organic input, and higher rates of sedimentation in Lake Norman as compared to 1995.
Overall phytoplankton community composition had shifted since last year toward higher numbers and biomass of diatoms. Diatoms dominated algal standing crops during all but August, when green algae were predominant. Cryptophytes and blue green algae were less important during 1996 than in 1995. The most abundant diatom was the pennate Tabellaria fenertmta, and the most common green algae were unidentified coccoid forms and the desmid Cosmarium asphemsporum var. strigosum.
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( l ZOOPLANKTON DATA Total zooplankton standing crops were generally highest in Febnury'and lowest in August and November. 'this represented a shiR from 1995 when peaks occurred in May. Densities wwe most oAen highest in epilimnotic samples. Few consistent spatial patterns were i observed in 1996, with the exception of Novemtar, when densities increased from downlake
, to uplake locations.
i Long term trends shor.ed much higher year-to-year variability at uptake or Background
- Locations than at Mixing Zone locations. In most cases, epilimnetic zooplankton densities.
- during 1996 were within ranges of those observed in previous years since 1987, except that long term maximum densities for February occurred in 1996 at Locations 2.0 and 11.0, and the long term maximum density for August occurred this year at Location 15.9. This indicates that epilimnetic zooplankton communities are mwe greatly influenced by environmental conditions at the uptake locations than at downlake locations. Location 15.9 F represents the transition zone between river and reservoir where populations are expected to be highest due to higher productivity of this dynamic region. At the locations nearest the dam (Locations 2.0 and .5.0), seasonal variations were dampened and lower overall Production.
Rotifers dominated zooplankton standing crops through most of 1996, as has been the case in previous years. Rotifers most oAen peaked in February and May, as has been the case since 1990. The relative .mndances of copepods and cladocerans weru higher this year than in i- 1995.
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FISHERIES DATA No mortalities of striped bass were reported by Duke Power Company personnel in 1996.
The temporal and spatial pattem of striped bass habitat expansion and reduction in Lake Norman during 1996 was well within the historic range.
Gill netting for stripod bass during 1995 yielded variable catches for summer and fall sampling. Summer gill netting yielded 69 fish ranging in kogth from 313 mm to 720 mm, and fall sampling yielded 95 fish ranging in length from 354 mm to 667 mm. All striped bass length and weight data collected in the study for condition factor determination were rtported to the NCWRC, for their analysis.
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! D LIST OF TABLES Page
!' Table 1 1 McGuire Nuclear Station (MNS) 1996 capacity factors 1-2 Table 2-1 Water chemistry monitoring program schedule 2 13 Table 2-2 Water chemistry meshods and detection limits 2-14 Table 2-3 Heat content calculations for Lake Norman in 1995 and 1996 2-15 Table 2-4 Comparison of Lake Norman with TVA reservoirs 2-16 Table 2 5 Lake Norman water chanistry data for 1996 2-17 Table 3-1 Mean chlorophyll a concentations in Lake Norman 3-11
, Table 3-2 Duncan's multiple range test for Chlorophyll a 3-12 Table 3-3 Total phytoplankton densities from Lake Norman 3 13 Table 3-4 Duncan's multiple range test for phytoplankton densities 3-14 Table 3 5 Duncan's multiple range test for seston in Lake Norman 5-15 Table 3-6 Phytoplankton taxa identified in Lake Norman from 1987-1996 3-16 Table 4-1 Total zooplankton densities and composition 4-10 Table 4-2 Duncan's multiple range test for zooplankton densities 4-12 Table 4-3 Zooplankton taxa identified in Lake Norman from 1987-1996 4-13 i
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LIST OF FIGURES Page Figure 21 Map of sampling locatiom on 14e Norman 2-20 4
Figure 2 2 hf.onthly precipitation near McGuire Nuclear Station 2 21 Figure 2 3 Monthly mean temperature profiles in background zone 2 22 Figu m 2-4 Monthly mean temperature profiles in mixing zone 2 24 Figure 2 5 Monthly terr.,wrature end disolved oxygen data 2-26 Figure 2-6 Monthly mean dissolved oxygen profiles mixing zone 2 27 Figure 2 7 Monthly mean dissolved oxygen in background zone 2 28 Figure 2 8 Monthly leotherms for Lake Norman 2-31 Figure 2 9 Monthly dissolved oxygen isopleths for Lake Norman 2-34 ,
Figure 2-10s Hen. content of Lake Norman 2 37 Figure 210b Dissolved oxygen content of Lake Norman 2 37 Figure 211 Striped bass habitat in Lake Norman 2 38
! Figure 31 Chlorophyll a mes.surements of Lake Norman 3 25 Figure 3 2 Mean chiorophyll a concentrations by yene 3 26 Figure 3 3 Chlorophyll a concentrations by location 3 27 Figure 3-4 Class composition of phytoplankton 3 29 Figut 3-5 Annual lakewide Myxophycean index from 1988-1996 3-30 Figuo 41 Zooplankton density by sample location in Lake Norman 4-14 j Fist 2 Lake Norman zooplankton densities among years 4-15 Figui 3 Lake Norman zooplankton composition by month and location 4-17 Figure 4-4 Lake Norman zooplankton composition among years 4-18 i
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CHAPTER 1 O McGUIRE NUCLEAR STATION OPERATIONAL DATA
)
INTRODUCTION As required per the National Pollutant Discharge Elimination System (NPDES) permit number NC0024392 for McGuire Nuclear Station (MNS) issued i,y the North Carolina Department of Environment, Health r.ad Natural Resources (NCDEHNR), the following annual report has been preparal. This report summarizes environmental monitoring of Lake Norman conducted during 1996.
OPERATIONAL DATA FOR 1996 Monthly capacity factors of MNS during 1996 averaged over 50% fc all months for both units except in April, May and June for Unit 1 (Table 1-1). During July, August, and September, when conservation of cool water an/ discharge tempemtures are most critical, the thermal limit for MNS increases from a monthly average of 95'F to 99 0F. The average monthly discharge 0 0 0 0 0 temperature was 95.8 F (35.4 C) for July,98.3 F (36.8 C) for August, and 93.4 F (34.1 C) for September 1996. Low level intake water was pumped by Unit I for additional cooling from September 18 to 29,1996. 'Ihe volume of cool water in Lake Nonnan was tracked throughout the year to ensure that an adequate volume was available to comply with both the Nuclear ,
Regulatory Commissim Technical Specification requirements and the NPDES monthly discharge water temperature limit.
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Table 11. Average asenthly espadty factors (%) calentated from daily unit capadty O
factors [Not Generation (Mwe per unit day) x 100 / 24 h per day x 1129 mw per unit l and anostbly everage discharge water temperatures for McGuire Nuclear Station during 1996.
NPDES DISCHARGE CAPACITY FACTOR (%) TEMPERATURE i
, Month Unit 1 Unit 2 Station Monthly Average Average Average Average OF OC January 11.2 101.3 56.2 61.4 16.3 February 90.7 102.7 95.2 63.6 17.6 March 101.2 101.2 101.2 69.1 20.6 April 100.7 12.9 56.8 72.4 22.4 ;
May 99.7 14.3 57.0 77.5 25.3 June 95.4 0.0 47.2 84.4 29.1 July 97.1 89.1 93.1 95.8 35.4 August %.9 97.7 97.3 98.3 36.8 September 97.5 95.1 %.3 93.4 34.1 October 88.7 71.5 80.1 84.4 29.1 60.5 57.3 69.7 20.9 O November 54.1 December 93.7 101.7 97.7 69.7 20.9 l
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CHAPTER 2 LAKE NORMAN WATER CHEMISTRY INTRODUCTION f The objectivn of & viater chemistry portion of the McGuire Nuclear Station (MNS)
NPDES Main.aance Monitoring Program are to:
- 1) maintain continuity in Lake Norman's chemical data base so as to allow detection of J
- 1 any significant station-induced and/or natural change in the physicochemical l I
structure of thelake; and :
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- 2) compare, where appropriate, those physicochemical data to similar data in other l hydroge wer reservoirs and cooling impoundments in the Southeast. j This year's report focuses primarily on 1995 and 1996. Where apptor 'ste, reference to pre- l 1995 da*.a tvill be made by citing reports previously subenitted to the North Carolina Department of Environment, Health, and Natural Resources (NCDEHNR).
METHODS AND MATERIALS j i
'the completo water chemistry monitoring program, including specific variables, locations, depths, and frequencies is outlined in Table 2-1. Sampling locations are identified in Figure 2-1, whereas specific chamical methodologies, along with the appropriate references are presented in Table 2-2. Data were analysed using two approaches, both of which were consistent with earlier studies (Duke Power Company 1985,1987,1988a,1989,1990,1991, ;
1992, 1993, 1994, 1995, 1996). The first method Hvolved partitioning the reservoir into -
mixing, background, and discharge mones, and making comparisons among zones and years, i
la this report, the discharge includes only Location 4; the mixing zone encompasses Locations 1 and 5; the background zone includes Locations 8,11, and 15. The second
! approach emphasized a much broader lake-wide investigation and encompassed the plotting l of monthly isotherms and isopleths, and summer-time striped bass habitat. Several quantits-l 2-1 1
tive =6th were also perfonned; these included the cal =le of the areal byg-"A oxygen deficit (AHOh, ximum whole water colman and hypolimnion oxygen content, snaulmum whole water column and hypolimnion heat content, mean spilimnion and hyp='s beating rates over the stratified period, and the Birgeon host 4
budset.
i Host (Kcal/cm') and oxygen (m3 /cm 8 or mg/L) content of the reestvoir were calculated I
according to Hutchinaan (1957), using the following equation: l 1
1 Lt = A,1. ' % TO
- Az . dz
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where; Lt = reservoir best (Kcal/cm*) or oxygen (mg/ce') aardant ;
Ao = surfeos area of reservoir (cen2)
TO = mean temperature (* C) or oxygen cantant oflayer z Az = area (om2) at depth z ds = depth interval (om) g = eurface 4 = anavisman depth RESULTS AND DISCUSSION Precipitation Amount Total annual prooipitation in the vicinity of MNS in 1996 (39.6 inches) was appreciably less than measured in the 1995 (49.5 inches) (Figure 2-2). 'the highest total monthly sinfall in 1996 ocouned in June with a value of 5.74 inches.
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~ Temperature and Dissolved Oxygen Water temperatures measured in 1996 illustrated similar temporal and spatial trends in the background and mixing zones (Figures 2 3,2-4). Water tempsatures in the winter of 1996 were consistently cooler by aproximately 12.5 *C throughout the water column, as compared to 1995, in both zones (Figure 2 3,2-4). No major difTerences between 1995 and 1996 water temperatures were observed in either the mixing or background zones for the remainder of the lake's heating period. Some inter year variability in water temperatures during certain months were observed, but these conditions were well within the observed historical variability and were not considered of biological significance (Duke Power Company 1985, 1989, 1991, 1993. 1994, 1995, 1996). The fall and early-winter temperature differences observed between 1995 and 1996 can be partially explained by variability in sampling. The October,1996 data were collected approximately ten days later in the month than in 1995, and as a consequence would be expected to exhibit cooler i
temperatures. (Note that no temperature data are available for the month of November 1996 due to equipment malfunction.) Despite some seasonal and spatial variability in temperature data between 1995 and 1996, the 1996 temperatures were well within the historic range (Duke Power Company 1985,1989,1991,1993.1994,1995,1996).
Temperature data at the discharge location in 1996 were generally similar to that measured in 1995 (Figure 2 5) and historically (Duke Power Company 1985,1987,1988a,1989,1990, 1991, 1992, 1993, 1994, 1995, 1996). The warmest disclmrge temperature of 1996 occurred in August and measured 36.9 *C, or slightly less than the historic maximum of 37.0 'C measured in August,1995 (DUKE POWER COMPANY 1996). Temperatures were appreciably less in December,1995 than in December,1996 becau*: of plant inactivity on the day of sampling in 1995.
. Seasonal and spatial patterns of DO in 1996 were reflective of the patterns exhibited for V temperature, i. e., generally similar in both the mixing and background zones (Figures 2-6 2-3
and 2 7). Winter and spring DO values in 1996 were generally equal to or slightly higher than measured in 1995, and may have been related to the cooler water column temperatures measured in 1996 versus 1995. 'the cooler water temperatures measured in 1996 would be expected to exhibit a higher oxygen content because of the direct effect of temperature on oxygen solubility, and indirectly vla an enhanced convective mixing regime wha would promote romeretion. Summer DO values in 1996 were highly variable throughout the water t
column in both the mixing and background sones ranging from highs of 6 to 8mg/L in the surface waters to lows of 0 to 2mg/L in the bottom waters, as has been observed in previous years (Duke Power Company 1985,1987,1988a,1989,1990,1991,1992,1993,1994,1995, 1996). All dissolved oxygen values recorded in 1996 were well within the histo-ic range (Duke Power Company 1985, 1987, 1988a, 1989, 1990, 1991, 1992, 1993,1994, 1995, 1996).
Fall and early winter DO values were generally similar between the two years in both zones.
Some interannual differences were observed in the October data and at least partially reflect O
variability in sampling schedule, as discussed entlier (flote that no dissolved oxygen data ,
are available for the month of November,1996 due to equipment malfunction). Interannual differences in DO are common in Southeastern reservoirs, particularly during the stratified period, and can reflect yearly differences in hydrological, meteorological, and limnological forcing variables (Cole and Hannon 1985; Pett:1984).
'the seasonal pattern of DO in 1996 at the discharge location was similar to that measured historically, with the highest values observed during the winter and lowest observed in the summer and early fall (Figure 2-5). Generally, DO salues in 1996 were equal to or slightly greate than 1995 values throughout the year. All DO values measured in 1995 and 1996 were well within the historic range (Duke Power Company 1985,1987,1988a,1989,1990, 1991, 1992, 1993, 1994, 1995, 1996). The lowest DO concentration measured at the
' discharge location in 1996 (5.8 mg/L) occurred in August, and was almost one milligram per liter granter than the yearly minimum of 4.9 mg/L measusad in July,1995 (Figure 2-5).
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Reservoir wide Temperature and Dissolved Oxygen
'the monthly reservoir-wide temperstwo and dienc0ved oxygen data for 1996 are presented in Figww 2-8 and 2 9. 'these data are similar to that observed in previous years and are i- characteristic of cooling impoundments and hydropower reservoirs in the Southeast (Cole and Hannon,1985; Hannon et. al.,1979; Potts,1984). For a detailed discussion on the i seasonal and spatial dynamics of temperature and dissolved oxygen during both the cooling and heating periods in Lake Nwman, the reader is referted to earlier reports (Duke Power Company 1992,1993,1994,1995,1996).
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'the seasonal heat content of both the entire water column and the hypolimnion for Lake Norman in 1996 are presented in Figwe 2-10s; additional information on the thermal regime l in the reservoir for the years 1995 and 1996 are found in Table 2-3. Annual minimum heat !
content for the entire water column in 1996 (5.47 Koal/cm'; 5.3 *C ) occurred in early.
8 February, wheroes the maximum heat content (27.96 Koal/cm ; 27.3 *C) occurred in August.
Ileet centent of the hypolimnion exhibited somewhat the same temporal trend as that observed for the entire water column. Annual minimum hypolimestic heat content occurred in February and measured 3.30 Koal/cm' (4.9 *C ), whereas the maximma occurred in August and snessured 15.2 Koallom' (22.9 *C ). Heating of both the entire water column and the hypolimnion occurred at approximately a linser rate from minimum to maximum heat l content. 'the mean heating rate of the entire water column equalled 0.111 Koal/cm'/ day :
4 versus 0.059 Koal/cm8 / day for the hypolimnion. The 1996 heat content data were generally similar to that observed in 1995 and earlier years (Duke Power Company 1992,1993,1994, 1995,1996). ;
'the seasonal oxygen oc 'mt and percent esturation of the whole water column and the hypolimnion are depicted in Figwe 2-10b. Additional oxygen data can be found in Table 2-
- 4 which presents the 1996 AHOD for Lake Norman and contrasts it with similar estimates for 18 TVA reservoirs. Reservoir oxygen content was greatest in mid-winter when DO q content measured 12.5 mg/L for the whole water column 11.5 mg/L for the hypolimnion. ;
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Percent saturation valuu at this time approached 102% for the entire water column and 93%
for - the hypothanion. Beginning in early-spring, oxygen content began to decline
- , 4tr!y in both the whole water column e r) the hypolimnion, and continued to do se in a linear fashi m until svaching a mmiman in mid-summer. Minimum summer DO values for the entire water column measured 4.4 mg/L (56.9% saturstion), whereas the minimum for the hypollennion was 0.7 mg/L (8.3% saturation). The mean rete of DO decline in the I i
hypolimnion over the stratifled period, i.e., the AHOD, was 0.044 mg/cm'/ day (0.066 mg/L/ day) (Figure 210b ), and is similar to that measured in 1995 (Duke Power Company 1996).
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i Hutchinson (1938,1957) proposed that the decrease of dissolved oxygen in the hypolimnion !
of a wri+ty should be related to the predactivity of the 66--:,,n!c zone. Mortimer (1941) W -d a similar perspective and proposed the following criteria for AHOD 8
associated with various trophic states; oligotrophic - 5 0.025 mg/cm / day, - : A f 's -
0.026 mg/cm'/ day to 0.054 mg/cm'/ day, and outrophic - 2 0.055 mg/cm'/ day. Employing these limits, Lake Norman should be classified as -- mph based on the calculated ,
AHOD value of 0.044 mg/cm'/ day. The oxygen based mesotrophic classification agrees
. well with the : AFA classification based on chlorophyll a levels (Chapter 3). The 1996 {
AHOD value is also similar to that found in other Southeastem reservoirs of comparable l depth, chlorophyll a status, and secchi depth (Table 2-4). :
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Striped Bass Habitat Suitable pelagic habitat for adult striped bass, defined as that layer of water with ,
temperatures s 26 *C and DO levels 2 2.0 mg/L, was found lake wide from late-September 1995~ through early July 1996. Beginning m July 1996, habitat reduction proceeded rapidly ;;.4.sut the reservoir both as a result of deepening of the 26 *C [
isotherm and metalimnetic and hypoliinnetic deoxygenation (Figure 2-11). Habitat r4+
was most severe fkom mid July to mid-August. Temperature and dissolved oxygen ;
measurements on 27 August revealed the presence of suitable habitat in the mid to upper ;
2-6 I
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4 portions of the reserve't. . Habitat measured in the upper reaches of the reservoir appsered to l be influenced by discharges from Lookout Shoals Hydroelectric facility which were l noraewhat cooler than ambient conditions in Lake Norman. Upon entering Lake Norman, l this water apparently mixes and then proceeds as a subsurface underflow (Ford 1985) as it migrates downriver.
Physicochemical habitat was observed to have expanded appreciably by mid September ;
i primarily as a resuh of epilimnion cooling and deepening, and in response to changing meteorological conditions. The temporal and spatial pattern of striped bass habitat expansion l and reduction observed in 1996 was similar to that previously reported in Lake Norman ,
and many other Southeastem reservoirs (Coutant 1985, Matthews 1985, Duke Power ;
Company 1992, DUKE POWER COMPANY 1993, 1994, 1995, 1996). The duration of l habitat elimination in 1996 extended from about mid-July to mid August, or about one
' month, and was well within the historic range. No mortalities of striped bass were reported in 1996 during weekly habitat assessments by Duke Power Company personnel in the summer.1hese conditions were similar to that in 1994 when no mortalities of striped bass were reported by local fishermen or observed by Duke Power Company personnel.
Tubidity and Specific CW=ar*
l Surface turbidity values were generally low at the MNS discharge, mixing zone, and mid-lake background locations during 1996, ranging from 2.0 to 21 NTUs (Table 2-5). Bottom turbidity values were also relatively low over the study period, ranging from 3.3 to 23 NTUs (Teble 2-5). These values were similar to those measured in 1995 (Table 2-5), and ;
- well within the historic range (Duke Power Company 1989, 1990, 1991, 1992, 1993, 1994, 1995,1996).
Specific conductance in Lake Norman in 1996 ranged from 52 to 74 umho/cm and was similar to that observed in 1995 (Table 2-5) and historically Ouke Power Company 1989,1992, 1993, 1994, 1995, 1996). Specific conductance in surface and bottom waters 2-7.
. . ~ . . . _ . . - - - . . _ _ - , _ - , - - - . . - . - - - - .- - . -
4 was generally similar throughom the year except in late fall at several of the deeper locations wher bottom waters averaged about 5 to 10 umhonfcm higher than surface values.
- - These hxeoases in coMuctance were undoubtedly related primarily to the release of soluble iron and manganees from the lake bottom under anoxic conditions (Table 2 5). This phenomenon is common in both natural lakes and reservoirs that exhibit hypolimnotic 4
oxygen depletion (Hutchinson 1957, Wetzel 1975).
pH and Alkalinity I
During 1996, pH and alkalinity values were similar among MNS discharge, mixing and .
background mones (Table 2 5); they were also similar to values measured in 1995 (Table 2-5) and historically (Duke Power Company 1989,1992, 1993, 1994, 1995). Individual pH values in 1996 ranged from 6.1 to 7.0, whereas alkalinity ranged from 4.6 to 14.0 mg /L of i CaCOs.
r Major Cations and Anions l
The concentrations (mg/L) of major ionic species in the MNS discharge, mixing, and mid-lake backsmund nones are provided in Table 2-5. The overall ionic composition of Lake Duke Power Company 1989,1992, 1993, 1994, 1995, 1996). Lake wide, the major cations were sodium, calcium, magnesium, and potsasium, whereas the major anions were bicar-bonate, sulfate, and chloride.
Nutrients 4-Nutrient concentrations in the discharge, mixing, and mid-lake background zones of Lake l .
Norman are provided in Table 2-5. Overall, nitrogen and phosphorus levels in 1996 were l similar to those measured in 1995 and historically (Duke Power Company 1989,1990,1991, i
1992,1993,1994,1995,1996); they were also characteristic of the lake's oligo-mesotrophic l_
j status. Ammonia nitrogen concentrations ired in bottom waters in each of the two i
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l 2-8
l mones and at the discharge location during the summer and fall, concurrent with the develop-ment of anoxic conditions. Total and soluble phosphorus concentrations in 1996 were similar to values recorded in 1995 and historically (Duke Power Company 1989, 1990, i
1991, 1992 , 1993, 1994, 1995, 1996).
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Metals 1
Metal concentrations in the discharge, mixing, and mid-lake background zones of Lake Norman for 1996 were similar to that measured in 1995 (Table 2-5) and historically (DUKE l POWER COMPANY 1989, 1990, 1991, 1992, 1993, 1994, 1995, 1996). Iron concen- l tre.tions near the surface were generally low (s 0.1 mg/L) during 1995 and 1996, whereas i
iron levels near the bottom were slightly higher during the stratified period, particularly in early fall. Similarly, manganese concentrations in the surface and bottom waters were generally low (s 0.1 mg/L) in both 1995 and 1996, except during the summer and fall when bottom waters were anoxic (Table 2-5). " Ibis phenomenon, i.e., the release of imn and
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manganese from the bottom sediments due to solubility changes induced by low redox conditions (low oxygen levels), is common in stratified waterbodies (Wetzel 1975).
Manganese concentrations near the bottom rose above the NC water quality standard (0.5 mg/L) at various locations throughout the lake in summer and fall of both years, and is characteristic of historic conditions (Duke Power Company 1989, 1990, 1991, 1992, 1993, 1994, 1995, 1996). Heavy metal concentrations in Lake Norman never approached NC water quality standards, and there were no consistent appreciable differences between 1995 and 1996.
FUTURE STUDIES No changes we planned f>s the Water Chemistry portion of the Lake Norman maintenance monitoring program during 1997.
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SUMMARY
4 Temporal and spatial trends in water temperature and DO data collected in 1996 were similar to those observed historically. Temperature and DO data collected in 1996 were within the range of previously measured values.
Reservoir-wide isotherm and isopleth information for 1996, coupled with heat content and
! hypolimnetic oxygen data, illustrated that Lake Nonnan exhibited thermal and oxygen dynamics characteristic of historic conditions and similar to other Southeastem reservoirs of comparable size, depth, flow conditions, and trophic status.
Availability of suitable pelagic habitat for adult striped bass in Lake Norman in 1996 was generally similar to historic conditions. Reservoir-wide habitat elimination occurred for i about a mouth in 1996, and was similar to conditions observed in 1995. No mortalities of striped bass were reported by Duke Power Company personnel or local fishermen in 1996. ,
All chemical parameters measured in 1996 were within the concentration ranges previously reported for the lake during both MNS preoperational and operational years. As has been 1
i observed historically, manganeee concentrations in the bottom watas in the summer and fall
! of 1996 often ex=wlad the NC water quality standard. 'Ihis is characteristic of waterbodies that experience hypolimnetic deoxygenation during the summer.
I
! LITERATURE CITED 1
Coutant, C. C.1985. Striped bass, temperature, and dissolved oxygen: a speculative l
hypothesis for environmental risk. Trans. Amer. Fisher. Soc. 114:31-61.
l Cole, T. M. and H. H. Hannan.1985. Dissolved oxygen dynamics. In: Reservoir i Limnology: Ecological Perspectives. K. W. *Ihornton, B. L. Kimmel and F. E. Payne editors. John Wiley & Sons. NY.
Duke Power Company.1985. McGuire Nuclear Station,316(a) Demonstration. Duke Power Company, Charlotte, NC.
2-10
__ .- .: = . . . . . . . . _ . - . . . - - _ _ - . - . --.-.=.-;-.,------.
i Duke Power Company.1987. Lake Norman maintenance monitoring program: 1986 mammary.
Duke Power Company.19882. Lake Norman maintenance monitoring program: 1987 mammary.
Duke Power Company. IS88b. Mathematical modeling of McGuire Nuclear Station thermal discharges. Duke Power Company, Charlotte, NC.
Duke Power Company.1989. Lake Norman maintenance monitoring program: 1988 summary.
Duke Power Company.1990. Lake Norman maintenance monitoring program: 1989 summary.
Duke Power Company.1991. Lake Norman maintenance monitoring program: 1990 summary.
Duke Power Company. 1992. Lake Norman maintenance monitoring program: 1991 l summary.
Duke Pcwer Company 1993. Lake Norman maintenance monitoring program: 1992 summary.
Duke Power Company. 1994. Lake Norman maintenance monitoring program: 1993 ,
summary. ,
Duke Power Company. 1995. Lake Norman maintenance monitoring program: 1994 summary. ,
Duke Power Company. 1996. Lake Norman maintenance monitoring program: 1995 summary.
Ford, D. E. 1985. Reservoir transport processes, in: Reservo!r Limnology: Ecological Perspectives. K. W. 'Ihornton, B. L. Kimmel and F. E. Payne editors. John Wiley &
Sons. NY. ,
Hannan, H. H.,1. R. Fuchs and D. C. Whittenburg. 1979 Spatial and temporal patterms of temperature, alkalinity, dissolved oxygen and conductivity in an oligo-mesotrophic, deep-storage reservoir in Central Texas. Hydrobilologia 51 (30);209-221.
Higgins, J. M. and B. R. Kim.1981. Phosphorus retention models for Tennessee Valley Authority reservoim. Water Resow Res., 17:571 576.
i w
1 2-11
liiggins, J. M., W. L. Poppe, and M. L. Iwanski.1981. Eutrophication analysis of TVA reservoirs. In: Surface Water Impoundments. H. O. Stefan, Ed. Am. Soc. Civ. Eng.,
NY, pp.404-412.
Hutchinson, G. E.1938. Chemical stratification and lake morphometry. Proc. Nat. Acad.
Sci.,24:63-69.
Ilutchinson, O. E.1957. A Treatise on LUnnology, Volume I. Geography, Physics and Chemistry. John Wiley & Sots,NY. .
Hydrolab Corporation.1986. Instructions for operating the Hydrolab Surveyor Datasonde.
Austin, TX.105p.
Matthews, W. J., L. G.11i11, D. R. Edds, and F. P. Gelwick. 1980. Influence of water quality and season on habitat use by striped bass in a large southwestern reservoir.
Transactions of the American Fisheries Society 118: 243-250.
Mortimer, C. II.1941. The exchange of dissolved substances between mud and water in lakes (Parts I and II). J. Ecol.,29:280-329.
Petts O. E.,1984. Impounded Rivers: Perspectives For Ecological Management. John Wiley and Sons. New York. 326pp.
Ryan, P. J. and D. F. R. Harleman.1973. Analytical and experimental study of transient cooling pond behavic:. Report No.161. Ralph M. Parsons Lab for Water Resources and Hydrodynamics, Massachusetts Institute of Technology, Cambridge, MA.
Stumm, w. and J. J. Morgan.1970. Aquatic chemistry: an introduction emphasizing chemical equilibria in natural waters. Wiley and Sons, Inc. New York, NY 583p.
Wetzel, R. G.1975. Limnology. W. B. Saunders Company, Philadelaphis, Pennsylvania, 743pp.
n 2-12
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a j
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li I i o !f nun imam um)4 a
i ,_ ! mm .m $s m p
! 5l mm amm a um ji -
" nas man a g l '
i l ll l1111 111l111 88888188ill llM l NJ lNu lidllh lh Lil!I o
2-13
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Table 2-2. : Water chaniary mesbods and analyte detecnon limits for the McGure Nuclear Stanon NPDES leeg-term insinanimar* program for Lake Normen.
j' Vanshian Premrvamen nsammae l.mnst Anshany,seen! Eleceommancnennen to a pH of5.1* 4*C Inse CACO 3 r'* i Alumusum Anoenic easmuseaflCPalmect nopecmon* 0.5% HNO 3 03 mg#
Anuno ties Autoessed phensee' 4*C 0.050 m9f cad ==== Atomic " ,- ._, - fansace-dwect impecuen* 0.5%HNO3 0.1 pg-r' !
Coleman Atoase cememoedCP-dweetinsecmon* 0.5% HNO 0.04 mg #
Chionde Ausammeed ferncysende' 4*C 1.0 mg #
rh specific Teamperneure nickel electrode' In-sta Ipsubetsi"*
Copper Atomic " - r ', ,
- furnace-drect mpecnon*
0.5% HNO3 0.5 pg-T' Fluonde 7_ ^2 4*C 0.10seg# ,
Iron Asamme esassmoedCP-direct impecnon* OJr%HNO3 0.1mg# ,
Lead Atomse ' ,
", " - furnace <brectimpecnoa* O.5% HNO, 2.0 pg-r' '
i Magnesnan Atonne esmesson/ICPwbrect injection
- 0.5% HNO, 0.001 aus-r'
. - ; n:-: Atoense emesseea1CP-direct inyection* 0.5% HNO 3 0.003 mg -f*
Nitrine-Nitrate ' Automased cedissue r=I= *=a=' 4*C 0.050ung#
Orthophosphase Ah accoubec acid reducson' 4*C 0.005 mg -f*
w Oxygen, dissolved Tesaperenne ,
" , : " ., ' ce!!' hwas 0.1 mg -f* ,
2~ pH . Teamperumme - ,
" glass elecerede' h> eses 0.1 sad. units
- Phosphorus, total Pe+ gigesmon fonowed by ausammed ascorbic acid 4*C 0.005 as -r' **
- =a=a=a= 0.015 mg -r* **
Potassmm Atonne " __,^__ ', ," - furnace-direct impecnon* 0.5% HNO, 0.1 mg # ,
Silica Aima===a-t 6 _" ' 4*C 0.5 mg #
f Sodium Asomac =======4CPw5 rect insecnoo* 0.5% HNO3 03 mg -l'*
Sulfb Turbeduneanc,using a 4*C 1.0 mg #
Twe. Therumsenatennemeter' hearin 0.1*C' Turtndsty T ,' " ^ aturbedity'
. 4*C INRP Zine Anounc cenmon/ICP-direct injecnon* 0.5% HNO3 4 pg-r'
'U _ sed Stsees E= 6v ~.^. Protecnon Agency 1979. Methods for chemical analysis cfwater and wastes.
Envronmental Mondanns and Support Laborneory. Cis==ari, OH. :
'USEPA. 1982
'USEPA. 1984 r
- Insinanent w^ .h used instead ofdesecnon limit.
- Detecuen timitsanged danng l989. ;
t
. - - ~ , . . . _ , -_ - . - _ . . - .- -,_ _ _ _ , .
Table 2 3. liest content calculations for the thermal regime in lake Norman 1
in 1995 and 1996 .
1921 DM l Maximum areal heat content ( g cal /cm') 28,215 27,959 i'
t Minimum areal best content (g cal /cm') 7,808 5,470 ,
4 Maxinem hypolimactic(below 11.5 m) 16,036 15,243 ;
i areal best content (g cal /cm')
l Ilirgean heat budget (g cal /cm') 20,407 22,489 -
p Epilimnion (above 11.5 m) beating rate ('C / day) 0.111 0.114 Ilypolimnion (below 11.5 m) beating 0.078 0.089 rate ('C / day) e a
i l
l 1
l:
2 15
..m ,,,,v,.,... I.-w,., .,.J-,....<.,r, y--,me,.,. ,.,--.,.%.,,-,,-s-,,J,..,,,,-.m.c_.,,,,%.. r,,..--,.--.-., .,-W,,..-_.m....m.. - - - -. _ , .--
_ _ ~ _ _ _ _ . _ _ . _ . . _ _ _ _ _ . _ _ _ _ _ _ _ __ _ ___.___ _ _
Table 2-4. A comparison of areal hypolimnetic oxygen de6cks (AHOD), ====r chlorophyll a (chi a), secchi depth (SD), and mean depth of Lake Norman :
and 18 TVA reservoirs.
AHOD Summer Chi a Socchi Depth Mean Depth Reservolt (mg/cm2/ day) (ug/L) (m) (m)
Lake Nonnan 0.044 6.02 1. 7 . 10.3 TVAa Mainstem Kentucky 0.012 9.1 1.0 5.0 Pickwick 0.010 3.9 0.9 6.5 Wilson 0.028 5.9 1.4 12.3 Wheelee 0.012 4.4 5.3 Guntersville 0.007 4.8 1.1 5.3 -
Nickajack 0.016 2.8 1.1 6.8 Chickamauga 0.008 3.0 1.1 5.0 Watts Bar 0.012 6.2 1.0 7.3 Fort London 0.023 5.9 0.9 7.3 Tributary Chatuge 0.041 5.5 2.7 9.5 Cherokee 0.078 10.9 1.7 13.9 Douglas 0.046 6.3 1.6 10,7 Fontana 0.I13 4.I 2.6 37.8 Hiwassee 0.061 5.0 2.4 20.2 Nonis 0.058 2.1 3.9 16.3 South Holston 0.070 6.5 2.6 23.4 Tims Ford 0.059 6.1 2.4 14.9 Watauga 0.066- 2.9 2.7 24.5 a Data from Higgins et at (1980), and Higgins and Kim (1981) l I
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- LAKE NORMAN 6IMIPED EMSS HABITAT
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Figure 2-11 Striped bass habitat (temperatures 5 26
- C and dissolved oxygen 2 2.0 mg'L) in Lake Norman in June, Juh, August, and September 1996.
2-38
C 240-
' : LAKE NORMAN STRIPED BASS HABITAT
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- LAKE NORMAN SIKlPED BASS HABITAT 8.0 11.0 13.0 15.015.9 62.0 69.0 72.0 80.0 23531.0 4
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O j Figure 2-11.- Continued.
2-39
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- LAKE NORMAN SIMIFtu BASS HABITAT 8.0 11.0 13.0 15.015.9 62.0 69.0 72.0 80.0 23531.0
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[ Figure 2-11. Continued.
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2 I
l l
6 CHAPTER 3 ;
s PHYTOPLANKTON ;
INTRODUCTION I l ,
'g
- Phytoplankton population pwes.d:s were monitored in 1996 in accordance with the e .
NPDES permit for McGuire Nuclear Station. 'Ibe objectives of the phytoplankton section for
- the Lake Nonnan Maintenance Monitoring Program are to
- 1) Describe quarterly pettoms of phytoplankton standing crop and, species
- composition throughout Lake Norman; and i
- 2) Compare phytoplankton data collected dunng this study (February, May, August, November 1996) with historical data collected during those same months.
Pivvious studies on Lake Norman have reporter m nr &6le spatial and temporal variability in phytoplankton standing crops and taxonomic # (Duke Power Company 1976, 1985; Menhinick and Jensen 1974; Rodriguez 1982). Rodriguez (1982) classified the lake as oligo-mesotrophic based on phytoplankton eta =d=ce, distribution, and taxonomic composition.
METHODS AND MATERIALS 1
Quarterly sampling was conducted at Locations 2.0, 5.0, 8.0, 9.5,11.0,13.0,15.9, and 69.0 i- in Lake Norman (see map oflocations in Chapter 2, Figum 2-1). Duplicate composite grabs L from 0.3,4.0, W d.0 m (i.e., the euphotic zone) were taken at all locations. Sampling was copaw*wi on 7 : ebruary, 23 May, 22 August, and 13 November 1996. Phytoplankton j- density, biovolume and taxonomic composition were determined for samples collected at Locations 2.0, 5.0,9.5,11.0, and 15.9; chlorophyll a concentrations and seston dry and ash-
! free dry weights were determined for samples from all locations. Chlorophyll a and total phytoplankton densities and biovolumes are used in determining phytoplankton standing 1
e
_., , _ . . . . s . - . . . -, -- - . . . _ . _ . . - _ . . _ , . . - . . - . . _ . . . ~ - . . . _ . . .. .
I crop. Field sampling methods, and laboratory methods used for chlorophyll a, seston dry b weights and population identification and enumeration were identical to those used by Rodriguez (1982). Data collected in 1996 were compared with corresponding data from quarterly monitoring beginning in August 1987.
A one way ANOVA was performed on chlorophyll a concentrations, phytoplankton densities and seston dry and ash free dry weights by quartes. This was followed by a Duncan's Multiple Range Test to determine which location means were significantly different.
RESULTS AND DISCUSSION l Standing Crop Chlorophyll a O Chlorophyll a concentrations ranged from a low of 0.75 mg/m3 at Location 69.0 in February to a high of 16.82 mg'm3 at Location 9.5 during the same month (Table 3-1, Figure 3-1). All values were well below the North Carolina water quality standard of 40 mg/m3 (NCDEHNR 1991). The range of chlorophyll observed in 1996 was similar to those observed during previous years since 1987 with the exception of November. The lakewide annual mean for November 1996 was the highest ever observed for this month (Figure 3-2). Lake Norman continues to be in the mesotrophic range.
During 1996, chlorophyll a concentrations showed considerable spatial variability with maximum and minimum values observed at different locc.tions each season. The trend of increasing chlorophyll conentrations from downlake to uplake, which had been observed in 1994 (Duke Power Company 1995), was only noted in May (Table 3-1, Figure 3-1).
Locations 15.9 (uplake, above Plant Marshall) and 69.0 (the uppermost, riverine location) had significantly higher chlorophyll values than Mixing Zone locations (2.0 and 5.0) in May 0
( and August; while Locations 2.0 and 5.0 had significantly higher concentrations in February 3-2
t i
(Table 3-2). During November, Location 15.9 had the highest chlorophyll values, while -
I acetion 69.0 had the loweet. Chlorophyll concentrations at Location 69.0 varied widely
- . with the maximum lakewide quarterly value ocurring there in August, and minimum lakewide values observed at this location in February and November. This type of overall
- variability was similar to that observed during 1995 (Duke Power Company 1996). The riverine mone of a reservoir is subject to wide fluduations in flow depending, ultimately, on meteorological conditions (Thornton 1992), although influences may be raoderated due to upstream dams. During periods of high flow, algal production and standing crop would be -
l depressed due in great part to washout. Conversely, production and standing crop would increase during periods oflow flow and high retention time. In contrast to high variability i observed uptake, chlorophyll a concentrations at Location 2.0, the most dcwnlake location, were within the same range as Location 5.0, the other Mixing Zone location, during all sampling periods of1996.
Chlorophyll a lakewide annual means by quarter ranged from approximately 7 mg/m3 in
' May to 11 mg/m 3in November. The November lakewide mean was the highest ever observed for this month since the study began (Figure 3-2). A trend of increasing values from May through November was observed among lake sneens, as was the case in 1995 and 1988.
Average annual chlorophyll concentrations during the period of record have varied considerably. During February, Locations 2.0, 5.0,~ 8.0, and 9.5 had the highest concentrations ever observed for this month; while those at the uptake location (15.9 and 69.0) were among the lowest ever recorded for February (Figure 3-3). November of 1996 i
^
also showed overall study period peaks at all but Locations 13.0 and 69.0. The November ,
peaks at most locations were the continuation of a trend of increasing chlorophyll values since 1993. During May and August, annual peaks occurred betw 1991 and 1994.
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--ww. e ---- ,
E i
Total Abundance Phytoplankton abundance is represented by total density and biovolume 'fhe lowest density and biovolume for 1996 ov:urred at Location 15.9 (644 unit <ml, 421 mm3/m3). The:
{
maximum annual density occured at the same location i: November (4362 units /ml); while the highest biovolume (3848 mm3/m3) was noted at Location 11.0 in May (Table 3-3, Figure 3-1). 'Ihese maximum values were still below the NC state standard definition for phytoplankton blooms of greater 10,000 unita/ml and 5,000 mm3 /m3 (NCDEHNR 1991). 1 Total densities at locations in the Mixing Zone (2.0 and 5.0) were in the same statistical range from May through November, as was the case in 1995; while in February, Location 2.0 had a significantly higher density than Location 5.0 (Table 3-4). From May through November, Location 15.9 had significantly higher densities than Mixing Zone locations. In February, this uptake location dess- --tod the lowest density; while Location 2.0 had a significantly higher density than all other locations.
r A trend of increasing densities from downlake to uplake was observed from May through November; while the opposite was noted during February (Figure 3-1). Similar downlake-uptake trends were observed in 1994; while few consistent spatial patterns occurred during 1995 (Duke Power Ccmpany 1995,1996).
Seston Seston dry weights represent a combination of algal matter, other organic material, and 4
inorganic components. Location 69.0, the uppermost riverine location, had the highest seston dry weights during all sample periods, and values were significantly higher than all other locations from May thmugh November (Table 3-5). In most cases, a trend of increasing values from downlake to uptake was observed, as was the case with other phytoplankton parameters (Figure 3-1). Downlake to uplake differences were more 1 pmnounced during 1996 than in 1995, and maximum values were ir. cater, and minimum S
3 ,
..s.__, y - ,,-c. , - , ,
l l
l values less, than those noted during 1995. Mean values during 1996 ranged from 0.8 mg/l at !
Locations 8.0 and 11.0 in August, to 15.15 mg/l at Location 69.0 in February; coreograd to a
- _ range of 2.65 to 7.46 mg/l in 1995 (Duke Power Company 1996). This in( ' m greater variability in inputs and flow rates prior to sampling, conditions similar to those observed during 1994 (Duke Power Company 1995).
i Seston ash free dry weights represent organic material and may reflect trends of algal <
standing crop parameters. For the most past, this was not the case during 1996; most 3
! notably, during 'iebruary when uptake locations had Ge lowest density and chlorophyll
, values, they also had the highest ash free dry weights. In terms of statistical significance,
- patterns were not as well defined as with seston dry weights. Location 69.0 had significantly higher values than other locations only in February and August; and during May, no i
significant differences were noted among all sampling locations (Table 3-5). The annual maximum and minimum ash free dry weight were both observed during February: 0.24 mg/l at Location 5.0, and 2.9 mg/l at Location 69.0. Lakewide, ash free dry weights this year were Id lower than those of 1995, and the proportions of ash free dry weights to seston dry weights l were loww than last year, indicating proportionally lower inputs of organic material into Lake Norman, and presumably higher rates of sedimentation from runoff. This was similar to what had been observed during 1994 (Duke Power Company 1995).
- Secchi Depths Secchi depth is a measure of light penetration. Secchi depths were often the inverse of suspended sediment (seston dry weight), with the lowest depths at Locations 13.0 through 69.0 and highest from Locations 9.5 through 2.0 downlake. Depths ranged from 0.2 m at Locations 15.9 and 69.0 in February to 2.40 m at Locations 2.0 through 9.5 in August (Table 3-1).-
4 3-5
Community con position Nine classes comprising 71 genera and 128 lower taxa of phytoplankton were identified in - .
samples collected during 1996, as compared to 73 genera and 120 lower taxa identified last 1
year (Table 34). The distribution of taxa within classes was'as follows: Chlorophyceae (green algae), 62; Bacillariophycer (diatoms), 29; Chrysophyceae,15; Haptophyceae and ,
Xanthophyceae, one each; Cryptophyceae (cryptophp), 4; Myxophyceae (blue green .
algae) 10; Euglenophyceae (eugimoida), 2; and Dinophyceae (dinoflagellates) 4. Since the study began in 1987, over 114 genera and more than 300 lower taxa have been recostled.
Seven new taxa were observed in 1996.
Species Compositon and Seasonal Succession Lake Norman supports a rich community of phytoplankton species. This community varies both seasonally and spatially within the reservoir. In addition, considerable variation may V duo be observed between years for the same months sampled. As mentioned earlier, no bloom conditions were observed during 1996 sampling periods, and no substantial numbers of nu.isance algae were founti.
Diatoms dominated algal densities and biovolumes during all sampiing periods except August when green algae were - numerically dominant (Figtre 3-4). Dinoflagellates dominated biovolumer,in the Mixing Zone and at Location 15.9 in August. This represents a shift in taxonomic composition from that observed during 1994-1995. During these years cryptcphytes (primarily the small flagellate Rh_ minuta) domi=*M February
- i. samples; while diatoms were predominant in May and November. As was the case in 1995, green algae dominated summer samples (Duke Power Company 1996).
- The most abundant diatom was the colonial pennate, Tabellariafenestmta. This diatom has been described as acidophilous and cosmopolitan, and common in lakes and ponds under a wide range of nutrient conditions (Lowe 1974). During August, when green algae were 3-6 i
dominant, the most common forms were unidentified coccoid greens and the small desmid ,
' (
Cormarium arphsamsporum var. strigorum. This was also the case during 1995 (Duke Power Company 1996).- ,
i CryWip and dinoflagellates were less important this year than in 1995. Blue green ,
algae, which are often implicated in wisance blooms and taste and odor psir.os, were seldom observed in large numbers, and were less Mi-it among algal communities this J
year than in past years. Densities and biovolumes of Myxcphyceae seldom exceeded 2% ,
during 1996.
Phytoplankton index Phytoplankton indexes have been used with varying iga of success ever since the concept was formalized by Kolkwitz and Marsson in 1902 (Hutchinson 1967). In 1949 ,
Nygaard proposed a series of indexes based on the number of species in certain taxonomic
, \ categories (Divisions. Classes, and Orders). We have selected the Myxophycean index to help determine long term changes in the trophic status of Lake Norman. This index is a ratio of the number of blue green algal taxa to Amenid taxa, and was designed to reflect the
" potential" trophic status; while chlorophyll gives an " instantaneous" view of phytoplankton concentrations. The index was calculated on an annual basis for the entire lake.
For the most part, the Myxophycean index tended to confir.n the conclusion that Lake Norman has been in the oligo-mesotrophic (low to intermediate) range since 1988 (Figure 3-4 5). Values were in the high, or eutrophic, range in 1989,1990, and 1992, p FUTURE STUDIES No changes were planned for the phytoplankton portion of the Lake Norman Maintenance Monitoring program during 1997.
. ~
3-7 i
,._a wm , m .--_-, , - - - , - - + ,.n , + ,e .~--- an--. , , - - , - , . ,e-r
,An O SuMurav Chlorophyll a concentrations at locations during 1996 were generally within ranges reported ;
during previous years, and Lake Norman continues to be classified as oligo-mesotrophic. ,
Lakewide chloiophyll means increased from May through November,- and the lakewide mean for November was the highest ever observed for that period. February and November chlorophyll values from Locations 2.0 through 9.5 were also the highect ever observed for these periods. The maximum chlorophyll value of 16.82 mg/m3 was well below the NC State Water Quality standard of 40 mg/m3 Considerable spatial variability was observed during 1996, as was the case last year.
Total phytoplankton densities and biovolumes observed in 1996 were within ranges of those observed during previous years. Based on NCDEHNR (1991), the maximum density and biovolume were below state standards of 10,000 units /ml and 5,000 mm3 /m3 and no bloom conditions were recorded at times of sampling. The lowest lakewide mean density occurred in Febmary, and the highest in May; while the minimum mean biovolume was in August and the maximum occurred in February. As was the case with chlorophyll, considerable spatial variability was noted during each sampling period.
Seston dry weights showed more variability during 1996 than during 1995, and downlake to uptake ditTerences were more pronounced. Maxi-mm dry and ash free dry weight were most often observed at the riverine location (69.0); while minima were most often noted in the mixing zone (2.0 and 5.0) and at Location 8.0. The proportion of ash free dry weights to dry weights were much lower in 1996 than in 1995, indicating proportionally less organic input, and higher rates of sedimentation in Lake Norman as compared to 1995.
Overall phytoplankton community composition had shifted since last year toward higher numbers and biomass of diatoms. Diatoms dominated algal standing crops during all but O August, when green algae were predominant. Cryptaphytes and blue green algae were less h
3-8
_ . _ . _ _ . ~ . . _ . _ _ . . _ _ . _ _ . _ _ . _ _ _ . . _ _ _ _ . _ . _ _ _ _ _ .
. . ~ . .
important during 1996 than in 1995. 'Ihe most abundant diatom was the pana* Tabellaria ;
-\ feartmta, and the raost' common green algae were unidentified coccoid forms and the desmid Cormarium aspheamsporum var. strigorum.
LITERATURE CITED Duke Power Company.1976. McGuire Nuclear Station, Units 1 and 2, Environ-mental Report, Operating License Stage. 6th rev. Volume 2. Duke Power Company, Charlotte, NC.
I Duke Power Company.1985. McGuire Nuclear Station,316(a) Demonstration.
Duke Power Company, Charlotte, NC.
Duke Power Company,1988. Lake Norman maintenance rnanitoring program:
1987 summary.
Duke Power Company.1995. Lake Norman maintenance monitoring program: l 1994 summary.
Duke Power Company.1996. Lake Norman maintenance monitoring program:
-\ - 1995 summary.
Hutchinson, G. E.1%7. A Treatise on Limnology, Vol. II. Introduction to the limonplankton. John Wiley and Sons, New York, NY.
Lowe, R. L. 1974. Environmental requirements and pollution tolerance of freshwater diatoms. United States Environmental Protection Agency, Cir-A=% Ohio.
Menhinick, E. F. and L. D. Jensen.- 1974. Plankton populations, p. 120-138 In L D. Jensen (ed.). Environmental responses to thermal discharges from Marshall Steam Station, Lake Norman, NC. Electric Power Research Institute, Cooling Water Discharge Project (RP-49) Report No. I 1. Johns Hopkins Univ., Baltimore MD. .
North Carolina Department of Environment, Health and Natural Resources, Division of Environmental Management (DEM), Water Quality Section. 1991,1990 Algal- ,
Bloom Report.
4
' Nygaard, G.1949. Hydrological studies of same Danish pond and lakes II. K. danske Vilensk. Selsk. Biol. Skr.
O
.3-9 e
i'
.+.-n . 6 ,. ., . . , . . , . . , . ,
l 1
Rodriguez, M. S.1982. Phytoplankton, p. 154-260 In J. E. Hogan and W. D. Adair (eds.).
Lake Norman summary, Tochical Report DUKEPWR/82-02 Duke Power Company,
- Charlotte, NC.
i Thornton, K. W., B. L. Kimmel F. E. Payne.1990. Reservoir Limnology. John Wiley and Sons, Inc. N. Y. 246 pp.
I f
I l:
i l
I l
i J
.I a
3-10 en-- e me r --n- , , .- ,- -- ~
. . ~ -
Table 3-1, Mean chlorophyll a concentrations (mg/m3) in composite samples (0.3, 5 and 8m - -
depths) and secchi depths (m) observed in Lake Norman, NC, in 1996.
Chlorophyll a Location FEB MAY AUG NOV 2.0 11.75 .ao 5.46_ 9.93
- 5.0 10.41 2.24 5.50 . 9.91 8.0 11.48 3.63 7.80 13.88 9.5 16.82 3.60 8.53 11.48 11.0 8.28 9.64 6.86 13.08 13.0 5.86 10.66 4.54 11.21 15.9 1.68 12.02 10.77 16.29 69.0 0.75 11.75 12.08 2.66 Secchi depths Location FEB MAY AUG NOV O
i 2.0 5.0 1.60 1.55 2.10 2.10 2.40 2.40 _
1.80 l.90 8.0 0.90 1.70 2.40 1.70
, 9.5 1.65 1.50 2.40 1.70 11.0 0.60 1.40 2.00 1.60 13.0 0.45 1.30 1.40 1.30 15.9 0.20 1.40 1.30 1.50 69.0 0.20 1.20 1.20 1.20 3-11
l l
Table 3-2. Duncan's multiple Range Test on chlorophyll a concentrations in Lake Norman, 1
O NC, during 1996.
February Location 69.0 15.9 13.0 11.0 5.0 8.0 2.0 9.5 Mean 0.75 1.68 5.86 8.28 10.41 11.48 11.75 16.82 May Location - 5.0 2.0 9.5 8.0 11.0 13.0 69.0 5.9 Mean 2.24 2.36 3.60 3.63 9.64 10.68 11.75 12.02 d
i August Location 2.0 13.0 5.0 11.0 8.0 9.5 15.9 69.0 Mean 4.46 4.54 5.50 6.86 7.80 8.53 10.77 12.08 O
November Location 69.0 5.0 2.0 13.0 9.5 11.0 8.0 15.9 Mean 2.66 9.91 9.93 11.21 11.48 13.08 13.88 16.29 9
O 3-12 l
l O
Table 3 3. Total mean phytoplankton densities and biovolumes from samples collected in Lake Norman, NC, during 1996.
Density (units /mi)
Locations Month 2.0 5.0 9.5 11.0 15.9 Mean FEB- 3518 2923 2950 2122 644 2431 MAY 1589 1748 1967 4316 4289 2782 AUG- 2136 2180 3506 2577 3005 2681 NOV 2420 2076 2202 2797 4362 2771 s
Biovolume (mm3/m3)
T
-, Locations Month 2.0 5.0 9.5 11.0 15.9 Mean FEB 4271 3317 3464 2078 421 2710 .
MAY 691 850 961 3848 3556 1981 AUG 1694 1415 2675 1570 2006 1872 1 NOV 1979 1683 2329 2424 3333 2350 l
l
- vn 3-13 4
Y w - ~ , - - - - -
1 i Table 34. Duncan's multiple Range Test on phytoplankton densities in Lake Norman, NC, during 1996.
February Location 15.9 11.0 5.0 9.5 2.0 Mean 644 2122 2923 2950 3518 May Locction 2.0 5.0 9.5 13.9 11.0 Mean 1590 1748 1%7 4289 4316 August Location 2.6 5.0 11.0 15.9 9.5 Mean 2136 2180 2577 3004 3506 p ,
' Q) November Location 5.0 9.5 2.0 11.0 15.9 Mean 2076 2202 2420 2797 4362 O .
3 14 y w -- ,.-.-, y-3w, y gm-. w ---. v --g- ,-3__ -,c.., _ ,- , --,,..r vi ---e
Table 3 5. Duncan's multiple Range Test on dry and ash free dry weights (mg/m3) in Lake O Norman, NC, during 1996.
DRY WEIGHT February Location 5.0 9.5 2.0 8.0 13.0 !!.0 15.9 69.0 Mean 1.12 1.20 1.76 3.25 5.49 6.21 11,82 15.15 May Location 2.0 5.0 9.5 8.0 15.9 11.0 13.0 69.0 Mean 1.25 1.77 1.82 1.92 2.53 3.02 4.58 9.39 August Location 8.0 11.0 13.0 15.9 5.0 9.5 2.0 69.0 Mean 0.80 0.80 0.98 1.lf 1.33 1.60 1.64 11.31 j Movember Location 8.0 2.0 5.0 9.5 !!.0 15.9 13.0 69.0 Mean 2.36 2.42 2.44 2.94 3.65 3.90 4.34 !1.47 l
ASH FREE DRY WElGHT February Location 5.0 9.5 8.0 13.0 2.0 11.0 15.9 69.0 Mean 0.24 0.43 0.61 0.84 1.13 1.14 1.39 2.90 May Location 2.0 15.9 5.0 9.5 8.0 I1.0 69.0 13.0 Mean 0.73 0.80 0.82 0.84 0.88 1.34 2.28 2.66 August Location 13.0 11.0 8.0 5.0 15.9 2.0 9.5 69.0 Mean 0.48 0.62 0.64 0.72 0.72 0.76 0.98 2.19 November Location 5.0 8.0 2.0 9.5 13.0 !!.0 15.9 69.0 Mean 0.71 0.80 0.80 0.90 1.22 1.22 1.39 1.89 3 15
j i
Table 3-6. Phytoplankton taxa identined in que terly samples collected in Lake Norman !
- from August 1987 to November 1996. !
l TAXON 87 88 89 90 91 92 93 94 95 96 i CLASS: CHLOROPHYCEAE :
Acev4mpone ancharieet L4mm. X X X :
Acridand== hoo&wi Reinach X Acviaanr== henru*it tagerheim X X X X X X X j A=&hoodsomw are==fi(Naes) an== X X i A./elevam (cada) Raik X X X X X X X X X X A./wpwmh Cards sensu Korsch. X X X X X X i A. gedrelds (Twnw) Lane. X X X X X X -
A. app.Cada X X Arv4nednew comroena Elwenbwg X A. Amew(seeb.)Haensil X X X i
A. su6edarw Kutaing X A. App. Ehrenhws X X ,
Amew.cew timaeticw 0. M. smkh X X X X X >
Aorryoconw armailKutsing X X ,
Cartwiefasc4diTakeda X X C app. Diestas X X X X Chanset== spp. Beaun X N'-f nr app. Ehrenbas X X X X X X X X X X :
c': ,,_. ',.chlawn Elvsabes X X X i C apinele Scherffel & peacher X X Ew 7:blowinian west a wat X X X X X X XX X X ctw w groedte av bissan X :
C Aarwv== Beobissan X X X X X ,
C spp.Nitssoh X X X X Caiawrwa c 'i-, Archa X X X X X X X X X X C mL, cr ; Nagell X X C 9 asricans 4 Nagell X X X X C pro 6ascidsean Bohlin X C spp. Nagell X X >
Cosmordsaw anulos== v. concianenn (Rab) - X West & West C g*.:: :g w v.ssrisoeum Nord. X X X X X X X X X X C contrwctime Kirchow X X X X X C patysomm(Nas.) Archw X X X i l C resaalid/ Wille X X X C asmet SchmW X X X 3-16
-W-y-,p 9-w e-9w -q m y-wr,P --J-m---g-i p --,m,- ,y,- g -y g-%gr-w yv--g y-- --,p---,,-t,----ywwe-g---,wy-m ,vy-r w 'w --"wwrwwwww '
i Table 3-6 (continued) page 2 of 9 TAXON 87 88 89 90 91 92 93 94 95 96 ,
4 c some Areiwr X X X X i C tdacrum Ralfs X X X X X X c spp.corde X X X X X X X X !
cr=cipade erscpere(Wolle) collins X X X X X X f cfauwress schmidle X C kresulark Wille X X X X X i C :ce:*-(Kirch.) WW & WW X X X X X X X X X X 4 nic.;71 in.!.;d.1xx Napli X X "
- u. pulchellem Wood X X X X X X X X X ;
c:- l::xca epp. nroun X i Klataw6rk,, ' : - Winie X X X X X X X X X X i Kassewa dankular== (Kirok.) Gay X X E. spp. Ehrenbors X X X X
, rh skgem Ehrenbws X X !
rnemin a: ::h:1(temm.)a. M. smith X X X X F. avalis (France) team. X X X X X X X Olo oryeris 6otrpider(Kutr )Nasell X :
G. sten K wains X X X X a.r' f- ::-(w w & W W)1mam. X X X X X X X X
- a. spp Neyli X X X X X X X X
, Gode=6dadersueurdan WW & WW X X ,
G nsdiasse X X X X X X X X X X Goad == wiele (thd.) Warmins X X KbcAnsrisite conforve (Schmidle) Bohlin X X X X X X X K l==sr* (Kirch.) Mobius X X X r J =sr* v. Asese schlin X r 6.se W. Wm X X X X X X X E a=6sulnards 0. s. West X X X X
, E spp. schmidle X X -X X i
Lauvr**dade c# data (Leg.) chodet X Lf-C:::(I--- ----) Printz X ,
L ,weisen (14mm.) O. M. smith - X X X X L sensale Lemmennen X X X X X X X X m___g_.ve*islauiaban* X X X X Aacreerdaha=rmedita= hosen. . X X X X X X X X X X g"*- awworv== nurm X X X X X X M pwill== Print X X X X X X -
Mose*#is elesaarmle Whittrock X X X X M spp. Asadh X X X X h
3-17
1 s Table 3-6 (continued) page 3 of 9 TAXON 87 88 89 90 91 92 93 94 95 %
Nephrocytlum agardhianum Naseli X X N. limnaticum (O.M. Smith) 0.M. Smith X X Oocystis ellyptica W. WeW X O. lacustris Chodet X O. parva Wed & West X X X X X X O.pwflla Hanagits X X X X X X O. app. Nagell X Pandorina charkowlensk Kptshikov X P. morum Bwy X X X X Pediastrum biradiorum Meyen X P. duplex Meyen X X X X X X X P. retrw v. tetroadon (Cada) Rabenhorm X X X X X X X X X X P. app. Meyen X X Planktosphaeria gelatinosa G. M. Smith X X X Quaelgula closterioides (Bohlin) Printz X X Q. lacustris (Chodat) O. M. Smith X F enedesaw abundans (Kirchner) Chodet X X X X S. abundans v. acymetrica (Scht.) O. Sm. X X X X X X X X X K abundans v. brevicauda O. M. Smith X X g S. acuminatus (Lagerheim) Chodat X X X X X X S. armatw v. 61caudatus (Oug. Prin.)chod X X X X X X X X X S. 6yusa(Twp.)Lagaheim X X X X X X X X S. byuga v. alterans (Reinsch) Hansg. y S. 6rwmash Bohlin X X S. denticulata Lagaheim X X X X X X X X X X S. dimorphus (Twp.) Kutzing X X X X X S. Ancit.asulatus O. M. Smith X 3 guakicauda(Twp.)Brebismon X X X X X X X X X X S. smithii Telling X S. app. Meyen X X X X X X Sshkocklamys conpacta Prescott X Schoederinetigers (Schroed.) Lemm. X X Selenastrum gracile Relnach X X S. minutum(Nageli)Ccilins X X X X X X X X X X S westii O. M. Smith X X X X X Sphaerocystis schotteriChodat X X X X Sphaero:osma granulatum Roy & Bliss X X Stauastrum americanum (WAW) O. Sm. X X X X S. qpiculatum Brebisson X i
\v/
3 18
\
Table 3-6 (continued) page 4 of 9
\
TAXON 87 88 89 90 91 92 93 94 95 %
S. brevispinum Brebisson X S. chwtocerus (Schoed.) O. M. Smith X X X S. curvatum W. West X X X X X X X X S. cuspidatum Brebinson X S. defectum Brebisson X X X X X X X S. dickeli v. maximum West & West X S. gladiosum Turner X
- 5. leptocladum v. sinuatum Wolle X X S. maqfeldtli v.fluminema Schumacher X X X X X S. megacanthum Lundell X X X X S. orbiculare R 1is X S.pamdoxum Meyen X X X X X X S. paradaxum v. cingulum West A West X S. paradoxum v.panwm W. West X S. sabervciatum Cook & Wille X X S. tetraccrum Rstfs X X X X X X X X X X S. turgescem de Not. X X S. spp. Meyen X X X X X p Tetraeden bifurcatum v. minor Prescou X
( T. caudatum (Cords)llansgirs X X X X X X X T. limneticum Borgo X T. lobulatum v. cmssum Prescott X T. minmum(Braun)llanagirs X X X X X X X T. muricum(Braun)llansgirs X X X X X X X T. obesum(W & W)Wille ex Brunathaler X T. pentoedkvm West & West X X T. regula Kutring X X X X T. regulare v. incus Teiling X X X T trigonum (Nageli)llanagirs X X X X X X T. trigonum v. gracile (Reinsch) DcToni X X T. spp. Kutzing X X X Termspom app. Link X X Termstrum heterocanthum (Nordst.) Chod. X Treubaria satigerum (Archer) O. M. Smith X X X X X X X X X X Westella linearis G. M. Smith X Xanthidium spp. Ehrenb-rg X O
3-19 i
- Table 3-6 (continued) page 5 of 9 TAXON 87 88 39 90 91 92 93 94 95 % <
CLASS: BACILLARIOPHYCEAE ;
Acinearnes microcephala Kwring X X X X X A. app. Bay X X X X X X X X X Anomoeoncis vitrea (Grunow) Ross X X X X X A. app. Pfitzer X >
AsterionellaAmosa Hweall X X X X X X X X X Atthepa tschariaal J. Brun X X X X X X X X X Cocamels ploesntula Ehrenbwg X X C spp. Ehrenberg X Cyclosella conta (Ehrenbwg) Kutzing X X X X C glomewa Bachmann X X C meaeg4dadaaa Kutzins X X X X X C perudastelliswa Huntedt X C stelligwa Cleve & Orunow X X X X X X X X X C app. Kutzing X X X t Cym6ella misura (Bliesch & Rabn.) Reim. X X X X X C summa (Breb.) van Huack X C Negida(Oregory)Cleve X C app. Agardh X X ;
oplanels app. Duenbes X Emmotie zaruminesis (Cab.) Kownw X X X X X X X X fngritaria crwonewis Kitton X X X X X X X X X Frwatulk' thomboides (Ehr.) de Toni X X C_- fx - app. Agardh X X Meloedm am6igua (Onm.) o. Mulla X X X X X X X X X X M Astow(Ehr.)Kutzing X X X X X X X X X M anwalata(Ehr.) Ralfs X X X X 4
M granulata v. angwrissima o. Muller X X X X X X X X X X M dialica(Dr.) Kutzing X X M wriam Agardh X X M spp. Asardh X X X X X X X X X Navicula crnvocephala Kutzing X X N. exigua (Gregory) O. Muller X N. exigua v. eqpitata Patrick X ,
N. subtilissima Cleve X N. app. Bory X X X X X X Nitachia acicularis W. Smith X X X X X X N. agelta Hustedt X X X X X X X X X N. Hsarica Hustedt X X X X X X N. pelea (Kutzing) W. Smith X X X X X b
3-20 q -p ,-w- -yar.
i Table 3 6 (continued) page 6 of 9 TAXON 87 88 89 90 91 92 93 94 95 %
N. subitwards Hustedt X X N. spp. Itamall X X X X X X X X finnularia app. Ehrenberg X A4famolania app. Ehrenberg X X X X X X X X X X
.w/wonemapotemw(Webw) Hilu X X X X X Sap; :*: w app. Ehrenbwg X X X X X X X X X X Sywew actinastroddes imamerman X S. acus Kutring X X X X S. delicaiinsIma Lewis X X X S. plan & tonka X X X X X X X X X X S. runrem Kutzing X X X X S. rwapem v. Amrilarioides Grunow X S. rwapem v. scotka Grunow X S. wina(Ntach) Ehrenbwg X X X X X S. opp. Ehrenbwg X X X X X X X X rebellardeAnastrata (Lyngb) Kutzing X X X X X X X X X X r.foccolosa (Roth.) Kutzing X X X X CLASS: CHRYSOPHYCEAE
(-
Automanapurdytt Lacksy Calckomonar peschert (Van Ooor) Lund X X X X
X Chromslina spp. Chien. X X Chq: :;!:.:ala solitaria X X X X X X C "-- . melata Lackey X Dinoeryon 6amrkw= Imhof X X X X X X X X X X D. cylineic== Imhof X X X X X X D. Awry,m Imhof X X X X X X X D. wrenlaria Ehrenbwg X X D. opp. Ehrenbwg X X X X X X Erdinia swaasywkilliate SkMa X X X X X X X Kapiprion tw&IslaustriConrad X X K. shayse X K. app. Pasclwr X X X X X X X X Mallomonar scaroides Party X M a&ro&amos(Naumann) Kriega X M caudata conrad X X X X X X X M globosa Schiller X M rwadocorenata Pracott X X X X X X X X X M towwrote Teiling X X X X X X X X X X O
i y
s 3 . .-, . - - . , _. - - -
l Table 3 6(continued) page 7 of 9 TAXON 87 88 89 90 91 92 93 94 95 %
M app. Petty X X X X X X X X ochromonas opp. Wynot. X X X X X X Rhhochrhis app. Pacher X X stelexomonas dichotoma Lackey X X X X X X X X X Synura spinosa Korschikov X X X X X S. uvella Phrenbers X X X X X X -
S. spp. Ehrenberg X X X X X X Urof lempsh americana (Caulk.) Lemm. X X X CLASS:IIAPTOPIIYCEAE Chryrochromulinaparva Lackey X X X X X X X X X X CLASS: XANTilOPliYCEAE Characlopsis dubia Pucher X X Dichotomococcus curvata Kotschikov X Ophiocytiurus caostatum v. longispinum X X (Moebius) Lemmerman CLASS: CRYPTOPIIYCEAE Cryptomonas erma Ehrenberg X X X X X X X X X X C crasa y, reflexa Marmon X C marsonilSkWa X X X X X X C omta Ehrenberg X X X X X X X X X X C phaseolus Skuja X X X X X X C refexa SkQa X X X X X X X X X X C app. Ehrenberg X X X X X X Rhodomonas minuta SkWa X X X X X X X X X X CLASS: MYXOPIIYCEAE Agmenellum quadrkhplicatum Brebisson X X X X Anabaena catenuta (Kutring) Born. X A. whcomineme Prescott X X X X A. spp. Bory X X X X X X X X Amocystis incerta (Lemm.) Druet & Daily X X X X X X A. spp. Meneghini X Chroococcus limneticus L.emmermann X X X C minor Kutring X C turgidus (Kutz.) Lemmermann X X C app. Naseti X X X X X X X X X s
3-22
l i
i Table 3-6 (continued) page 8 of 9 j 1
- TAXON 87 8G 89 90 91 92 93 94 95 % j C
- :!:f::h= kunsdagiona Nagell X Daend=weepsk deresalas Hanagits X X X i
- c. . . :;r-c lacweris chodet X X X [ X X X W ewwwvatm am w mana X X i Lis wsontemmermana X X X X X X s
L s=6tilar X X X X X .
L ep. Asudh X X X X X X X X X X i Micrwyw4 w fr - Kutr. e end Elen. V
. X X X X X X X X l Decillands seahwa Meneshini X X X -X ?.'.
i
- o. Id= .etica temmamana X X X
- o. splomade oreville X X i
- o. app, voucher X X X X rharmisma anewtind=== west A Wat X X X X l P. spp. Kutdag X X X. X X ;
. * ; "';rir ceste Fritsch A Rich X X X X X X Ahabdadwma s; :f'r Schm. A 14utrb. X spawmeew idee (Sek. A Laut.) Kom. X X X X X X X l CLASS: EUGLENOPHYCEAE ,
KW acw Ehrenberg X K.minna Prososet X K. , 4_., ' - Denseerd X K. app. Bhrenbors X X X X X X X X lecciacdw app. Party X 1
Pharm erMeulards Hubner X
- r. swww(temm.) Skvartsew X X X
- r. app. D4erdin X Thechele==ine acawkmsome (Stok.) Deft. X X
- r. Adqpids(Porty) Stein X r.pulchwr*=n Playthir X t r, wtweine Ehru. bas X X X L spp. Bhanbas X X X CLASS: DINOPHYCEAE l - Cwwdna Ah=Awila(OFM) Schrank X X X X X X X adenudnia= 6 zel(temm.)Schilla X X X G. e===dal== Penard X X X X X a.pelowre (tamm.) Schilla - X G. ;rafix (seein) Schilla X X t
u V
+
l 3-23 !
2 A -
Table 3-6 (continued) page 9 of 9 TAXON 87 88 89 90 91 92 93 94 95 96 G. spp. (Ehrenberg) Stein X X C,=: *- ' r app,(Stein) Kofold A X X X X X X Swory PeridisJust ocwwl$rerw= Locamermann X
- r. h,r-- L*=namann X X X X X X X X X X-
- p. pwitin= (tenard) Lemmamann X X X X X X X X X X
- r. m 6ensr== stein X X X
- r. wisconstwnee Eddy X X X X X X X X X
- r. app. Ehrenbas X X X- X X X CLASS: CHLOROMONADOPHYCEAE c=,x:es== J.c. ::= Lausaterne X X 0, semen (Ehrenberg) Diesing X G. app. Diesias X X X X t
l l
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1 1
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- w. .......... .. ....... ... 4m. .................. ....
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************* ' ^**** ~~
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n o q m o o e o e e e
-+- -a- -o- -x-Figure 3 1. Phytoplankton chlorophyll a, densities, ad biovolumes; and seston weights at locations in Lake Norman, NC, in February, May, August, and Noveraber 1996.
6
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FEB MAY AUG NOV MONTH
~
+TM7 1988 + 1989 + 1990 1991
, 1992 1993 + 1994 1996 o 1996 Figure 3 2. Phytoplankton chlorophyll a annual lake means from all !ocations in Lake Nonnan, NC, for each quarter since August 1987. .
a 3 26
% N E MI)
FammuARY MAY
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10 . ...................... 10 . .......... . .........
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50 -...... ....... ........ w. .......... .... ..
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- n. .... .............a a. ..... .. ...... .......
0 . 0
.7 mw .0 ei a a w n a er n m .0 ei n es a w a m ne m ne Figure 3 3. Phytoplankton chlorophyll a concentrations by location for samples collected in Lake Norman, NC, from August 1987 through November 1996.
n i
h, 3 27
me onomtie We4 AUGUST Novmeest 10 j 0 .e t0]
[ 10]
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$$ 0.a $1% j Sie e 110l
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0 0 ;w er se se so m se W m e5 es er se se to M se se a es se rum vous Figure 3-3 (continued).
\.
3 28
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l.
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l msine soauw ,M
. . . . _ - , - i n n . u. --- - --- - _ _ - --, im u.u
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em - - - -
se t I
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m, . . . . , . . . . . - . _ .. .. g, . _ .,,. . . _ . , , .
.g . . . , . . . . . . . . . . . . . . . . . .
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j g, . . _ . . . . . . . . - . . . . . .<
i
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FEB MAY hfue(De 40 'KW FEB WY Isnome AUG PsN i
CMORGHr2AE OfM5GHr3AE M 371PfGHfCEAE 4 vrowaAE uu maa B,AGLAWIW7CEAt mm j Figure 3-4. Class composition of phytoplankton from cuphotic zone samples collected at
- locations in Lake Norman, NC, during 1996.
(1 v
L i
3-29 .
i e
4
--. __ .. - .~ ..~ ..- ,-__- _ . .- _ . -. _ _ . _ _.._ .. ....~... . ..
i i . . .
i l
1 1
i \
l j 1.8 4
1.7 :
l l I
i 1.6 ._- l
' 1 1.5 i l _
I l l 1A. .-
l '
j 1.3 l h1.2 p ._
j g HGH INTERhEDIATE LOW 1,1 _
l l 1.0 - - -
l 0.9 _ _ _
y_
l 0.8 ,
l 0.7 -. - - - _ __._ y_ -
i na .
_,_ _r _g _ _t_ ., .4_ _,_ _,_ . _
1988 1989 1990 1991 1982 1983 1E04 1995 1996 YEARS Figure 3-5. Annual lakewide Myxophycean index results for Lake Norman, NC, for 1988
! through 1996.
i l
l l
i l 3 30 t
4
.________-__,-__r_ - -
. . _ . _ _ - - , - . - _ _...,-._...._,-..-_-,.-.~,,w,..---...-._,-,m,._,
CHAPTER 4 ZOOPLANKTON INTRODUCTION The objectives of the Lake Norman Maintenance Monitoring Program for zooplankton are to:
- 1) Der.cribe and characterize quarterly pattems of zcoplankton standing crops at selected locations on take Norman; and
- 2) compare and evaluate zooplankton data collected during this study (February, May, August, and November 1996) with historical data collected during the period 1987-1995.
Previous studies of Lake Norman zooplankton populations have demonstrated a bimodal casal distribution with highest values generally occurring in the spring, and a less pronounced fall peak. Considerable spatial and year-to-year variability has been observed in zooplankton abundance in Lake Norman (Duke power Company 1976,1985; llamme 1982; Menhinick and Jensen 1974).
METilODS AND MATERIALS Duplicate 10 m to surface and bottom to surface net tows were taken at Locations 2.0, 5.0, 9.5,11.0, and 15.9 in Lake Norman (Chapter 1, Figure 2-1) on February 7, May 23, August 22, and November 13,1996. For discussion purposes the 10 m to surface tow samples are called coilimnetic samples and the bottom to surface net tow samples are called shgic splumn samphs. Locations 2.0 and 5.0 are defm' ed as the Mixing Zone and Locations 9.5, d 4-1
t i
11.0 and 15.9 are defined as Background LMw. Field and laboratory methods for ;
E--;' " = 2= '; crop analysis were the same as those reported in Hamme (1982).
Zooplankton standing crop data from 19% were compared with corresponding data from j quarterly monitoring begun in August 1987. j i i
) A one way ANOVA was perfonned on spilimactic total zooplankton densities by quarter. l This was followed by a Duncan's Multiple Range Test to determine which location means 4 were significantly differeut. !
l RESULTS AND DISCUSSION i
I Total Abundance .
. (
- During 1996, total mooplankton densities in epilimnetic samples were highest in February, except at Location 15.9, where the annual maximum occuned in May (Table 4-1, Figure 4-1). Epilimnetic densities ranged from a low of 20,900/m3 at Location 2.0 in November to a ;
high of 217,400/m3 at Location 11.0 in February. In the whole column samples, maxima !
l also occurred in February, except at Iamdous 5.0 and 15.9, where annual maxima were
, observed in November. Whole column densities ranged from 23,100/m3 at Location 9.5 in '
l August to 179,800/m3 at Location i1.0 in February. 'Ihis represented a seasonal shift from l 1995 when peaks were most often observed in May (Duke Power Company 1996). Hamme ,
l (1982) reported that spring peaks among zooplankton att typical. Theitfore,1996 data represent a variation from long term trends. Higher than normal February values may have :
been a response to elevated phytoplankton concentrations observed in the Mixing Zone and oertain Background Locations during February (Chapter 3).
i s
4-2 :
t' u_ _ _ . _ . . _ _ . _ _ _ , _ . . . . , _ , _ , - __w._ ,_._,_a,..__,,....__.. _
Total mooplankton densities were generally greater in epilimnetic samples thari in whole I
column samples in 1996, as has been the case in previous yews (Duke Power Company 195.,1991,1992,1993a,1994,1995a, and 1996). This is related to the ability of zooplankton to orient vertically in the water column in response to physical and chemical gradients and the distribution of food sources, primarily phytoplankton, which are generally most abundant in the euphotic zone (Hutchinson 1967). During November, the period of ,
lake turnover, spilimnotic samples had fewer zooplankton than whole column samples at all j but Location 15.9. Again, this reflected zooplankton orientation in response to food sources ;
which are pushed deeper down the water column as a result of annual mixing in the lake.
Considerable spatial variability in epilimnetic zooplankton densities was observed during -
each sampling pericJ. In February, Location 11.0 had a significantly higher mean density than other locations, and Location 15.9, the furthest uplake had the lowest mean density (Table 4-2). For May, August, and November, Location 15.9 had the highest densities (significantly higher than all other lccations in August and November). Lakewide ,
minimums were observed at Location 5.0 in May, Location 9.5 in August, and Location 2.0 in November. '!he trend of ireressing epilimnetic mooplankton population densities from Mixing Zone to Background Locations obseryml during most of 1995 was only apparent in Novemier 1996 (Duke Power Company 1996).
Comparisons of long term trends of total epilimnetic zooplankton densities showed that much higher year-to year variability occurred among Background Locations (9.5,11.0,15.9) than smong Mixing Zone locations (2.0, 5.0); and that the highest levels of variability were f
l noet often observed at the uppermost location,15.9 (Figure _4-2). 'Ihis indicates that spilimertic mooplankton communities are more greatly influenced by environmental coexlitions at the uptake locations than at downlake locations. Locatica 15.9 represents the l
transition mone between river and reservoir where populations are expected to be highest due to higher proh :tivity of this dynamic region. At the locations nearest the dam (Locations
/
l - i, 4-3 b
. ~ , . . ~ . . . . _ _ . - _ . . . , . . . . - , . _ . - - - . , _ . . . . _ - . . _ _ , . - _ , _. m.. . - . _ - . . - _ . - - _ . _ . - _ _ . _ - . - . , -
- - - --. . - - _ . - - .- - . . . - - _ _ - - - - . - _ _ = .
2.0 and 5.0), sene mal variations are dampened and the overall production would be lower
( (Thornton, et al.1990).
in most cases, epilimnetic zooplankton densities during 1996 were within ranges of those observed daring previous years of the study. In February, long term maxima at Locations 2.0 and 11.0 occurred this year; while February maxima at Locations 5.0 and 9.5 were observed in 1995. At Location 15.9, the highest ' bruary density owurred in 1992. During May periods, Locations 2.0, 5.0, and 11.0 hat simum values in 1995; while May peaks at Locations 9.5 and 15.9 occurred in 1988. Durin, August periods, all but Location 15.9 had maximum densities in 1988; while Location 15.9 had its highest August
- alue in 1996. For November, all locations demonstrated long term maximum values in 1988. ,
Community Composition
(
Eighty-eight zooplankton taxa have been identified since the Lake Norman Maintenance Monitoring study began in August 1987 (Table 4-3). Seventeen new taxa were identified in 1996; however, eight of these had been reported from Lake Nonnan in previous studies (Hamme 1982, Duke Power Company 1985), or were observed in other Duke Power reservoirs (Duke Power Company 1993b,1995b). Nine previously unreported taxa, six cladocerans of the genus Dqphnia (D. leavis, D. longiremisi, D. pulex, D. pulicaria, D.
retrocurva, and D. schodien), and three new rotifers (Collotheca balatonica, C. mutabilis, and Colurella spp.) were identified in 1996, indicating a higher propensity for specific taxonomy on the part of the analysts.
Rotifers were the most abundant and diverse group during 1996, as has been the case in previous studies (Table 4-1. Figures 4-3 and 4-4). Copepods dominated zooplankton vO epilimnetic assemblages at Locations 2.0 and 9.5 in November. Copepods also dominated 4-4
_ - _ . ~ __ . _ _ _ _ _ _ - . _ _ _ _ _ . . _ - __.
i i
whole colonn acoplankton densities at Location 5.0 in February, Location 9.5 in August, and IM,ees 2.0 and 9.5 in November (Table 41). Cladocerans wure numerically l dominent in whole column semples at Locations 2.0 and 5.0 in August. His represents an l
increase in the overall importance of miaocrustaceans since 1995 when copopods were ;
dorninant in six samples, and cladocerans were never numerically dominant (Duke Power ,
Company 1996).
P.otifers demonstrated a spatial patter.. of increasing densities from downlake to uptake locations in all but February, as was 'he cas last year (Duke Power Company 1996). His pattern was also documented by F.am~. (1982) in earlier studies on Lake Norman. l
> Copepods also demonstrated this pattern in May and November; while cladocerans showed ;
no consistent spatial trends in 1996 (Table 4 1, Figure 4-3).
Kemtella and Polyarthm were co-dominants among ratifers at Lake Norman locations in i i
February. In May, Polyarthm dominated ratifer densities at all locations. During August, the dominance pattern was more vanable: Kellicortle-Polyarthm were chinants at Location 2.0; Polyarthm was dominent at Location 5.0; Trichocerca was the dominent at Location 9.5, and was co dorninent with Polyarthm at Location 11.0; while Conochilus was dominant at Location 15.9. Kemsella and Polyarthm were again co-dorninants during November. All of these taxa have been identified as important constituents of zooplankton communities in previous studies (Duke Power Company 1988, 1989, 1990, 1991, 1992, 1993a,1994,1995a, and 1996; Hamme 1982).
Long term tracking of ratifer populations indicated some notable seasonal patterns since 1992. Peak mean densities occurred at Mixing Zone and Background Locations in May of 1992 and 1993, and February 1994. In 1995, peak densities occurred at Mixing Zone ,
locations in February, and at Background Locations in May. Daring 1996, peak densities in V 4-5 1
,,..,-,y-,-.,.,..--,,,,y.....,,-,,,-- .--,.- y-m ,y,- w .mw,,,,,--,,,w,,3 m.,3--,m. # w +,%,,.,m, -.,,%om . , , -..------.,__m. - .-----m.---.,,----#- _-m
J both areas occurred in May, and densities declined through November (Figure 4-4). 'the highest mean ratifer density from Background locations since 1990 was observed in May i 1995; while the highest mean Mixing Zone density during this period occurred in February 1995, 1
Copepod populations were consistently dominated by immature forms (primarily nauplii, f and occasionally cyclopoid copepodites) during 1996, as has always been the case. !
Tropocyclopr, Marocyclops, and Cyclope were often important constituents of adult {
populations, but adult copepods seldom comprised more than 5% of the total zooplankton density at any location throughout 1996. Seasond trends of copepod densities were similar to those of 1095, with annual peaks generally occurring in May and minimum values in :
August (Figure 4-4).
Bormina was the most abundant cladoewan observed in 1996 samples, as has been the case in most previous studies (Duke Power Company 1996, Hamme 1982). Bormina ofte :
comprisad greater than 5% of the total zooplankton densities in both epilimactic and whole
~
column samples. Diaphanosoma and Borminopsis were also important among cladocerans.
Diaphanaroma dominated cladoceren populations at all locations in May, and Borminopsis was the dominan: cladoceren at Locations 2.0,5.0, and 9.5 in August. In the Mixing Zone, Borminopsis actually dominated whole column zooplankton densities in August. Seasonal t trends of cladoceran densities were variable: from 1990 to 1993, peak densities occurred in February; while in 1994 and 1995, maxima were recorded in May (Duke Power Company 1996). During 1996, peak cladoceran densities occurred in May in the Mixing Zone, and in August among Background locations (Figure 4-4).
4-6 l
i BRURE STUDIES
- a No changes are planned for the zooplankton portion of the Lake Norman maintenance !
monitoring program in 1997. j I i
SUMMARY
Total zooplankton standing crops were generally highest in February and lowest in August [
and Novunber. '!his represented a shift from 1995 when peaks occurred in May. Densities i were most onen highest in epilimnstic samples. Few consistent spatial patterns were observed in 1996, with the exception of November, when densities inaensed from downlake to uplake locations.
Long tonn trends showed much higher year-to year variability at uptake, or Background, l Locations than at Mixing Zone locations, indicating increasing ir.gaets on zooplankton populations from downlake to uptake locations. In most omnes, spilimestic zoopir.h i
densities during 1996 were within ranges of thoes observed in previous years since 1987, except that long term maximum densities for Febmary occurred in 1996 at locations 2.0 and 11.0, artd the long term maximum density for August occurred this year at Location 15.9.
t Rotifers dominated zooplankton standing crope through most of 1996, as has been the case in .
previous years. Rotifers most often peaked in Febmary and May, as has been the case since f
1990, 'the relative abundances of copepods and cl% were higher this year than in
- 1995. Copepods occasionally dominated zooplankton densities in February, August, and November 1996; while cladocerans were dominant in the Mixing Zone in August. Copepods have typically showed peak densities in May. Over the long tenn, cladoceren-densities peaked in February 19901993, May 1994-1995, and May-August 1996.
Makr rotifer taxa observed in 1996 were: Kemtella, Polyankm, &fchoema, and Kellicotia, Copepods were dominated by immature forms with adults seldom accounting for more than
{
4-7 i
f
,. - -,->..,-,v-an_-n- - -- - - . , . ,- . .,. . - - , . , - . ---..--- - -- . ,.~. .- - -----
i i
5% of mooplankton densities. Boemina was the predominant cladoceren, with Diaphanosoma i and Boeminopels occasionally dominating cladoceran populations. !
4 IJTERATURE CITED i
Duke Power Company.1976. McGuire Nuclear Station, Units 1 and 2, Environmental Report, Operating License Stage. 6th rev. Volune 2. Duke Power Company, Charlotte , NC.
i Duke Power Company.1985. MoOuire Nuclear Station,316(a) Demonstration. Duke !
! Power Company, Charlotte,NC. ;
Dake Power Company.1988. Lake Norman Maintenance monitoring program: 1981 l Summary. Duke Power Company, Charlotte, NC.
Duke Power Company.1989. Lake Non.m Maintenance monitoring program: 1988 :
Summary. Duke Power Company, Chariotte, NC.
Duke Power Company.1990. Lake Nonnan Maintenance monitoring program: 1989 Summary. Duke Power Company, Charlotts, NC.
ll Duke Power Company,1991. Lake Norman Maintenance monitoring program: 1990 !
Summary. Duke Power Company, Charlotte, NC.
i Duke Power Company.1992. Lake Norman Maintenance monitoring program: 1991
> Summary. Duke Power Company, Charlotte, NC.
Duke Power Company.1993a. Lake Norman Maintenance monitoring program: 1992 Summary. Duke Power Company, Charlotte, NC. :
i' Duke Power Company.1993b. Catawba Nuclear Station Supplemental 316(a)
Demonstration Data. Duke Power Company, Charlotte, NC. ,
Duke Power Company.1994. Lake Norman Maintenance monitoring program: 1993 ,
Summary. Duke Power Company, Charlotte, NC.
Duke Poww Compmy.1995a. Lake Nonnan Maintenance monitoring program: 1994 Summary. Duke Power Company, Charlotte, NC.
Duke Power Company.1995b. Ocone'e Nuclear Stati.m 316(a) Demonstration Repost.
Duke Power Company, Charlotte, NC.
4-8 i
7_,
Duke Power Company.1996. Lake Nonnan Maintenance monitoring program: 1995 Swanary. Duke Power Company, Charlotte, NC. ,
Hamme, R. E.1982. Zooplankton, h J. E. Hogan and W. D. Adair (eds.). Lake Norman Summary Technical Report DUKEPWR/82-02. p. 323 353, Duke Power Company, Charlotte, NC. 460 p.
Hechia aa4 0. E.1967. A Treatise on Limnology. Vol. II. Introduction to Lake Biology and the Limnoplankton. John Wiley and Sons, Inc. N. Y. Ii15 pp.
Menhinick, E. F. and L. D. Jensen.1974. Plankton populations. k L. D. Jensen (ed.).
Environmental raponses to thennal discharges from Marshall Steam Station, Lake Norman, North Carolina. Electric Power Research Institute, Cooling Water Discharge Research Project (RP-49) Report No.11., p.120138, Johns Hopkins University, Baltimore, MD 235 p.
'thornton, K. W., 3. L. Kimmel, F. E. Payne.1990. Reservoir Limnology. John Wi!ay and t Sons, Inc. New York, NY.
?
k .
4 4
M 4-9 m
w-,-.,, ,...,,-,,.-..,yr .+.m-.,w- e,,-.mw-.-.....,- ,~w...m.v.,,.- .y.my.. ,.--..--,,,.---,..,,,,r., -.. m,c -,.m-...,.. - . - - - .-e,-m.. . _ - - - , . - . -
1 Table 4-1. Total zooplankton densities (no. X 1000/m3), densities of major plankton j p taxonomic groups, and percent composition (in parentheses) of major taxa in 10m to surface (10 S) and bottom to surface (B-S) net tow samples collected from Lake Norman in :
February, May, August, and November 1996. l Sample Locations Delf . Tat Inun 1.0 10 El ILQ 112 2/7/96 10 S COPEPODA 19.2 8.4 33.9 37.3 4.2 :
(13.4) (9.6) (28.6) (17.1) (5.8)
CLADOCERA 12.1 6.9 18.6 34.0 0.5 ;
(BA) (7.9) (15.7) (15.7) (0.7)
ROTIFERA 112.2 71.9 66.1 146.0 68.2 (78.2) (82.5) (55.7) (672 (93.5)
TOTAL 143.5 87.2 118.6 217.4 73.0 B-S ,
depth (m) oftow COPEPODA 25.6 10.2 27.2 26.6 7.2 for each (18.4) (36.2) (25.3 (14.8) (12.3) location CLADOCERA 12.8 9.5 9.4 20.8 1.1 2.0=31 (9.2) (34.0) (8.7) (11.6) (1.9) 5.0=19 ROTIFERA 101.3 8.4 71.1 132.4 50.1 9.5-21 (72.5) (29.8) (66.0) (73.6) (85.8)
O I1.0=25 15.9-21 TOTAL 139.8 28.1 107J 179.8 58.5 5/23/96 10 S COPEPODA 16.7 17.3 17.0 30.8 51.3 4 (25.9) (32.4) (29.8) (23.5) (33.5)
CLADOCERA 10.1 9.0 14.1 34.5 36.0 (15.6) (16.8) (24.6) (26.3) (23.5)
ROTIFERA 37.9 27.1 26.1 65.8 65.8 (58.6) (50.8) (45.7) (50.2) (43.0)
TOTAL 64.7 53.3 57.3 131.1 153.1 B-S depth (m) oftow COPEPODA 13.8 13.8 10.4 13.7 26.2 far each (39.3) (30.4) (26.9) (27.6) (32.1) location CLADOCERA 4.1 8.0 10.3 18.0 18.5 2.0-30 (11.7) (17.6) (26.6) (36.2) (22.6) 5.0=18 ROTIFERA~ 17.1 23.6 18.0 18.0 36.9 9.5=20 (48.9) (52.0) (46.$) (36.3) (45.2)
I1.0=25 15.9=19 TOTAL 35.0 45.3 38.8 49.7 81.6 l
A t V 4-10 l
a ., ,= . - - ,.
Table 4-1. (continued).
ON Sample Locations DAlf LPs IEQD 28 19 fl IL.0 312 8/22/96 10.S COPF.PODA 7.9 12.3 13.0 10.5 20.5 (14.6) (30.0) (35.2) (23.2) (16.0)
CLADOCERA 23.0 13.1 9.6 6.6 8.2 (42.4) (31.9) (26.1) (14.6) (6.4)
ROTIFERA 23.4 15.7 14.3 28.1 99.5 (43.0) (38.1) (38.7) (62.2) (77.6)
TOTAL 54.3 41.1 36.8 45.2 128.2 B.S depth (m) oftow COPEPODA 7.5 8.6 8.9 5.6 17.8 for encl. (29.9) (32.6) (38.7) (22.8) (19.9) location CLADOCERA 10.8 9.4 8.2 4.7 8.8 2.0-30 (43.2) (35.3) (35.4) (19.3) (9.9) 5.0=18 ROTIFERA 6.7 8.5 6.0 14.1 62.6 9.5=20 (26.9) (32.0) (25.9) (57.9) (70.2) i1.0-25 15.9=19 TOTAL 25.0 26.5 23.1 24.4 89.2 11/13/96 10.S COPEPODA 10.3 9.6 19.1 26.3 41.6 (49.2) (39.4) (48.8) (43.8) (35.2)
CLADOCERA l.8 0.7 3.4 5.0 4.5 (8.6) (2.8) (8.8) (8.4) (3.4)
ROTIFERA 8.8 14.0 16.6 28.8 7.2 (42.3) (57.8) (42.4) (47.9) (61.0)
TOTAL 20.9 24.3 39.1 60.1 118.4 B-S depth (m) oftow COPEPODA 17.7 19.4 25.7 30.4 25.0 for each (48.9) (33.2) (46.4) (34.6) (28.0) location CIADOCERA 4.5 1.0 4.2 8.6 2.5 2.0=30 (12.4) (1.7) (7.5) (9.8) (2.8) 5.0=18 ROTIFERA 14.0 37.9 25.6 48.7 61.9 9.5=19 (38.7) (65.0) (46.1) (55.6) (69.3)
I1.0=25 15.9=20 TOTAL 36.2 58.3 55.4 87.7 89.4 0 4-11
Table 4-2. Duncan's Multiple Range Test on epilimnetic zooplankton densities (no. X 1000/m3) in Lake Nonnan, NC during 1996.
Febru:.ry Location 15.9 5.0 9.5 2.0 11.0 Mean 73.0 87.2 118 6 143..' 217.4 May Location 5.0 9.5 2.0 11.0 15.9 Mean 51.3 57.3 0 .7 131.1 153.1 ,
August Location 9.5 5.0 11.0 2.0 15.9 Mean 36.9 41.1 45.2 54.3 128.2
' 15.9 y/ November Location 2.0 5.0 9.5 11.0 Mean 20.9 24.3 39.1 60.1 118.4 i
4-12
Table 4-3. Zooplankton taxa identified from samples collected quarterly on Lake Norman j from August 1987 through November 1996 (* indicates new taxa observed in 1996).
COPEPODA ROTIFERA Cylops thomasi Forbes Anuropsis spp. Lauterborne
- C vernalis Fischer Asplanchna spp. Gosse ,
C spp. Brachionus caydata Battois and Dadsy Dipptomus birget Marsh B. hawivoensis Rousselet D. mississippiensis Marsh B. patulus O. F. Muller D.pallide Herick B spp.Pallas D. app. Marsh Chromogaster app. Lauterborne Episkurafluviatists Herrick *Collotheca balatonica Harring
- Ergasilus spp. *C mutabilis (Hudson)
Mesocyclops edax (S. A. Forbes) C spp. Harring M. app. Sars *Colurella spp. Bory de St. Vincent Depocyclopsprasinus (Fincher) Conochiloides app. Klava T. app. Conochilus unicornis (Rousselet)
Calanoid copepodites C spp. Hlava Cyclopold copepodites Gastropus spp. Imhof Harpacticoides Nexarthra spp. Schmada Nauptli Kellicotia hostoniensis (Rousselet)
K. spp. Rousselet CLADOCERA Keratella spp. Bory de St. Vincent
- Alona spp.Baird Lecane app.Nitzsch
?armina longirostris (O. F. Muller) Macrochaetus spp. Perty O B. spp. Baird Bosminopsis dieserst Richard Monastyla stenroosi(Meissener)
M. app. Ehrenberg Ceriodaphnia spp. Dana *Notiiloca app. Gosse Chydorus spp. Leach Ploeosona hudsoniiBrauer Daphnia ambigua Scoutfield P. truncatum (Levander)
- D. catawbn Coker P. spp. Herrick
- D. galeata Sars Polyarthra eurypte a(Weitzeijski)
- D. laevin Birge P. vulga-is Carlin
- D. longiremist Sars P. spp. Ehrenberg D. lumholzi Sars
- Pompholyx spp. Gosse D. parvula Fordyce Ptygure spp.
- D. pulex (de Geer) Synchaeta spp. FArenberg
- D.pulicaria Sars &ichocerca eqpucina(Weireijski)
- D. retrocurva Forbes T. cylindrica (Imhof)
- D. schodleri Sars T. porcellus (Gosse)
D. spr.. Mullen T. similis Lamark Ddqphanosoma spp. Fischer T. spp. Lamark Holopedium amazonicum Stingelin Wichorria spp. Bory de St. Vincent R. spp. Stingelin Unidentified Bdelbides Leptodora kindtil(Focke)
Leydigia spp. Freyberg flyveryptus sordidus (LievetQ INSECTA
- 1. spp. Sars Chaoborus spp. Lichtenstein Sida crystallina O. F. Muller b
U 4-13
t i
\ tom To SURFACE TOWS 250 1
3 o. ............................... .. .........
.......... ............... ............ .. i 1 m.
4 ,
L M
g too . ........
soil _....:. - .. ........... , .. d. .........
0 2.0 80 9.8 11.0 il 9 BOTTOM TO SURFACE TOWS ano i N
no............................... .................
3oo . ...............................................
iscL............................. ...... ........
M i
- m. .... ................. ....... ...........
so ...... a../........ ....... _ .. ......
i'r Y -
- h. .
0 2.o 60 9.5 11.0 16 9 LOCAT10004
{ + FEB -e MAY e AUG +NOV l Figure 4-1. Total zooplankton density by location for samples col;ected in Lake Norman, NC in 19%.
4-14 l
l l
l l
O FR8RUARY w.mo rone m
IAAY ,
a 18458]
= ........................ ==. .......................
m ......................... ==-. . . . . . . . . . . . . . . . . . . . . . . . .
M M g m. .. .... ................. , gm . . . . . . . . . . . . . . . . . . . . . . . . .
l m. ....... ........ ... ..
lm _.............. . .... .
n ..... .. . ..... .. .. .... . ....:.......... >
or a m ei = = = = =
n m a m ei = = = = =
3 BACM00UND LOCATIONS soo
[e7. I~MI4.e IIIj 427,000 ma. .-. .......-...-----. .-
m ........................
1
= .......... ............. no . .. ............... . .
\ M M .............. .... ,
gm ..... . ... ..... . . . . g m. ... u e '
- . . . . . . . . .. ... . .. m. -... ....... . .. .. .
l m. ,
. ..... ... ... . .. . m. _.... ..................
3 Of a = to 01 et = N = = 87 m $$ to t1 ed = = = te m ae Figure 4-2 Total zooplankton density by location for epilimnetic samples collected in Lake Nonnan, NC in 1996, s
(
4-15 1
- - - - - - - - - - _ _ _ _ _ _ __. ---._--u___- -
l t
us)meaOME AUGUST NOMBSER
= m :' ';
l--e 10.e.ILOl no ......................... mo..........................
- m. ......................... m..........................
M M gm .........................
ga ................ ........
m, . ..................... m.-........................
I so _ ... .......... ......
eo< ... ... ............ ..
l
- y I O 0 m se se so m a e a es no ea e so e eam a se aAacOUNDLOOATIONS
= m
[~+-'~h -e.,R67 tO]
no - . . . . . . . . . . . . . . . . . . . . . . . . . no -. ....-............-...
m... . . . . . . . . . . . . . . . . . . . . . . m. .......................
M M g m... ......................
g m.
c 6 e A g m. .. .. . . . . . . . . . . . . . . .
g m, . .... . . . . .. .- .
d l I
so,.. . .. ...... ... . so ...... . .... . .. ...
l ,
0 o a es e ao m a ea es a a se a so e ae a es a m an wm Figure 4 2. (continued).
4 16
. - . - . . _ _ . - . - . . _ . _ _ . . . . - _ _ . . . . . _ . . _ . . . . - . . . . . . ~ . . . . . . . _ . . . . _ - . . . - ~ ..
E
- o _
14 .
20, 5
i 190 10 E0 AS 11 0 15 0 10 EO 65 11 0 15 9 i
l _ _
lo i
A l
Ieo ..
4 i
~
10
&O SS 11.0 15 9 t.oCATIONS RR10 80 SS 11 0 15 0 RODFERS l lCOPEPOOS MCLADOCERANS 4
Figure 4-3. Zooplankton composition by month for epilimnetic samples collected in Lake Norman, NC, in 1996.
O 4-17
t I
, COPEPODS 70 .................................... .....................
to .-.................................. .......................
60 -................................. . ..............__....
40 ......... .................... . . ...... ............
H. . ....4, .... .. ..... ...... .. .. . . .. . .. ,
to . 4. .. .. .. . . . .. ... ... .... ... .. . ...... .
10 P...
1 0
CLADOCERANS l utKneorows e sAcKomouh LecATKHes j 30 -.............................................. .............
35 .............................................. ....... ....
I, 30 1 5 ............................................ . . ... .. ...
1,. . -....._................... ................. . .... ... ..
110 <
% g. . .... .. . .... . . .. ... . __.. .. ... .........
i 9
0
,, ROTIFERS 120 .-............................................ ............
100 . _ . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .............
00 .-......................................_.... .. ... . ...
00 , _........................ .. ............... .. . . . ....
I 40 . ................. ..... .. .. ....... ._ . . ... .... i 20 . -_.. ..... . .. . .. . ...... . . .. ..... ....... .
O 1111111111111111111111111111 Figure 4-4. Zooplan'. con composition by moath for epilimnctic samples collected in Lake Norman, NC, in 1996.
C
\s 4-18
CHAPTER 5 FISHERIES INTRODUCrlON In accordance with the NPDF,S permit fo McGuire Nuclear Station (MNS), monitoring of specific fish population parameters for Lake Norman continued during :' %. The objectives of the fish monitoring program were to: .
- 1) Continue striped bass mortality monitoring throughout the summer.
- 2) Continue a cooperative striped bass condition study with NCWRC to evaluate stocking rates and to determine the feasibility of stocking hybrid striped bass-white bass in Lake Norman.
- 3) Analyze and summarize the 1994-95 Lake Norman creel data acd prepare a report on fish distribution, angler harvest, pressure, and success.
I hgTHODS AND MATERIALS The MNS mixing zone was monitored for striped bass mortalities from July 15 through September 1. Weekly surveys were conducted specifically to locate dead or dying striped bass.
Summer pre-stress and winter post stress gillnetting samples for striped bass were conducted during June and Noveaber, respectively, for condition factor determ' m ation as part of the cooperative study with NCWRC. Three suspended gill nets (each 250 feet long x 25 feet deep) were fished for three days during June and one day during November. The number of days that gill .iets were fished was dependent upon catching a sufficient number and size range of fish for analysis. A target catch of about 75 fish was established, however, a good, variable size distribution was the primary detenninant of a sufficient sample. Collected vriped bass were weighed (g) and measured for total length (mm).
The summary report for the Lake Norman creel survey conducted from March 1994 through February 1995 was completed. The delay in preparation of the report was due to problems
(
\
encounten:d with the way the cree! program handled catch and release data. The problems 5-1
, were corrected, and the 1994-95 Lake Norman Creel Report will be forwarded for agency L review. ;
RESULTS AND DISCUSSION Monitoring of the McGuire Nuclear Station mixing zone for striped bass mortalities during the summer of 1996, yielded no mortalities. These results are consistent with the 1994 and 1995 studies, which also yielded no mortalities.
Gill netting for striped bass during 1996 yielded variable estches for summer and fall ,
sampling. _ Summer gill netting yielded 69 fish ranging in length from 313 mm to 720 mm, and fall sampling yielded 95 fish ranging in length from 354 mm to 667 mm. All striped bass length and weight data collected in the study for condition factor determination were reported to the NCWRC, for their analysis.
FUTURE FISH STUDIES -
The following studies were requested by the NCWRC for 1997 and 1998:
(1) Continue striped bass mortality monitoring throughout the summer, (2) Continue a cooperative striped bass condition factor study with NCWRC to evaluate stocking rates and to determine the feasibility of stocking hybrid striped bass-white bass in Lake Norman, (3) Continue crappie trapanting study on Lake Norman (implemented in 1997), and (4) Continue spring electrofishing program on a 3-year basis after 1997 sample (next sample i to be conducted in 2000) 5-2
. - _ - -