ML20080G499
| ML20080G499 | |
| Person / Time | |
|---|---|
| Site: | Crystal River  |
| Issue date: | 08/31/1983 |
| From: | APPLIED BIOLOGY, INC. |
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| NUDOCS 8309200298 | |
| Download: ML20080G499 (113) | |
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POST-0PERATIONAL ECOLOGICAL MONITORING PROGRAM CRYSTAL RIVER UNITS 1, 2 AND 3 1977 - 1981
SUMMARY
REPORT ' BENTHIC COMMUNITY STRUCTURE STUDIES 8309200298 830914 PDR ADOCK 05000302 PM R
AB-509 POST-0PERATIONAL ECOLOGICAL MONITORING PROGRAM CRYSTAL RIVER UNITS 1, 2 AND 3 1977 - 1981
SUMMARY
REPORT BENTHIC COMMUNITY STRUCTURE STUDIES l l Prepared for FLORIDA POWER CORPORATION St. Petersburg, Florida l AUGUST 1983 7 l- ! Prepared by APPLIED BIOLOGY, INC. Decatur, Georgia
CONTENTS Page LIST OF TABLES --------------------------------------------------- iii LiSi 0F FIGURES -------------------------------------------------- iV EXECUTIVE
SUMMARY
------------------------------------------------ Viii INTRODUCTION ----------------------------------------------------- 1 PLANT HISTORY ---------------------------------------------------- 2 OBJECTIVES ------------------------------------------------------- 5 METHODS ---------------------------------------------------------- 6 RESULTS AND DISCUSS 10N ------------------------------------------- 8 P hy s i c al E n v i ro nme nt ---------------------------------------- 8 Macrophytes ------------------------------------------------- 14 Benthic Macroinvertebrates ---------------------------------- 20 Benthic Core Program ---------------------------------------- 21 Suction Dredge Program -------------------------------------- 26 Oys ter Ree f Comun i ti e s ------------------------------------- 28 Salt Marshes ------------------------------------------------ 32 Marsh Grasses ----------------------------------------------- 33 Marsh Macroinvertebrates ------------------------------------ 37 LITERATURE CITED ------------------------------------------------- 39 FIGURES ---------------------------------------------------------- 46 TABLE ------------------------------------------------------------ 89 l
1i _-____ \
LIST OF TABLES Table Page 1 Operational Capacities of Crystal River Units 89 1, 2 and 3, C rystal Ri ve r Power Pl ant ----------------- 2 Studies Conducted in the Vicinity of the C rystal R i ve r Powe r Pl a nt ----------------------------- 90 3 Summary of Benthic Sampling Program Conducted at Crystal River Power Plant, 1977-1981 -----------------. 95 4 Average Monthly FPC Discharge (AD) and Intake (AI) Canal Temperatures, Mean Monthly Temperature Differentials (at) and Percentage of Days Each Month that Unit 3 was operating (P0), Crystal River Power Plant, 1977-1981 ------------------ 97 5 Polychaete Taxa Collected in at least 90 Percent of the Samples Taken Each Year in Discharge (D) and Control (C) Basins, Crystal River Power Plant,1981 --- 98 6 One-Way ANOVA Applied to Quarterly Macroinvertebrate Densities at Seven Discharge (1-7) and One Control Station (S), Crystal River Power Plant,1981 ---------- 99 7 One-Way ANOVA Applied to Total Number of Macroinvertebrate Taxa Collected at Seven Discharge (1-7) and One Control Station (8), C ry stal Ri ve r Powe r Pl ant , 19 81 ----------------------- 101 8 Dominant Mollusc Species Associated with Crassostrea virginica Reefs of Discharge and I Control Zones, Crystal River Power Plant, 1977-1981 --- 103 1 l I I l l iii'
LIST OF FIGURES Figure Page ;
.1 1 Location of the Crystal River Power Plant -------------- 46 2 C ry st al R i ve r S tu dy A rea ------------------------------- 47 3 Location of the 12 permanent stations used for collecting benthic core, sediment core, suction dredge and macrophyte biomass samples and taking physical measurements, Crystal River Power Plant, 1977-1981 --------------------------------------------- 48 4 Transects used for monitoring benthic macrophytes, Crystal River Power Plant, 1977-1981 ------------------ 49 5 Location of permanent stations used for examining oyster reef communities and salt marsh vegetation, Crystal River Power Plant, 1977-1981 ------------------ 50 6 Mean monthly water temperature of discharge and intake canals, Crystal River Power Plant, 1977-1981 --- 51 7 Quarterly mean salinities of discharge and control basins, Crystal River Power Plant, 1977-1981 ---------- 52 8 Comparison of preoperational and postoperational data on mean gravel, sand, silt and clay fractions of sediments, Crystal River Power Plant,1974 and 1977-1981 ----------------------------------------- 53 9 Percentage contribution of seagrasses and macroalgae to total quarterly macrophyte biomass in discharge and control basins during preoperational and operational years, Crystal River Power Plant,1973 and 1977-1981 -- 54 10 Mean quarterly biomass for total macrophytes, sea-grasses and macroalgae, Crystal River Power Plant, 1973 and 1977-1981 ------------------------------------ 55 11 Mean density and mean biomass of macroinvertebrates collected by benthic cores, Crystal River Power Plant, 1977-1981 --------------------------------------------- 56 12 Total number of macroinvertebrate taxa collected by benthic core each quarter, in discharge and control basins, Crystal River Power Plant, 1977-1981 -- 57 13 Mean diversity and mean evenness of macroinvertebrates collected by benthic cores, Crystal River Power Plant, 1977-1981 --------------------------------------------- 58 iv
LIST OF FIGURES (continued) Figure Page 14 Total number of polychade species collected annually in discharge and control basins, Crystal River Power P1 ant, 1977-1981 -------------------------------------- 59 15 Results of Tukey-Kramer multiple range test applied to quarterly macroinvertebrate densities at discharge stations (1-7) and a comparable control station (8), C ry stal Ri ve r Powe r Pl ant , 1981 ----------------------- 60 16 Results of Tukey-Kramer multiple range test applied to total number of macroinvertebrate taxa collected each quarter at discharge stations (1-7) and a com-parable control station (8), Crystal River Power Plant, 1981 ------------------------------------------- 61 17 The zone of significant negative impact on discharge basin macroinvertebrate densities relative to a comparable control station, Quarter 1, Crystal River P ow e r P 1 a n t , 19 81 ------------------------------------- 62 18 The zone of significant negatiye impact on discharge basin macroinvertebrate densities relative to a comparable control station, Quarter 2, Crystal River Power Plant, 1981 ------------------------------------- 63 19 The zone of significant negative impact on discharge basin macroinvertebrate densities relative to a comparable control station, Quarter 3, Crystal River P owe r P 1 a n t , 19 81 ------------------------------------- 64 20 The zona of significant negative impact on discharge basin macroinvertebrate densities relative to a comparable control station Quarter 4, Crystal River Power P1 ant, 19dl ------------------------------------- 65 21 The zone of significant negative impact on total number of discharge basin macroinvertebrate taxa relative to a conparable control station, Quarter 1, C ry st al R i ve r Powe r P l ant , 1981 ----------------------- 66 22 The zone of significant negative impact on total number of discharge basin macroinvertebrate taxa relative to a comparable control station, Quarter 2, C rystal Ri ver Power Pl ant , 1981 -------------------- 67 y
LIST OF FIGURES (continued) Figure Page 23 The zone of significant negat'ive impact on total ! number of discharge basin macroinvertebrate taxa relative to a comparable control station, Quarter 3, Crystal R i ver Power Pl ant , 1981 --------------------- 68 24 The zone of significant negative impact on total number of discharge basin macroinvertebrate taxa relative to a comparable control station, Quarter . A, C rys tal Ri ve r Power Pl a nt , 1981 --------------------- 69 l 25 Density and biomass of benthic fauna collected by suction dredge, Crystal River Power Plant, 1977-1981 ---------------------------------------------- 70 26 Diversity and evenness of benthic fauna collected by suction dredge, Crystal River Power Plant, 1977-1981 ---------------------------------------------- 71 27 Quarterly mean abundance and mean biomass for adult oysters from oyster reef stations in the control and discharge zones, Crystal River Power Plant,1973 and 1977-1981 ---------------------------------------------- 72 28 Quarterly mean abundance and mean biomass for spat from oyster reef stations in the control and discharge zones, Crystal River Power Plant,1973 and 1977-1981 --- 73 29 Mean dry weight of adult oysters for control and discharge zones, Crystal River Power Plant,1973 and 1977-1981 ---------------------------------------------- 74 30 Mean number of adult oysters collected quarterly at each station, Crystal River Power Plant,1981 ---------- 75 31 Number of mollusc taxa collected from oyster reefs in discharge and control zones, Crystal River Power Plant, 1977-1981 ---------------------------------------------- 76 32 Mean number of macroinvertebrate taxa collected quarterly at each oyster reef station, Crystal River P owe r P 1 a n t , 19 81 -------------------------------------- 77 33 Mean number /m2 of macroinvertebrates collected quarterly at each oyster reef station, Crystal River P ow e r P l a n t , 19 81 -------------------------------------- 78 34 Mean density of live Spartina stems during 1973 preoperational and 1977-1981 operational monitoring, C rys tal Ri ve r Powe r P l a nt ------------------------------ 79 vi
r I 1 l LIST OF FIGURES (continued) ; Figure Page 35 , Mean stem length of Spartina during 1973 preoper-ational and 1977-1981 operational monitoring, C ry s t s ) R i ve r P owe r P l a nt ------------------------------ 80 36 Mean biomass of live Spartina during 1973 preoperational and 1977-1981 operational monitoring, Crystal River P ow e r P l a n t -- -------- -- -- --- ----- ------ -- --- ---- - --- - -- 81 37 Mean density of live Juncus stems during 1973 pre-operational and 1977-1981 operational monitoring, C ry st al R i ve r Powe r Pl ant --------------------------.... 82 38 Mean stem length of Juncus during 1977-1981 operational monitoring, Crystal Ri ver Power Plant ------------------ 83 39 Mean biomass of live Juncus during 1973 preoperational and 1977-1981 operational monitoring, Crystal River P ow e r P 1 a n t -- --------- -- - --- - -- -- ---- -- ----------- -- --- 84 40 Mean density of periwinkles in Spartina marshes during 1973 oreoperational and 1977-1981 operational monitor- > i ng , C ry st al R i ve r Powe r P l a nt -------------............ 85 41 Mean density of periwinkles in Juncus marshes during 1977-1981 operational monitoring, Crystal River Power Plant -------------------------------------------------- 86 42 Mean density of fiddler crab burrows in Spartina marshes during 1973 preoperational and 1977-1981 operational monitoring, Crystal River Power Plant ------ 87 l 43 Mean density of fiddler crab burrows in Juncus marshes during 1977-1981 operational monitoring, C ry s t al R i ve r Powe r P l a nt ---------------------------... 88 vii
EXECUTIVE
SUMMARY
From 1977 through 1981, the nearshore marine environment adjacent to Florida Power Corporation's Crystal River Power Plant was monitored to assess the effects of once-through cooling water discharge on resident benthic communities. This program was conducted pursuant to Nuclear Regulatory Commission operating license DPR-72. Both combined and incre-mental effects of one nuclear (Unit 3) and two fossil-fueled units (Units 1 and 2) were examined. Effects of plant operation were inferred from comparisons of community structure between benthos inhabiting a shallow receiving basin immediately adjacent to the plant site (nearshore discharge basin) and those of a similar area unaffected by plant effluents (nearshore control basin). Plant operation measurably elevated water temperatures and salini-ties and decreased dissolved oxygen levels within the discharge basin relative to the control basin. Average monthly summer temperatures in l the intake canal never exceeded 31'C, while in the discharge canal they ranged from 32'C to 38'C. As the thermal plume exits the discharge canal and mixes with recet. lag waters, water temperatures decline. The actual temperatures impacting resident organisms varied in relation to the number of units operating and the distance of monitoring locations from the point of discharge. Sediments in the discharge basin were significantly finer and less heterogeneous than those in the control basin. This divergence of sedi-CRYRIVI EXECSUM-2 l viii a -,
ment characteristics occurred prior to the operation of Unit 3 and apparently resulted from a history of relatively high sedimentation rates in the discharge basin. The control basin represented a more complex and less stressful phy-sical environment than the discharge basin and consequently supported a greater variety and abundance of benthic plarits and animals. In the control basin, oyster shell and emergent limestone outcroppings provided ample attachment sites for a diverse assemblage of macroalgae, while unconsolidated sediments supported a heterogeneous mixture of seagrasses. By contrast, macroalgae which was present in the discharge basin during preoperationai studies, was essentially absent during operational years. Instead, discharge basin macrophytes consisted of a nearly pure stand of the seagrass Halodule wrightii. Biomass of Halodule in the discharge basin exhibited marked temporal and spatial fluctuations in reponse to prevailing temperatures. Seagrass biomass was noticeably reduced during the summer when temperatures often exceeded thermal tolerance levels for the species. The areal extent of thermal impact was enlarged during periods when all three units were operating. Differences in macroph.yte community structure further accentuated differences in habitat complexity between basins, and as a result, den-sities, biomasses, numbers of species and diversity and evenness indices of benthic macroinvertebrates were consistently greater in the control i CRYRIVI EXECSUM-2 ix
basin than in the discharge basin. Communities in both basins experienced marked seasonal fluctuations in community parameters in f response to cyclical environmental variables. However, assemblages in l l the control basin appearad more stable over time as evidenced by relati-vely high and constant diversity and evenness values. Within the discharge basin, macroinvertebrate community parameters were particularly depressed during the summer and the magnitude of dif-ferences between basins was greater during years when all three units were operating. Although densities of macroinvertebrates generally re-covered to background levels during cooler months of the year, the operation of all three units seems to have permanently suppressed species richness. Oyster reef community parameters displayed trends similar to those observed for benthic macrophyte and macroinvertebrate assemblages. The number and biomass of adult oysters and oyster spat and the density and species richness of associated reef fauna were consistently greater at control stations than at discharge stations. Within the discharge zone, values for these parameters increased with increasing distance of the reef from the point of discharge. Community. structure of oyster reefs farthest from the point of discharge was similar to that observed on f reefs in the control zone. The combined operation of all three units did not appear to have had any greater impact on oyster reef communities than the combined operation of Units 1 and 2. CRYRIV1 EXECSUM-2 x
The structure of salt marsh communities exposed to thermal effluents was measurably different from that of control marshes. Both dominant marsh grasses, Juncus and Spartina, were shorter but more dense in the discharge marsh. However, above-ground biomass for both species was similar between basins. l l I k' k l CRYRIVI EXECSUM-2 xi
BENTHIC COMMUNITY STRUCTURE STUDY INTRODUCTION Benthic organisms play an important role in estuarine ecosystem dynami cs. They are also particularly well suited for use in assessing the local impact of environmental perturbations. Because of affinities for certain combinations of physicochemical f actors, benthic plants and animals tend to segregate into communities characteristic of prevailing environmental conditions. Once established in an area, their relatively 1+. degree of motility usually precludes escape from subsequent changes in the physical envi ronment. Consequently, alterations in comnunity structure often reflect changing water quality. Heated effluents discharged into coastal waters from electric generating stations have the potential to affect the structure and func-tion of resident biotic communities. The degree of impact is related to both the level of perturbation (i.e., the intensity, duration and areal extent of the thermal plume) and the resistance and resiliency of the communities experiencing the stress (Boesch and Rosenberg,1981). Near power plants, increased temperatures have impacted benthic comnunities through shifts in primary production, faunal density, biomass, species richness, diversity and species composition (Warinner and Brehmer,1966; Virnstein, 1972; Patrick 1974; Logan and Maurer, 1975; Blake et al., 1976; Thorhaug et al., 1978). 1
Environmental monitoring of benthic communities adjacent to Florida Power Corporation's Crystal River Power Plant was conducted from March 1977 through December 1981. These non-radiological studies were mandated by Nuclear Regulatory Commission -(NRC) Envi ronmental Technical Specifications (ETS) pursuant to the licensing and operation of Crystal River Unit 3, a nuclear-fueled power plant. Program results were pre-sented in a series of five annual reports (FPC,1978a,1979,1980,1981, 1982a). This document summarizes those findings. PLANT HISTORY The Crystal River Power Plant is located on the west coast of Florida approximately 112 km north of Tampa (Figure 1). During the period of ETS monitoring, it consisted of three electic units with a com-bined generating capacity of 1854 MW (Table 1). All use a once-through seawater cooling system, receivir.g and discharging their cooling water from and into the Gulf of Mexico through common intake and discharge canals (Fi gure 2). Consequently, observed responses of biotic com-munities adjacent to the plant site reflect the cumulative operational impact of all three units. A thorough description of the study area was previously presented by j Applied Biology, Inc. (FPC, 1982a). In general, the area is charac-terized by expansive stretches of salt marsh vegetation along the shore-line and by long, discontinuous oyster reefs in the shallow, nearshore waters of the Gulf of Mexico. Hydrological conditions are estuarine, 2 _ _ _ _ _ _ _ _ _ _ _ _ _ i
resulting from the mixing of saline Gulf waters with fresh water runoff from the Withlacoochee and Crystal Rivers and numerous tidal creeks. A series of manmade and natural features partition the study area into relatively distinct zones (Figure 2). The discharge zone lies be-tween the spoil islands of the Cross Florida Barge Canal (CFBC) and the intake dike of the power plant. The area south of the intake dike was designated as the control zone. Emergent geological and biological structures further subdivide both zones into a number of relatively distinct basins. Major emphasis of the ETS monitoring program was placed on the innermost (nearshore) basin in each zone. Within the discharge zone, substrates consist primarily of a relati-vely homogeneous and often deep layer of fine sediments, while in the control zone, sediments consist of a heterogeneous mixture of sand, shell and mud of varying depth overlying a consolidated layer of limestone. When emergent, the limestone provides a hard substrate for benthic orga-nisms. Water depths in both zones are typically less than three meters. Hydrological parameters differ appreciably between discharge and control zones. Temperatures in the discharge zone are higher than those in the control zone and vary in relation to the operating capacity of each unit, tidal stage and distance from the point of plant discharge. Discharge salinities are also higher than those in the control zone due to the channeling of higher salircity offshore waters through the plant 3
canal system. Sedimentation rates, and consequently turbidities, are similarly higher in the discharge zone. The cutting and redirecting of tidal creeks adjacent to the plant site, the input of sediments from the CFBC and Withlacoochee Rivers and the periodic channeling of spoil materials from intake canal maintenance dredging have all been implicated I l as possible causes for differences in the sedimentation rates of the l discharge and control zones. Numerous environmental studies have been conducted at the Crystal River Power Plant (Table 2). Between January 1969 and July 1971, the Florida Department of Natural Resources conducted the first comprehensive study of the area in an effort to develop a monitoring plan for sub-sequent years. However, before the baseline study was completed, Units 1 and 2 were both operational. Between 1972 and 1974, numerous researchers from the Universities of Florida and South Florida conducted a variety of studies to document preoperational conditions prior to the activation of Unit 3. Unit 3 began commercial operations in 1977, and the consulting firm of Connell, Metcalf and Eddy was contracted by FPC to provide operational monitoring of resident benthic and zooplankton communities. During this period, researchers from the University of Florida continued to collect data relating to the structural and functional aspects of selected biotic com-munities (Table 2). Metabolic studies of estuarine and sa y marsh com-munities and studies of zooplankton community structure were terminated 4
after 1980. In 1981, Applied Biology, Inc. assumed monitoring respon-sibilities for all remaining study parameters. In 1982, ETS monitoring was suspended in anticipation of a more comprehensive NPDES 316(a) and (b) study. That study began in 1983. Metabolic studies of estuarine and salt marsh ecosystems and struc-tural analyses of the salt marsh community conducted as part of the ETS program were summarized by the Systems Ecology and Energy Analysis Group of the University of Florida (FPC,1982b). The present report summarizes findings of the various ETS benthic community structure programs and augments structural data previously presented for the salt marsh eco-system. OBJECTIVES Objectives of the ETS operational benthic community structure study were:
- 1. Determine the combined impact of Units 1, 2 and 3 on resident i
benthic communities (including seagrasses, macroalgae, macroin-l vertebrates and oyster reefs) of the nearshore discharge basin,
- 2. Segregate the additional impact of Unit 3 on resident benthic communities from that of Units l'and 2, and
- 3. Document any long-term alterations -in community structure of benthic systems following the activaticn of Unit 3.
The objectives of ETS operational monitoring were complict.ted by the lack of daca -from true baseline years (years when no units were operating). Additionally, considerable changes in sampling methodologies l 5
(sagling locations, collection frequencies, collecting gear and pro-cessing techniques) between preoperational and operational studies largely invalidated data comparisons between years when only Units 1 and 2 were operating and those when all three units were on-line. Operational conparisons of comnunity parameters between thermally affected and control zones were also inappropriate because the discharge and control basins used for study had already developed noticeably dif-l ferent biological and physical characteristics prior to 1977 when Unit 3 went on-line (FPC,1978a). Finally, the operation of Unit 3 from 1977 thrcugh 1981 was intermittent with only two years of relatively con-tinuous operation (1977 and 1981). Consequently, inferences regarding the potential impact of Unit 3 have largely been obtained from qualita-tive comparisons of data sets generated during years of continual and intermittent operations. METHODS Methodologies utilized during the Crystal River ETS monitoring program were approved by the NRC as part of Florida Power Corporation's nuclear operating license, DPR-72. Over the five years that ETS moni-toring was conducted, those methods applicable to the study of benthic communities remained essentially unchanged. The collections requested by FPC and the sampling gear, number of stations, replication and sampling frequency used in the various ETS program segments are provided in Table 3. 6
r Benthic community structure was examined at 7 stations in the nearshore discharge basin and 5 in the nearshore control basin (Figure 3). Unless otherwise stated, biological and/or physical conditions implied to exist within either zone are based on data collected at these 12 pirmanent locations. Temperature, salinity and dissolved oxygen (D0) measurements were taken concurrently with benthic collections. In 1980 and 1981, grain size analyses were also performed on sediments from these 12 locations. Macrophyte distribution was monitored along a series of transect lines throughout the discharge and control zones (Figure 4). At fixed-interval stations, divers noted the relative abundance of major species within randomly thrown 1.0 m2 quadrats. Oyster reef communities were examined at nine emergent reefs within the study area (Figure 5) by excavating oysters and associated fauna within 50 x 50-cm quadrats. Salt marsh community structure was studied in a thermally affected and a natural marsh habitat (Figure 5). Again, 50 x 50-cm quadrats were employed to provide estimates of above-ground biomass and stem densities. Detailed field and laboratory methodologies used in studying benthic communities, oyster reefs and salt marshes and habitat characteristics of the 12 nearshore stations can be found in the 1981 annual report (FPC, 1982a). 7
RESULTS AND DISCUSSION Physical Environment Temperature measurements taken concurrently with benthic collections revealed a trend of consistently higher water temperatures in the discharge basin than in the control basin (FPC,1982a). Hewever, because of the scarcity of measurements taken each year, mean monthly temperature data from the intake and discharge canals better illustrate annual tem-perature patterns (Figure 6; Table 4). Intake canal temperatures represent background conditions. From 1977 through 1981, mean nonthly intake canal temperatures ranged from 9.8*C to 30.9*C with the warmest readings occurring in July and August. Discharge canal temperatures measured at the point where the discharge canal empties into the nearshore discharge basin followed the same pat-tern but, during the summer, mean monthly temperatures were beetween 31.8*C and 37.9*C. There is some indication that background temperatures in the nearshore discharge basin are naturally higher than those in the nearshore control basin due to differences in water depth (FPC,1982b). However, much of the observed difference is directly related to power plant operation. The magnitude of temperature differential (At) between the two basins is positively correlated with combined power output from Units 1, 2 and 3 (FPC,1982b). Knight and Coggins (FPC,1982b) examined total monthly output for the three units from 1977 through 1980. For the 8
,a% c 9 'y---- - , , = r+-w -- i-- --
i i purpose of determining the sole impact of Unit 3, monthly output great 3r than 500,000 MHW (average monthly output of Units 1 and 2 combined) was considered attributable to Unit 3 regardless of which units were actually producing the electricity. Using this criteria, at was always less than 4 C when Unit 3 was not operating and 3 *C to 8 C when Unit 3 was generating electricity. Similar results were obtained by comparing intake and discharge canal temperatures during months in which Unit 3 was operated at least 50 percent of the time with those in which it was operated less than 50 per-cent of the time (Table 4). During the summer (June - September), discharge temperatures ranged from 33.5'C to 37.9 C when Unit 3 was operated at least half the time and between 31.8 C to 33.5'C when it did not. Thus, from 1977 through 1981, mean monthly summer discharge canal temperatures were raised an average of 3*C when Unit 3 operated at least 50 percent of the time. Obviously, heat will dissipate from plant effluents with distance f rom the point of discharge. Thus, discharge canal temperatures do not necessarily represent actual temperatures impacting discharge zone benthos. Thermal histories for individual benthic stations would be required to adequately assess the range of temperatures and the maximum temperatures affecting resident organisms. That data is not available. i 9
Comparisons of preoperational and operational data indicate that Unit 3 raises summer temperatures within the discharge basin 2*C to 3*C above those occurring when only Units 1 and 2 are operating (FPC,1982a). Communities closest to the southern boundary of the discharge basin, where a channel directs plant effluent; into the Gulf of Mexico, experience the greatest impact. During the summer, these communities are nearly always exposed to temperatures of 32 C and greater. Communities throughout the remainder of the basin gererally experience these con-ditions only when Unit 3 adds to the thermal load of Units 1 and 2. Temperatures above 32*C have been shown to be stressful to macroinver-tebrate communities in other areas of Florida (Bader and Roessler,1972; Virnstein, 1972; Thorhaug et al., 1978). Throughout the preoperational and operational monitoring programs, plant impact has been synonomous with high temperatures. Even though the discharge plume is most readily characterized by elevated water tem-peratures, it carries with it a mixture of physicochemical variables which either singularly or in interaction with other plume variables may j affect a variety of changes in community structure. Certainly, tem-l perature is the most probable causative agent for observed changes in l community structure. However, it should be recognized that other factors associated with the discharge plume may be operati ve as well. Additionally, factors unrelated to plant operation may be affecting l structural changes in assemblues within the two nearshore basins. Only l experiments designed c.o allow f actorial analyses could separate the 1 effects of these assorted physical variables. 10
Similar to temperatures, salinities measured throughout ETS moni-toring were consistently higher in the nearshore discharge basin than in the nearshore control basin (Figure 7). The intake canal, which extends 13.7 km from the plant site into the Gulf, channels higher salinity offshore water through the plant and into the discharge zone. A net southerly flow of nearshore water also brings relatively low salinity waters from the Withlacoochee River and CFBC into the discharge zone. These processes can result in a wedge of heated, higher salinity water under a layer of cooler, less saline surface water (Grimes,1971; Grimes and Mountain,1971). Dissolved oxygen (D0) levels were only reported for one year of ETS monitoring. In 1981, 00 at discharge stations was significantly lower than at control stations during all sampling periods but winter (FPC, 1982a). Annual patterns of D0 variation exhibited an inverse rela-tionship with water temperature, D0 being highest in the winter and lowest in the summer. Lowest summer D0 values observed in the control zone were 4.4 ppm, while in the discharge zone, values as low as 0.4 ppm , were recorded. Low summer D0 levels in the discharge basin may further compound the problem associated with high temperatures because thermal tolerance levels of many macroinvertebrates are reduced when D0 levels are low (Vernberg and Vernberg, 1974). The role of sediments in structuring benthic communities has been well documented (Gray, 1974). Sediment grain size analyses performed 11
during 1980 and 1981 showed that unconsolidated sediments within the study area were composed primarily of sand-sized particles (FPC,1981, 1982a). Nearshore control basin sediments exhibited significantly larger percentages of granules and very coarse, coarse and medium sands than I sediments in the nearshore discharge basin, while discharge basin sedi-ments had significantly larger percentages of fine and very fine sands. Silts and clays were not significantly different between basins and contributed relatively small percentages to total composition. Cottrell (1974) reported that sedimentation rates in the nearshore discharge basin were five times greater than in the nearshore control basin. This accounts for the significantly smaller mean grain size com-position of discharge oasin sediments (3.74 h for discharge basi.1 vs. 2.91 h for control basin). Sources of sedimentation in the discharge zone include: 1) runoff from tidal creeks, 2) dredge spoils, either deposited into the area or circulated through the plant from the intake canal, 3) erosion from the spoil islands of the CFBC, 4) erosion flow from the mouth of the CFBC, and 5) erosion flow from the mouth of the Withlacoochee River. Emergent geological and biological structures within the relatively confined discharge zone act as baffles to water flow and impede circulation. The result is reduced current velocity and higher sedimentation rates. Although overall mean grain size of sediments in the control basin I was significantly larger than in the discharge basin, the control station 12
i closest to shore (Station 8) exhibited remarkably similar grain size com-position to sediments at discharge stations. This may be explained by the greater sedimentation rates reported to occur near shore (Cottrell, 1974). The similarity of sedimentary characteristics at Station 8 and discharge stations (FPC, 1982a) permitted the only valid comparison . of biological community parameters between thermally affected and unaffected a reas. Total organic carbon content of sediments was relatively uniform throughout the study area and no spatial trends were apparent. During most seasons, differences between basins were not significant. Conversely, total carbonate contribution to sediment composition was usually significantly greater in the control basin where the larger sedi-ment size fractions were almost entirely comprised of mollusc shell fragments. Spatial variability of sediment characteristics was much greater in the control basin than in the discharge basin and was affected by a variety of factors including distance from shore, proximity to oyster reefs and water depth. Comparisons of 1973-1974 preoperational and 1980-1981 operational data also revealed slight seasonal and annual shifts in sediment composition (Figure 8). However, no long-term trends were apparent, and over the five years of operational status, Unit 3 does not appear to have appreciably altered the structure of sediments within the nearshore discharge basin. Natural temporal variability may be 13
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attributed to fluctuations in rainfall, river and tidal creek runof f, winds, storm periodicity and maintenance dredging activities. Macrophytes Denthic macrophytes account for a large percentage of total primary production in shallow coastal waters, serve as a food source to higher trophic forms, provide sites of attachment to a variety of marine plants and animals, increase habitat complexity for benthic fauna, stabilize sediments and enhance nutrient recycling (Humm,1964; Wood et al.,1969; Thayer et al.,1975; Thayer and Phillips,1977: Phillipr,1978). Both quantitative and qualitative assessments were made of macrophyte assemblages adjacent to the Crystal River Power Plant. Within the nearshore basins, seagrass and macroalgae composition and biomass were quantitatively determined (Figure 3), while qualitative assessments of seagrass coverage and distribution were made along transects over an expanded area in both discharge and control zones (Figure 4). Over the five years of ETS monitoring, 31 genera of macroalgae and five species of seagrasses were collected at the 12 permanent discharge and control stations. Distinctively different assemblages associated ( with divergent envi ronmental conditions were found to exist within the two zones. 14
Benthic macroalgae predominated in the control zone, generally contributing over 75 percent of total macrophyte biomass (Figure 9). Within this basin,17 genera of Rhodophyta (red algae) and 7 genera each of Phaeophyta (brown algae) and Chlorophyta (green algae) were collected over the five years of sampling. Gracilaria was the most frequently encountered red alga, followed by Spyri di a , Chondria and Laurencia. Sargassum and Caulerpa were the most frequently collected genera of brown and green algae, respectively. Natural fluctuations in abundances of constituent species produced seasonal shifts in the relative contribu-tions of each division to total biomass. By contrast, macroalgae contributed little to total macrophyte biomass in the discharge basin (Figure 9). These that were present were p rimarily dri f t forms in the di vision Rhodophyta. Comparisons of preoperational and operational data indicated that algae biomass in the discharge zone was noticeably greater in 1973 than during the period of Unit 3 operation (1977-1981). It is unclear if the general absence of macroalgoe at discharge stations after 1977 was related to the operation 1 of 'Init 3 or was merely an artifact of changes in sampling locations. The seagrasses Halodule wrightii, Syringodium filiforme, Ruppia l maritima, Halophila engelmani and Thalassia testudinum were all repre-sented in collections made during ETS monitoring at the Crystal River Power Plant. Within the nearshore discharge basin, seagrass beds were comprised almost exclusively of Halodule, while mixed grass beds occurred in the unconsolidated sediments of the control basin. 15
l l I Monitoring of seagrasses along transects within the nearshore control basin revealed a widespread, yet patchy distribution. Where pre-sent, seagrass coverage was generally sparse to moderate, even though some dense beds did occur close to shore. Throughout operational years, Syringodium filiforme had the most widespread distribution in the control basin. Individual species contributions to total seagrass biomass was not reported for the years 1977-1980, but in 1981, Ruppia accounted for most of the seagrass biomass collected at control stations (FPC, 1982a). Relative to macroalgae, seagrasses in the control zone generally contri-buted less than 25 percent to total macrophyte biomass (Figure 9). Control stations containing both algae and seagrasses usually had a much smaller total macrophyte biomass than stations where only algae was pre-sent. Within the discharge basin, transect monitoring of seagrasses during operational years revealed pronounced seasonal and spatial fluctuations in the distribution and coverage of Halodule. Coverage was generally widespread and dense throughout most of the basin during some portions of the year except in the area along the southern perimeter of the basin, where a channel directing thermal effluents offshore produced relatively high temperatures. This area was devoid of vegetation over most of the year. 16
Growth patterns of Halodule collected during operational years were consistent between basins, with mean blade length showing greatest growth increments between spring and early summer. Consequently, greatest Halodule biomass occurred during summer sampling periods. However, within the discharge basin, both the sampling period during which maximum biomass was observed and the absolute quantities present varied annually in relation to mean monthly summer water temperatures. In 1978 and 1980, Unit 3 operated less than 20 percent of the time between March and September (Table 4) and the mean summer discharge canal temperatures were less than 35'C (Figure 6). During those years, biomass increased throughout the summer, reaching its peak (143 and 139 9 dry wt/m2, respectively) in September (Figure 10). In 1979, Unit 3 operated 45 percent of the spring-summer period, and although maximum Halodule biomass was also observed in September, the basin average was only 77 g dry wt/m2 In 1977 and 1981, Unit 3 operated over 80 percent of the time between March and September. During those years, mean monthly discharge canal temperatures during the summer exceeded 35*C (Figure 6), and tne maximum observed biomass (58 and 52 g dry wt/m2, respectively) occurred in early summer prior to the period of maximum temperatures. Spatial differences in biomass of Halodule within the nearshore discharge basin were also affected by power plant operation. Stations closest to the point of discharge rarely had seagrasses present, regardless of the operational status of Unit 3. Stations farthest from
-17
l the' point of discharge always had some grasses present, even when all three units were operating. Halodule biomass et intermediate stations varied in relation to season and the combined operating capacity of the three units. Thus, gradients of-Halodule biomass, corresponding to gra-dients of prevailing temperatures, existed within the basin. During 1981, some of the warmest temperatures ever recorded occurred in the nearshore discharge basin, and seagrasses disappeared from all but two stations during late summer. They remained absent for the remainder of the year. When similar die-offs had occurred during other years, sub-sequent recovery had taken place. Thus, it seems that, when provided with periods of thermal relief, Halodule can recolonize areas of the discharge basin previously devoid of vegetation. Several factors nay have been responsible for observed differences in macrophyte composition between nearshore discharge and control basins. The relative scarcity of hard substrates at discharge stations probably prevented the establishment of most species of necroalgae found in the control basin. High water temperatures nay have inhibited the establishment of others. Laboratory and field studies conducted elsewhere in Florida indicate that temperatures in excess of 33 C, such l as those often experienced at discharge stations during the summer, are detrimental to many forms of macroalgae and seagrasses (Bader and Roessler, 1972; Thorhaug et al., 1978). During periods of the year when water temperatures in the discharge basin were less stressful, relatively 18 J c ,- - ..e ..,.-r -
-,ep - - - - , , , , - - - - . - , m --, e-,
high sedimentation rates may have been inhibitive, as the deposition of fine sediments can smother plants, alter sediment chemistry and reduce water clarity (Philips,1978). Of all the seagrasses found in the area, Halodule wrightii, a eurythermal, euryhaline species, is most tolerant of environmental stress. Throughout operational years, Syringodium was :he most ubiquitous seagrass along outer transects in the control zone. In these areas, grasses were widely distributed, but coverage was generally less dense than that observed in the inner control basin. Seagrass distribution in areas of the discharge zone seaward of the nearshore basin was similar to patterns observed in the control zone. All five species of seagrasses were observed, and, as in the control zone, S.vringodium was the most ubiquitous form. Because of higher tur-bidities, however, seagrasses in the discharge zone were primarily limited to the shallow areas near shorelines and adjacent to oyster bars where light penetration was adequate for sustained growth. Seasonal variations in seagrass distribution and coverage occurred throughout the study area and did not repeat themselves precisely each year. No data were presented during ETS monitoring to suggest that power plant thermal effluents were negatively impacting macrophytes in the discharge zone seaward of the nearshore basin. Even within the inner basin, seagrass biomass at stations farthest from the point of discharge 19
1 I i was often greater than that reported for a comparable control station. i More intensive monitoring of macrophyte assemblages throughout the discharge zone, including thermal histories of monitoring stations, are required to accurately determine the areal extent of plant impact under a variety of operating conditions. 1 Benthic Macroinvertebrates Benthic macroinvertebrates exhibit a diversity of form and function; and, as a result, occupy a wide variety of habitats and virtually all trophic levels. Communities of these organisms often support major com-mercial fisheries, serve as important agents in the coupling of benthic and pelagic food webs, affect the sedimentary environment and enhance nutrient regeneration within the-ecosystem (Rhoads,1973; Driscoll,1975; Rhoads et al.,1977; Flint et al.,1982). They are also particularly useful as water quality indicators and have been used to assess the effects of a variety of hydrological parameters (Warriner and Brehmer, 1966; Holland et al.,1973; Rosenberg,1976; Rosenberg and Moller,1979; Reish et al., 1980). During ETS monitoring, benthic macroinvertebrates were collected at 12 permanent stations in the nearshore discharge and ccatrol basins adja-cent to the Crystal River Power Plant. Smaller infaunal forms were collected with core samplers while larger epifaunal forms were taken with a suction device (FPC,1982a). 20
Benthic Core Program The shallow waters of the Gulf of Mexico adjacent to the Crystal River Power Plant were found to support an abundant and diverse assemblage of benthic macroinvertebrates. A total listing of all species collected during operational years is not practical because of taxonomic discrepancies among different researchers performing the work. However, in 1981 alone, 384 taxa were reported from benthic core collections (FPC, 1982a) Over the 1977-1981 monitoring period, the structure of benthic com-munities, as measured by abundance, biomass, species richness, diversity (H') and evenness (J') often experienced marked seasonal fluctuations in response to cyclical envi ronmental conditions (Fi gures 11, 12, 13). However, with few exceptions, values of measured community parameters were higher in the control basin than in the discharge basin. The larger number of control basin taxa is particularly noteworthy, because more sampling stations were located in the discharge basin (7 discharge vs. 5 control stations). Conditions being comparable, increased sampling effort would generally be expected to yield more spe-cies. Inter-basin differences in faunal diversity were attributed pri-marily to differences in water quality and environmental heterogeneity. The discharge basin represented a less complex and more physically stressed environment and, consequently, harbored fewer species. 21
l Most neasured community parameters exhibited seasonal lows during late summer. Because this pattern generally existed in both basins, :t was suggested that warm summer temperatures nay be naturally inhibitive to a number of resident organisms. However, reduced faunal densities, species richness and diversities were much more pronounced in the discharge basin indicating that combined plant operation was having its greatest impact during the summer. A comparison of long term abundance and species richness data showed that the magnitude of nearshore basin differences was greatest in 1977 and 1981 when Unit 3 was operating most of the year (Figures 11 anr.12). Both diversity and evenness of macroinvertebrate communities in the control basin remained remarkably constant throughout operational years indicating a very stable community structure (Figure 12). These param-eters showed much more fluctuation in the discharge basin where power plant effluents created a more dynamic and generally more stressful phy-sical envi ronment. Consequently, macroinvertebrate populations in the discharge basin underwent more frequent population adjustments with nany species being excluded entirely during the summer, it should be noted tha species richness and diversity values reported for 1981 were artifi-cially higher than those reported during previous operational years. u This resulted from a higher level of taxonomy employed that year. Biomass values were consistently higher and more seasonally variable in the control basin (Figure 11). This resulted from the greater variety 22 4
of species inhabiting the control basin. Each collection was composed of a unique combindtion of heavy (arthropods, molluscs, and echinoderms) and > soft bodied forms (annelids, nemerteans, sipunculans) which allowed for a __ potentially wider range of biomass values. In the discharge basin, where primarily soft bodied forms predominated, biomass was more stable. Other C: f actors atypical of community structure (e.g., the occasional collection of a very large specimen) also influenced biomass values, and therefore, this parameter was not particularly well suited for assessing power plant , effects. Although direct comparisons of the benthic data gathered in the various studies commissioned by FPC is difficult because of differences in the level of taxonomy used by different workers, a reasonable degree of confidence can be placed in comparisons of polychaetous annelids collected and identified during operational years. Polychaetes are useful as indicators of water quality because they are generally more tolerant of environmental stress than members of other major macroinvertebrate groups (Rosenberg,1976). Consequently, they are , usually the last group to be excluded from stressful environments and the first to be recruited following abatement of the conditions creating stress. Since po'ychaetes numerically dominated faunal assemblages in both basins, changes in species composition occurring within this group during operational years nay have reflected broader changes occurring throughout the entire benthic community. 23
Total nurabers of polychaete species were conpared between control and discharge basins. From 1977 through 1979, the numbers of species collected in the two basins were similar (Figure 14). In 1980, there were a few more species in the control basin than in the discharge basin. However, in 1981, when Unit 3 operated throughout most of the year, the number of polychaete species collected in the discharge basin declined to the lowest value ever recorded. This decline was not related to dif-ferences in the level of taxonomy employed between years, because the number of taxa collected in the control basin during 1981 was the highest ever recorded. The depressed number of polychaete taxa found in the discharge basin in 1981 coincided with the highest water temperatures recorded during any year of operational monitoring. Even though the number of polychaete species in the nearshore basins was similar in all years but 1981, 18 species were dominant in the control basir, during some portion of the study, while only five species attained dominant status in the discharge basin. For this report, domi-nance was defined as those species occurring in at least 90 percent of the samples collected during a year. Aricidea philbinae was the only species in the discharge basin attaining dominance every year. It was also a dominant in the control basin during all but one year. Tharyx sp. similarly attained dominance in the control basin during four of five years but was never dominant in the discharge basin. 24 \
Within the discharge ' basin, communities experienced a gradient of stress which was most closely related to distance of the sampling loca-tion from the point of discharge of plant effluents. In order to better define the zone of impact, benthic core data for 1981 was reanalyzed and individual discharge stations compared with Station 8 in the control basin. This station was chosen because it was the only control station displaying sediment and macrophyte characteristics similar to those found at discharge stations. The analysis was restricted to total faunal den-sity and species richness. Statistical testing was by means of one-way ANOVA (Tables 6 and 7) and Tukey-Kramer multiple range tests (Figures 15 and 16). Data were tested for homogeneity of variances and -transformed when necessary. During Quarter 1, infaunal densities in the discharge basin were significantly. depressed at Stations 1 and 7 (Figure 17). As temperatures increased during spring and early summer, the zone of impact increased to include Stations 4, 5 and 6 (Figure 18). Except for Station 4, densities remained significantly depressed at these stations throughout the summer (Figure 19). However, by winter, densities at all stations but Station 1 had recovered to levels recorded at the control station (Figure 20). Thus, even though densities at most discharge stations were negatively ( affected, communities were capable of recovering to pre-perturbation
~ levels as thermal plume temperatures declined. It should be noted that during Quarters -3 and 4, macroinvertebrate densities at Station 3, the station farthest from the point of discharge, were significantly greater than those at the control station (Figure 15).
25
L L Species richness was more permanently affected. During Quarter 1 Stations 1, 7, 2 and 4 had significantly fewer species than the control station (Figure 21). The zone of impact expanded in early summer to include all discharge stations (Figure 22). This wide zone of adverse effects was maintained throughout the remainder of the year (Figures 23 and 24)..
- Suction Dredae Program A suction dredge has been used throughout the ETS benthic monitoring program at Crystal River to supplement data generated from the collection of benthic core macroinvertebrates. This device samples a larger area than do 'the cores, and the powerful suction catches the larger, more motile animals which are often -missed. in core sampling. Unfortunately,
.there are numerous problems in utilizing the data from these collections.
For example, the minimum size of animals retained for analysis varied in different studies. Inspection of the preoperational study (1973-1974)
' species list revealed that ' primarily larger animals such as crabs and shrimp were retained for analysis. Later researchers, 1977-1981, kept
.and analyzed all animals retained by the mesh bags. Consequently, com-parisons of preoperational and operational macroinvertebrate densities and biomass obtained by suction dredge are not appropriate. However,.
comparisons could be made between operational years when sampling metho-dologies and processing techniques were the sa"p. I 26
l Since 1977, when Unit 3 became operational, the mean numbers of individuals per square meter were consistently less in the discharge basin than in the control basin (Figure 25). During these years, dif-ferences between basin means were generally greater during periods when Unit 3 was operating most of the time (1977 and 1981). No seasonal trends were apparent from the data. Biomass was generally greater in the control basin during opera-tional years; but, for three quarters in 1980, the discharge basin had greater values than the control (Figure 25). Discharge biomass values were particularly depressed during periods when Unit 3 was operating much of the time. Diversity (H') followed a pattern very similar to that of faunal density (Figure 26). The control basin usually had values greater than the discharge basin, and differences between basins were accentuated in years that Unit 3 was operating a large percentage of the time. Evenness (J ') showed little deviation over the years of opaational monitoring (Figure 26), and there was no clear pattern of differences between basins. Suction dredge data supported inferences drawn from benthic core data. Control basin community parameters were generally higher than those measured for the discharge basin, and differences between basins were greatest during periods when Unit 3 added to the thermal load of 27
Units 1 and 2. Similar to the smaller infaunal forms, the greater variety of' larger macroinvertebrates found in the control basin was related to the less stressful physical environment and greater habitat complexity found there. Within the discharge basin, individual' station data presented for 1981 indicated a gradient of decreasing plant effect with increasing distance from the point of discharge. Oyster Reef Communities large beds of the American oyster, Crassostrea virginica, are common in the study area and serve a variety of ecological functions. They pro-vide _ links in the benthic, pelagic and planktonic food chains; and, by increasing habitat heterogeneity, provide living space for many sessile and motile species which might otherwise be absent. The oyster system with its rich associated fauna constitutes an important ecological com-ponent of tropical and warm temperate estuarine ecosystems and is a source of high biological productivity '(Odum,1971).
~ During preoperational (1973) and operational monitoring (1977-1981),
the recruitment, growth and general condition of the oyster and the den-sity, species richness, species composition and dominance of fauna living on the reefs were monitored in control and discharge zones (Figure 5). All~ oyster reefs sampled in the discharge zone were close enough to the point of discharge to be potentially affected by thermal effluents. 28
Between 1977 and 1981, mean numbers of adult oysters in the control zone were always greater than mean numbers in the discharge zone (Figure 27). Only during the winter sampling of the 1973 preoperational study did the number of adult oysters in the discharge zone exceed that of the control zone. Differences between quarterly zone means did not appear to be influenced by the operational status of Unit 3. l Zone differences in number of adult oysters between preoperational
, and operational years could not be accounted for by changes in the rela-tive numbers of oyster spat occurring during those periods. During - preoperational years, the mean number of spat was greater in the control than in the discharge zone, and this pattern continued throughout opera-tional years (Figure 22). This suggests that differences in spat den-sities between zones were either natural or had previously developed from the operation of Units 1 and 2. Mean biomass values for both adult oysters and oyster spat closely approximated trends observed for den-l sities (Figures 27 and 28).
The ratio of oyster biomass to shell length previously used as an index of plant effect may vary with several factors not associated with 1 envi ronmental stress (Scott and Lawrence, 1982). Mean dry weight of oysters, expressed in mg of meat per adult individual, is a function of size-selective mortality and growth rates and may provide a better gauge of prevailing environmental conditions. In the four years (1973,1978, 1979, 1980) when Unit 3 was inoperative during most of the summer, the 29
mean weight per individual was greater in the discharge zone during all but one year (Figure 29). In both years for which Unit 3 was operating throughout most of the summer (1977, 1981), the average weight per indi-vidual was greater in the control zone. Although there are not enough years to adequately test these distributions statistically, the trend suggests that the continual operation of Unit 3 during summer months may have decreased the average weight of adult oysters below levels measured when only Units 1 and 2 were operating. This may have been achieved through increased mortality of large animals and/or decreased growth rate of individuals. During 1981, the only year for which individual station data were reported, the annual mean number of oysters collected per square meter increased with increasing distance of the reef from the point of discharge (Figure 30). There was also considerable spatial variation among stations in the control zone. However, mean numbers per square meter at the least dense control station (107) were greater than the mean values recorded in all but two of the discharge stations (Figure 30). Observed differences in the numbers of adult and juvenile oysters , comprising the reefs sampled in discharge and control zones may be attri-i butable to a number of factors. The American oyster is sensitive to tem-peratures above 32 C and rapid temperature transitions can be equally detrimental at tenperatures less than 32*C (Menzel,1956; Galtsoff,1964; Tinsman and Maurer,1974). Furthermore, low D0, high salinities and high ; 30 i
sedimentation rates, all conditions periodically affecting the discharge zone, can each limit oyster survival, growth and reproduction. Consequently, the control zone constituted a less stressful physical envi ronment for the oysters and greater numbers of Individuals were collected there. Prior to the 1981 report, the fauna associated with oyster reefs were presented in the form of relative abundances per zone. Only molluscs and decapod crustaceans were routinely identified to species level. Furthermore, it was indicated that decapods frequently escaped collection and may not have been quantitatively sampled (FPC, 1979). Consequently, only molluscs collected on oyster reefs during operational years could be quantitatively compared. f In general, the number of taxa of molluscs associated with the oyster reefs in both zones increased throughout operational years (Figure 31). This may have been an artifact of the different levels of taxonomy employed over the years, or may reflect a real long-term trend. The number of mollusc species was consistently lower _in the discharge zone than in the control zone (Figure 31), however, there was no consistent pattern of differences between zones that could be attri-buted to Unit 3. The years with the greatest and least differences be-tween zones in terms of numbers of mollusc taxa were the two years in which Unit 3 was operating most of the year (1977 and 1981). 31
For coaiparative purposes only, 50 percent relative occurrence in all ~i samples for a year was arbitrarily set as an indicator of dominance. In the discharge zone', there was never more than one dominant mollusc spe-cies during any year (Table 8). The bivalve, Ischadium recurvum, domi-nated the associated fauna in the discharge zone in 1977 and 1978, while another bivalve Brachidontes spp., dominated in 1979, 1980 and 1981. The number of dominant oyster reef molluscs in the control zone ranged from 1 (1981) to 5.(1978, 1979).
- The mean number of taxa for all oyster reef ' macroinvertebrates collected during 1981,- the only year for which individual station data were reported, increased as the distance of the reef from the point of thermal discharge increased (Figure 32). The least densely populated-control zone station (107) had greater numbers of associated fauna than all but one station in the discharge zone (101). The mean number of taxa
] of oyster reef-associated fauna followed the same pattern (Figure 33). Salt Marshes ! Salt marshes . occupy the sea-to-land transition zone in temperate latitudes. These wetland systems are of great ecological importance since they _ serve as nursery areas for many species of fish and macroin-
' vertebrates (same commercially valuable), partially support the detritus food web of adjacent estuaries, retard erosion and freshwater runoff and serve to increase - the habitat heterogeneity of 'the estuarine system
_(Humm,1973). , 32
. ~ . _ _ - . . - . . , _ . - . . . - . . , _ . . . . _ . - . _ . . _ . . - _ . . , , . . . .
1 In -the vicinity cf the _ Crystal River Power Plant, there are two -
' basic- forms . of ' salt marshes. Shoreline areas with relatively -low -
topographic relief 'are usually inundated daily (at leasti during high tides) and are characterized by almost pure stands of the smooth cordgrass, Spartina alterniflora. Areas farther inland .have slightly-higher topographic relief and inundation- by sea water is usual;v aperiodic, often -- coming during storm tides or during times of high onshore winds. This latter region'is dominated by the black needlerush, Juncus roemarianus. Near-the Crystal River Power Plant Spartina forms a relatively narrow seaward fringe around vast areas of Juncus. Inunediately adjacent to the discharge canal of the power plant is a
- relatively large-salt marsh (Figure 5). In order to determine if thermal effluents from Units- 1, 2 and 3 were affecting this area, marsh plants and selected invertebrates were monitored from 1977 through 1981'and data
= compared with 'a . comparable marsh habitat in the control zone. Pre-operational and operational data were compared to assess the additional impact caused by Unit 3.
Marsh- Grasses Preoperational data indicated similar stem densities, stem lengths and biomass of ' live Spartina plants between discharge and control marshes i L(Figures 34, 35 and 36). During operational monitoring, stem densities were consistently greater in the discharge marsh than in the control marsh, except in 1981 when densities were again similar between marshes 33 i.
~,-.. .w , -~.v. -y. 7y,,-,,4.,m.,my,,vm..m -,..,,.,.,,,,%-~,,.m.-__,..m.c-- - . - _ , , ,
(Figure 34). Throughout all operational ye2rs, stem lengths were shorter in the discharge marsh (Figure 35). Thus, it seemed that the operation of Unit 3 caused stem densities of discharge Spartina plants to increase
.and stem lengths to decrease. However, long-term data indicate that the most appreciable changes in these characteristics occurred not- in the discharge marsh but rather in the control marsh. In fact, when only data for the- discharge marsh are examined, Spartina stem lengths appear to have actually increased after Unit 3 began operatior..
The most probable cause for the observed structural - patterns was a change in control sampling locations between preoperational and opera-
- tional years. During 1973, the control station was located within the discharge zone but on an offshore island believed to be outside the
^ influence of plant operations. Marsh structure of this " control" station . was apparently similar to that ' observed in the discharge marsh on the mainland. During operational years, the control marsh was located in the control zone where influences of plant operation were known to be mini-mal. As a result of this change in sampling location, Spartina plants in i the control marsh appeared to have become dramatically less dense and ! taller. i Assuming that patterns observed at the two operational sampling locations are typical of general conditions existing within the discharge and control zones, and assuming that marshes within the two zones were once similar, it can be concluded that the construction and/or operation 34 ] 1
, . , . - - - . ,-,,,-~,,.,.~~,.-+.w.,,.--,-,--,m~,,,,--r,-~,n--, ,,-e,, --,w- ,.,._,,-._--~---.r-w , n , n ,. . , . , . - , , , , . , - -
of the Crystal River Power Plant has affected structural changes in the Spartina marsh adjacent to the dicharge basin. However, the additional impact o' Unit 3 cannot be inferred from this data. Examination of operational data indicate that stem densities of 1 Spartina were more seuonally variable in the discharge marsh than in the control marsh. Within the discharge marsh, densities were generally lower during 1977 and 1981 when Unit 3 operated much of the year (Figure 34). Seasonal growth patterns were similar between discharge and control marshes, largest Spartina plants being collected during the warmer sampling periods and the smallest plants being collected during the cooler months of the year (Figure 35). Above-ground biomass within the Spartina marshes was generally similar between discharge and control zones, but significantly greater values were sometimes obtained in the control marsh (Figure 36). No preoperational data regarding stem densities and lengths exist for the Juncus marsh. Operational data suggest that discharge marsh plants were generally more dense and shorter than control marsh plants (Figures 37 and 38). However, in 1981, a dramatic decline in Juncus stem densities occurred within the discharge marsh and a reversal of this pat-tern took place. Although this decline could be attributed to the con-tinual operation of Unit 3 during 1981, Unit 3 also operated throughout much of 1977 and densities that year were similar to other operational years. 35 _ _ . ~ . _ -. . . _ - . _ - _ - __ _
l The most likely cause for the observed chaage in pattern is again related to a change in sampling location. The discharge sampling site was reliably maintained between 1977 and 1980, but when different researchers assumed monitoring responsibilities in 1981, the location of the site was not precisely determined. These data suggest that Juncus stem densities may exhibit considerable spatial variability. The lengths of plants seem much less variable since stem lengths between 1981 and previous operational years were similar even though a change in sampling location had occurred. Above-ground biomass of Juncus plants was similar between marshes thoughout operational years, except in 1981 when reduced stem densities probably accounted for the appreciable decline in biomass (Figure 39). Similarly low biomass values were also obtained in the discharge marsh during the preoperational study. It is unknown if this reflected a real difference in the structure of the discharge Juncus marsh prior to the operation of Unit 3 or was, again, merely an artifact of station changes within a spatially variable marsh system. In summary, the construction and subsequent operation of Units 1, 2 and 3 have apparently structured shorter but more dense salt marshes in J the discharge zone. The increased densities may be a function of decreased apical growth stimulating increased output of more stems, but experimentation would be required to demonstrate this. The similarity of above-ground biomass between discharge and control marshes suggests that 36
the loss of biomass in the discharge zone associated with reduced stem lengths has largely been offset by increased stem densities. Marsh Macroinvertebrates The periwinkle, Littorina i rrorata, inhabiting the Spartina marsh had similar densities in the control and discharge basins during the preoperational (1973) study (Figure 40). However, during all years after Unit 3 began operation, densities were consistently greater in the discharge marsh. Again, differences between studies were probably related to changes in the location of the control station. Long-term data suggest that observed increases in the densities of Littorina within the discharge marsh after Unit 3 began operating are real. In 1977-1978, the control marsh had very low numbers of L. irrorata, and in 1981, no indi-k viduals were found in the control marsh. Whether or not this is a natural, cyclical population phenomenon is unknown. There are no 1973 data for L_. irrorata from the Juncus marshes, however, data for all other years follow trends similar to those reported for the Soartina marshes (Figure 41). Differences between control and discharge marshes were generally less than those noted for the Spartina marshes. This is not unexpected since the Juncus marshes are on higher ground; thus, the animals are not subjected to heated water as frequently 1 as they are in the Spartina marsh. 37
.. .. _ . - - _ _ _ _ )
The density of fiddler crab (Uca spp.) burrows in the Spartina marshes were generally higher in the control marsh during the preopera-tional study (Figure 42). During years of intermittent Unit 3 activity, densities were sometimes significantly greater in the discharge marsh than in the control, but the control marsh never had densities signifi-cantly greater than the discharge marsh. When Unit 3 was operating for most of the year (1981), densities in the control and discharge marshes were the same excyt in Quarter 4 when the control had greater numbers. Insufficient data are available to determine whether or not the decrease in burrow density in the discharge zone during Quarter 4 was related to Unit 3 operation. No preoperational data exist for Uca spp. burrows in the Juncus marshes. However, data from 1977-1981 followed the same trends reported for the Spartina control and discharge marshes -(Figure 43). These data suggest that thermal effluents may stimulate population growth of periwinkles in both Spartina and Juncus marshes, and the effects are accentuated . in the Spartina marshes where sea water inundation is greatest. Fiddler crab burrow densities were more uniform between discharge and control basins, and no consistent patterns were apparent. 38
LITERATURE CITED Adams, C.A. 1974. Comparison of selected vertebrate populations in two estuaries adjacent to the Crystal River Power Generation Facility, pages III 111-106. In Crystal River Power Plant environmental considerations, final rep 6rt to the Interagency Research Advisory Committee. Vol. III. Florida Power Corporation, St. Petersburg, Florida. Adams, C.A., M.J. Desterling and S.C. Snedaker. 1974 Effects of im-pingement and entrapment on the Crystal River blue crab, Callinectes sapidus, Rathbun, population, pages III-107 - 111-146. M Crystal River Power Plant environmental considerations, final report to the Interagency Research Advisory Committee. Vol. III. l Florida Power Corporation, St. Petersburg, Florida. Bader, R.G. , and M.A. Roessler. 1972. An ecological study of south Biscayne Bay and Card Sound. Progress report to U.S. Atomic Energy Commission (AT (40-1)-3801-4 ) . Rosenstiel School of Marine and Atmospheric Science, University of Miami. Coral Gables, Florida. Blake, N.J., L.J. Doyle and T.E. Pyle 1976 The macrobenthic community of a thermally altered area of Tampa Bay, Florida, pages 296-301. In G.W. Esch and R.W. McFarlane (eds.), Thermal ecology II. NTIS Iio. CONF-750425 Technical Information Center, Energy Research and Development Administration. Boesch, D.F. and R. Rosenberg. 1981. Response to stress in marine ben-thic communities, pages 179-200. h G.W. Barrett and R. Rosenberg (eds.), Stress effects on natural ecosystems. John Wiley and Sons, New York. Cottrell, D.J. 1974 Sediment composition and distribution at Crystal River Power Plant: erosion vs. deposition, page.s 11-309 376. h Crystal River Power Plant environmental cc1siderations, final report to the Interagency Research Advisory Committee. Vol . II . Florida Power Corporation, St. Petersburg, Florida. Cottrell, D.J. 1978. Analysis of suspended and surficial sediment in the discharge basins of Crystal River Power Generating Facility, Crystal River, Florida, Appendix C. M Special surveillance stu-dies, Crystal River - Unit 3. Florida Power Corporation, St. Petersburg, Florida. Driscoll, E.G. 197S. Sediment-animal-water interaction, Buzzards Bay, Massachusetts. Journal of Marine Research, 33:275-302. 39 CRYRIVI LITCITED-5
LITERATURE CITED (continued) ; I Evink, G. and B. Green. 1974. Benthic invertebrate comparisons in two estuaries adjacent to the Crystal River Power Generation Facility, pages 111 111-55 In Crystal River Power Plant environmental considerations, final retort to the Interagency Research Advisory 1 Committee, Vol. III. Florida Power Corporation, St. Petersburg, ' Florida. Flint, R.W., S. Rabalais and R. Kalke. 1982. Estuarine benthos and eco-system functioning, pages 185-201. M J.R. Davis (ed.), Proceed-ings of the symposium on recent benthological investigations in Texas and adjacent states. Texas Academy of Sciences, Austin. l FPC (Florida Power Corporation). 1978a. Crystal River Unit 3, Annual Envi ronmental Operating Report, Vol. I. Non-radi ological , 1-14 12-31-77. Florida Power Corporation, St. Petersburg, Florida. FPC (Florida Power Corporation). 1978b. Intake velocity determinat an, Appendix B. h Special surveillance studies, Crystal River - Unit
- 3. Florida Power Corporation, St. Petersburg, Florida.
FPC (Florida Power Corporation). 1979. Post operational ecological monitoring program, Crystal River Units 1, 2 and 3. Annual report, 1978. Vols. I and II. Florida Power Corporation, St. Petersburg, Florida. FPC (Florida Power Corporation). 1980. Post operational ecological monitoring program, Crystal River Units 1, 2, and 3. Annual report 1979. Vols. I and II. Florida Power Corporation, St. Petersburg, Florida. FPC (Florida Power Corporation). 1981. Post operational ecological monitoring program, Crystal River Units 1, 2 and 3. Annual report, 1980. Vols. I and II. Florida Power Corporation, St. Petersburg, Florida. FPC (Florida Power Corporattor.). 1982a. Post operational ecological monitoring program, Crystal River Units 1, 2 and 3. Annual report, 1981. Vol . I . Florida Pcwer Corporation, St. Petersburg, Florida. FPC (Florida Power Corporation). 1982b. Post operational ecological monitoring program, Crystal River Units 1, 2 and 3 Final report on estuarine and salt marsh metabolism studies, 1977-1981. Florida Power Corporation, St. Petersburg, Florida. Galtsoff, P.S. 1964 The American oyster. Fisheries Bulletin, 64:1-480. 40 CRYRIVI LITCITED-5
LITERATURE CITED (continued) Gibson, R.A., J.0.R. Johansson, M.E. Gorman and T.L. Hopkins. 1974. Phytoplankton ecology in the vicinity of the Florida Power Corpor-ation Generating Plant at Crystal River, November,1973 - April, 1974, pages IV-419 - IV-444. M Crystal River Power Plant environ-mental consideratiSns, final report to the Interagency Research Advisory Committee. Vol. IV. Florida Power Corporation, St. Petersburg, Florida. G ray , J.S. 1974 Animal-sediment relationships. Annual Revue of Oceanography end Marine Biology, 12:223-261. l- Grimes, C.B. 1971. Thermal addition studies of the Crystal River Steam Electric Station. Florida Department of Natural Resources, Marine Research Laboratory, Professional Papers Series,11:1-53. Grimes, C.B. and J.A. Mountain. 1971. Effects of thermal effluent upon m6rine fishes near Crystal River Steam Electric Station. Florida Department of Natural Resources, Marine Research Laboratory, Professional Papers Series,17:1-64 Holland, J.S., N.J. Maciolek and C.H. Oppenheimer. 1973. Galveston Bay benthic community structure as an indicator of water quality. Contributions- to Marine Science, 17:169-188. Homer, M. 1974 Tidal creeks and effects of power plants, pages I-387
- I-417. h Crystal River Power Plant Environmental Considera-tions, final report to the Interagency Research Advisory Committee.
Vol. I. Florida Power Corporation, St. Petersburg, Florida. Humm, H.J. 1964. Epiphytes of the seagrass, Thalassia testudinum Konig, in Florida. Bulletin of Marine Science of the Gulf and Caribbean, 14:306-341. Humm, H.J. 1973. III. The biological environment, A. Salt marshes, pages IIIa IIIA-6. h J.I. Jones, R.E. Ring, M.0. Rinkel and R .E. Smith (eds). A summary of knowledge of the eastern Gulf of Mexico 1973. Coordinated by State University System of Florida Institute of Oceanography, St. Petersburg, Florida. Kemp, M. 1974. Ecosystems of the intake and discharge canals, pages
- I-367 -
I-386. h Crystal River Power Plant envi ronmental i considerations, final report to the Interagency Research Advisory , Commi ttee. Vol. I. Florida Power Corporation, St. Petersburg, l t Florida. Kemp, M.H. McKellar and M. Homer. 1974 Value of higher animals at Crystal River estimated with energy quality ratios, pages 11-93 108. h Crystal River Power Plant environmental considera-tions, final report to the Interagency Research Advisory Committee. Vol. II. Florida Power Corporation, St. Petersburg, Florida. 41 CRYRIVI LITCITED-S
LITERATURE CITED (continued) Klausewitz, R.H. 1979. Thermal plume determination and model verifica-tion during Unit 3 operation, Appendix A. In Special surveillance studies, Crystal River - Unit 3. Florida Tower Corporation, St. Petersburg, Florida. Klausewitz, R.H., S.L. Palmer, B.A. Rodgers and K.L. Carder. 1974
" Natural heating of salt marsh waters in the area of the Crystal !
River Power Plant", pages 111-379 - 111-412. In Crystal River Power Plant environmental considerations, finaFreport to the Interagency Research Advisory Committee. Vol. III. Florida Fower Corporation, St. Petersburg, Florida. Knight, R.L. and W.F. Coggins. 1982. Record of estuarine and salt marsh metabolism at Crystal River, Florida, 1977-1981. In Post operational monitoring program, Crystal River Units 1, 2 and 3. Final report on estuarine and salt marsh metabolism studies, 1977-1981. Florida Power Corporation, St. Petersburg, Florida. Lehman, M. 1974 Oyster reefs at Crystal River and their adaptation to thermal plumes, pages I-269 - I-361. M Crystal River Power Plant envi ronmental considerations, final report to the Interagency Research Advisory Committee. Vol . I. Florida Power Corporation, St. Petersburg, Florida. Logan, D.T. and D. Maurer. 1975 Diversity of marine invertebrates in a thermal effluent. Journal of the Water Pollution Control Federation, 47:515-523 Lyons, W.G., S.P. Cobb, D.K. Camp, J.A. Mountain, T. Savage, L. Lyons and E.A. Joyce, Jr. 1971. Preliminary inventory of marine inverte-brates collected near the electric generating plant, Crystal River, Florida, in 1969. Florida Department of Natural Resources, Marine Research Laboratory, Professional Papers Series,14:1-45 Maturo, F.J., Jr. and R.D. Drew. 1974 Effects of power plant entrain-ment on major species of copepods: Measurement of zooplankton mortality using adenosine tri-phosphate as a viable biomass indicator, pages IV-235 - IV-264 M Crystal River Power. Plant envi ronmental considerations, final report to the Interagency Research Advisory Committee. Vol. IV. Florida Power Corporation, 5 St. Petersburg, Florida. Maturo, F.J., Jr., R. Alden and W. Ingram, III. 1974a. Effects of power plant entrainment on major species of copepods, pages IV-69 - IV-102 In Crystal River Power Plant envi ronmental considerations, finaIreport to the Interagency Research Advisory Committee. Vol. IV. Florida Power Corporation, St. Petersburg, Florida. 42 CRYRIVI LITCII'ED-S
LITERATURE CITED (continued) Maturo, F.J., Jr., J.W. Caldwell and W. Ingram, III. 1974b. Effect of power plant operation on shallow water coastal zooplankton, pages IV-265 - IV-268. In Crystal River Power Plant envi ronmental considerations, final-~~ report to the Interagency Research Advisory Committee. Vol . IV. Florida Power Corporation, St. Petersburg, Florida. McKellar, H. 1974. Metabolism and models of outer bay plankton eco-systems affected by power plant, pages I-159 - I-268. M Crystal River Power Plant envi ronmental considerations, final report to l the Interagency Research Advisory Committee. Vol. 1. Florida Power Corporation, St. Petersburg, Florida. Menzel, R.W. 1956. The effect of temperature on the ciliary action and other activities of oysters. Florida State University Studies 22. Papers from the Oceanographic Institute, 2:25-33. Mountain, J.A. 1972. Further thermal addition studies at Crystal River Florida with an annotated checklist of marine fishes collected 1969-1971. Florida Department of Natural Resources Marine Research Laboratory, Professional Papers Series, 20:1-103. Odum, E.P. 1971. Fundamentals of ecology. W.B. Saunders. Philadel-phia. 574 pp. Patrick, R. 1974. Effects of abnormal temperatures on algal com-munities, pages 335-349. In J.W. Gibbons and R.R. Sharitz (eds.), j Thermal ecology. AEC SympoTium (CONF)-73505. Augusta, Georgia. Phillips, R.C. 1978. Seagrasses and the coastal marine environment. ! Oceanus, 21:30-40. Reish, D.J., D.F. Soule and J.D. Soule. 1980. The benthic biological conditions of Los Angeles-Long Beach Harbors: Results of 28 years ! of investigations and monitoring. Helgolander Meeresunters, l 34:193-205 l Rhoads, D.C. 1973. The influence of deposit-feeding benthos on water turbidity and nutrient recycling. American Journal of Science, 273:1-22 Rhoads, D.C., R.C. Allen and M.B. Goldhaber. 1977. The influence of colonizing benthos on physical properties and chemical diagenesis l of the estuarine seafloor, pages 113-138. M B.C. Coull . (ed. ), Ecolog" of marine benthos. University of South Carolina Press, Columbia. 43 CRYRIVI LITCITED-5
I l l LITERATURE CITED (continued) ; Rodgers, B.A., R.H. Klausewitz and T.J. Keller. 1974. Results on bathymetry and bottom type analysis of the Crystal River Power Plant discharge basin ,- Technical report No. 5, pages 111-413 111-443. M Crystal River Power Plant envi ronmental con-siderations, final report to the Interagency Research Advisory Committee. Vol. III. Florida Power Corporation, St. Petersburg, Florida. Rosenberg, R. 1976. Benthic faunal dynamics during succession following pollution abatement in a Swedish estuary. Oikos, 27:414-427. Rosenberg, R., and P. Moller. 1979. Salinity stratified benthic macro-faunal communities and long-term monitoring along the west coast of Sweden. Journal of Experimental Marine Biology and Ecology, 37(2):176-203. Scott, G.I. and D.R. Lawrence. 1982. The American oyster as a coastal zone pollution monitor: A pilot study. Estuaries, 5:40-46. Smith, - W. 1974. Shallow inshore ecosystem of bottom communities and the effect of thermal plume, pages I I-158. M Crystal River Power Plant envi ronmental considerations, final report to the Interogency Research Advisory Committee. Vol . I . Florida Power Corporation, St. Petersburg, Florida. Snedaker, S.C 1974 Impingement at the Crystal River Power Generation Facility. A quantitative analysis, pages II-259 308 I n, Crystal River Power Plant envi ronmental considerations, final report to the Interagency Research Advisory Committee. Vol. II. Florida Power Corporation, St. Petersburg, Florida. Steidinger, K.A., and J.F. Van Breedveld. 1971. Benthic marine algae adjacent to the Crystal River Electric Power Plant (1969 and 1970). Florida Department of Natural Resources, Marine Research Laboratory, Professional Papers Series,16:1-46 Thayer, G.W., and R.C. Phill4s. 1977. Importance of eelgrass beds in Puget Sound. Marine F',: hery Review, 39:18-22. Thayer, G.W., D.A. Wolfe and R.B. Williams. 1975. The impact of man on seagrass systems. American Science, 63:296. Thorhaug, A., N. Blake and P.B. Schroeder. 1978. The effect of heated effluents from power plants on seagrass (Thalassia) communities quantitatively comparing estuaries in the subtropics to the t ropics. Marine Pollution Bulletin, 9:181-186. 44 CRYRIVI LITCITED-5
l LITERATURE CITED (continued) Tinsman, J.C., and D.L. Maurer. 1974 Effects of a thermal effluent or, the American oyste r, pages 223-236. In J.W. Gibbons and R.R. Sharitz, eds. Thermal ecology. AEC. Symposium Series (CONF 730505), Augusta, Georgia. Van Tine, R.F. 1974 Comparisons of the benthic flora in estuaries adjacent to the Crystal River Power Generation Facility, pages 11-377 437. In Crystal River Power Plant environmental con-siderations, final report to the Interagency Research Advisory Commi ttee. Vol. II. Florida- Power Corporation, St. Petersburg, j Florida. Vernberg, F.J. and W.B. Vernberg. 1974. Synergistic effects of temperature and other environmental parameters on organisms, pages 94-99. In J.W. Gibbons and R.R. Sharitz, (eds.) Thermal Ecology. CONF-7305Ii5. NTIS, Springfield, Virginia. Virnstein, R.W. 1972. Effects of heated effluent on density and diver-sity of benthic infauna at Big Bend, Tampa Bay, Florida. M.S. Thesis, University of South Florida, Tampa, Florida. 60 pp. Warinner, J.E., and M.L. Brehmer. 1966. The effects of thermal effluents on marine organism. Ai r and Water Pollution International Journal, 10:277-289. Wood, E.J.F., W.E. Odum and J.C. Zieman. 1969. Influence of seagrass on the productivity of coastal lagoons, pages 495-502. In Lagunas Costeras. Un Simposio Mem. Simp. Intern. UNAM-UNESCIT, Mexico D.F. Nov. 1967. Woodin, S.A. 1976 Adult-larval interactions in dense infaunal assemblages: patterns of abundance. Journal of Marine Research, j 34:25-41. i Young, D. 1974 Salt marsh and the effect of thermal plume, pages 11 11-92. _I_n, n Crystal River Power Plant environmental consider-ations, final report to the Interagency Research Advisory Cemmi ttee. Vol. II. Florida Power Corporation, St. Petersburg, Florida. l 45 CRYRIVI LITCITED-b
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. Crystal River Power Plant, 1977-1981.
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* ^
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! Z ; g 0.40-i W g 0.20-0 , , , , , , i i i i i i i i i i i I i
1 2 3 4 1 2 3 4 1 2 3 4 1 2 3 4 1 2 3 4 1977 1978 1979 1980 1981 QUARTERLY SAMPLING PERIODS l Figure 13. Mean diversity and mean evenness of macroinvertebrates collected by Lenthic cores, i Crystal River Power Plant, 1977-1981. I
l 12Q- $ CONTROL O DISCHARGE l i l l l 100-f ~~g
/ N
' N 0
b' N 80-
- 3 D 37.2, D 33.9, D 32.0, y
0 37.0 g C 30.0* C 30.9' C 29.5* C 30.O* D 37.5, C o' 5 i 2 60-l 5 40-20-
, e i i i 1977 1978 1979 1980 1981 YEAR Figure 14. Total number of polychaete species collected annually in discharge and control basins, Crystal River Power Plant, 1977-1981. Numbers below the curves represent maximum observed discharge (D) and control (C) basin water temperature ( C).
9 e
- n. . - - . - - , . -- ,. -- ,, , . - - - , , . , . . - . . , . - . ,-.n.n..
l QUARTER 1 QUARTER 2 1 2 3 4 5 6 7 8 1 2 3 4 5 6 7 8 x . . . . . . , N . . . . . . 2 .3 A . . . 2 m, x . . . . 3 .595 .287 . 3 L323 .001 . . . . 4 A66 .157 .130 . . 4 .925 .397 398 . . . . 5 .688 379 092 .222
- 5 .536 .786 .787 .389 . .
6 .655 .347 060 .190 .032 . 6 .376 .946 .947 546 .159 . . 7 151 .157 .444 314 .536 .504 . 7 .000 <L3221323.925 .536 376
- 8 .512 .204 .083 .361 8 L285 037 037 .361 .750 .909 L285
.047l.175.143 CRITICAL VALUE 0.212 CRITICAL VALUE 0.342 QUA R TER' 3 QUARTER 4 1 2 3 4 5 6 7 8 1 2 3 4 5 6 7 8 N . . . . . . . ,
N . . . . . 2 1.146 . . . 2 .524 . . 3 603 .543 . . . 3 .567 .043 . . . 4 .979 .167 .376 . 4 .347 .177 .220 5 882 .264 .279 097 . . 5 .214 .310 .353 .133 . 6 .766 .380 .163 .213 .116 . . 6 ,511 012 .056 .165 296 . 7 424 1570102E140213051.18e . 7 .190 334 377 .157 024 322 8 1298 .152 .695 .319 A16 .533 L722 8 .304 ,219 .263 .042 .091 .207 .115 I CRITICAL VALUE 0.350 CRITICAL VALUE 0.258 l l Figure 15. Results Of Tukey-Kramer multiple range test appliea w quarterly l macr 0 invertebrate densities at discharge stations (1-7) and a l comparable control station (8), Crystal River Power Plant,
- 1981.
- indicates a significant difference.
l t i
QUARTER 1 QUARTER 2 1 2 3 4 5 6 7 8 1 2 3 4 5 6 7 8 1 N . . . . . . . , N . . . . 2 .,4 2 N . . . . , ,00 N . . . . 3 .359 2,, N . . 3 5 m6 N . . . . 4 .228 .086 .132 . . 4 338 .162 .197 . .
. 5 .170 .329 .365 .168 . .
5 .363 .221 .004 .135 6 .338 .197 .021 .111 D25 \ . 6 .167 343 .378 .181 .013
\ . .
7 .177 035 .182 ,051 .186 .161 . 7 .080 379 415 418 .250.237 . 8 .376 234 .016 .148 .013 D37 399 8 762 .262 .227 .424 592 .605 .842 CRITICAL VALUE 0.113 CRITICAL VALUE 0.199 QUARTER 3 QUARTER 4 2 4 5 6 7 8 1 2 3 4 5 6 7 8 1 3 N . . . . . . , N . . 2 .285 N . $ 2 153 N . . . . . .
.303 .018 $ $ 3 924 .177 .
3 4 .283 002.019
\ *
- 4 .002 151 .027 \ *
$ $ 5 .012 .140 .037.010 .
5 260 .025 .043 .024
& $ 6 D63 ,216 .039 .065 ,075 .
6 .181 105 .122 .103 079 7 .280 .565 582 .563 .539 460 \ $ 7 068 22: D44 070 n80 005 262 8 .751 465 .448 A67 491 570 1.03C 8 .249 402 .225 .251 .186 .181 l CRITICAL VALUE 0.193 CRITICAL VALUE 0.134 l l Figure 16. Results Of Tukey-Kramer multiple range test applied to total number Of macr 0 invertebrate taxa collected each quarter at discharge stations (1-7) and a comparable control station (8), Crystal River Power Plant,1981.
- indicates a significant difference.
l l
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1 l Figure 18. The zone of significant negative impact on discharge basin macro-fr. vertebrate densities relative to a comparable control station, Quarter 2, Crystal River Power Plant,1981.
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ggtoMETER \ Figure 19. The zone of significant negative impact on discharge basin macro-invertebrate densities relative to a comparable control station, Quarter 3. Crystal River Power Plant,1981.
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1.0 i i KtLOMETER l li I Figure 20. The zone of significant negative impact on discharge basin macro-l invertebrate densities relative to a comparable control station Quarter 4, Crystal River Power Plant,1981.
. 4..'...,,'.,. .s-( - ? *,-
s ..
% . . ., . ......,.s,-
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1.0 1 5 i K)LOMETER I l Figure 21. The zone of significant negative impact on total number of discharge basin macroinvertebrate taxa relative to a comparable control station, Quarter 1, Crystal River Power Plant,1981, l
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K\LOMETER Figure 22. The zone of significant negative impact on total number of discharge basin macroinvertebrate taxa relative to a comparable control station, Quarter 2 Crystal River Power Plant, 1981. S
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1 { Figure 23. The zone of significant negative impact on total number of I discharge basin macroinvertebrate taxa relative to a comparable control station, Quarter 3, Crystal River Power Plant,1981.
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1.0 1 1 gtOMETER l i Figure 24. The zone of significant negative impact one total number of discharge basin macroinvertebrate taxa relative to a comparable control station, Quarter 4, Crystal River Power Plant,1981. l l
i 1600-N >______o
- l E I ~
comRot 'j N : : j g DISCHARGE
- J 1200-Z 343000_
I 4 < W _O l g g 800- ,o____o Q / \ E,,,
, ^%g
,4 ,F \
Fy 'N 'N ' ID i i l O g
- 400-m# / \
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i 100- p ) On It E E 80- /
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\/
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/
m. gv 0 A 1 2 3 4 1 2 3 4 1 2 3 4 1 2 3 4 1 2 3 4 1977 1978 1979 1980 1981 QUARTERLY SAMPLING PERIODS
- Figure 25. Density and biomass of benthic fauna collected by suction dredge, Crystal River Power Plant, 1977-1981.
~
O-----O CONTROL
^
0 DISCHARGE 5.00-F Os
/%
W
/ MN f 4.00-w /
! / O.&- C s A --d l y) 3.00- O' 'n -O,
~
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^
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'v'Av, --O---o -O--9-4v,p-S A%, o-
- s -
- N a60-E
- 2 2 0.40-W l W 0.20-O I I I I I I I I I I I i i i i i i i i 1 2 3 4 1 2 3 4 1 2 3 4 1 2 3 4 1 2 3 4 1977 1978 1979 1980 1981 QUARTERLY SAMPLING PERIODS Figure 26. Diversity and evenness of benthic fauna collected by suction dredge, Crystal River Power Plant, 1977-1981.
- a E
N g 2,000- O----- o CONTROL Q _J /\ R O O DISCHARGE A b
]; \ j 'g D fg l 4 u"- N,/ \\
i i 2O m
/
/
\j
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R j o \ 'l ! 4 5 t000 b.a/ mO N 'd 3 s 4- --<r.- i 2 500- 'ty 4 O o. Z 250-l9\ M "^ 200- &-q g I f\ E \ 4Q / \ t\ l I \ i 3I Oeiri 150- e 0-- / \
\ /
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s i I g g 100- s
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. i . . . . . . . . . . . . . . . .
1 2 3 4 1 2 3 4 1 2 3 4 1 2 3 4 1 2 3 4 1 2 3 4 1974 1977 1978 1979 1980 1981 QUARTERLY SAMPLING PERIODS l Figure 27. Quarterly mean abundance and mean biomass for adult oysters from oyster reef j stations in the control and discharge zones, Crystal River Power Plant,1973
' and 1977-1981. (aData not available).
- N '
g O-----O CONTROL E ir O DISCHARGE s 3,000- / g O J 2500- d
/ \\ 1
;\
z$ /\ ~
\\ ,R As 4Q 2 /sg
/ \ / hT i uJ - \ / 4N / s/-
- 1,500- \ / p d \
g >b I g I s / O ] 3 1000- g P -d s / l
& / V d 500- A ,A g i z o.
O ~T e ' '
- 500-I M "a 9 l U) g #' A l\ R 1 <a EI 300-
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i h'%d 3 ct' \ ,1 8 l 0
- 0 1 b3 1 i 55d i b3 I I b5d i h3 ii55I 1973 1977 1978 1979 1980 1981 QUARTERLY SAMPLING PERIODS Figure 28. Quarterly mean abundance and mean biomass for spat from oyster reef stations in the control and discharge zones, Crystal River Power Plant,1973 and 4 1977-1981. (aData not available).
0 0 CONTROL 150 O- ~A DISCHARGE b~ -a- ,%
; N / \
}100- N y' N
! K\
\
E A g so-E 19b 0974) id77 1978 Id79 IY'0 id81 YEARS Figure 29. Mean dry weight of adult oysters for control a'id discharge zones, f' Crystal River Power Plant,1973 and 1977-1981.
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Basin 5 Q . r]y/- - 480.8 % .?* ii',1 (83.0) % ** "%goB '
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% 2 f - % 76.5 MLfhe /'[ (73.2)=..
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s ,,ff ... .
'gn.oMETER .;iv. , ,, , . ..
Figure 30. Mean number of adult oysters collected quarterly at each station, Crystal River Power Plant, 1981, dumbers in parentheses are 1 standard error about the means.
31 e---.e CONTROL b---d DISCHARGE 26-21-0 5
~
16-o 5 I E A 11- / 16
/
/
/
/
.h
~
4' W N,7 1 6 _ - 3 h ' / 17 11 1977 Id78 1979 1980 id81 YEARS Figure 31. Number of mollusc taxa collected from oyster reefs in discharge and control zones, Crystal River Power Plant, 1977-1981. Numbers under the discharge basin curve are the actual differences in number of taxa between control and discharge basins.
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KILOMETER ., f g . .. . . Figure 32. Mean number of macroinvertebrate taxa collected quarterly at each oyster reef station, Crystal River Power Plant, 1981.
I l (
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KILOMETER .,q.. '. . : 2 Figure 33. Mean number /m of macroinvertebrates collected quarterly at each oyster reef station, Crystal River Power Plant, 1981. [ s
0 0 DISCHARGE { Mean
- 11*
- ONMOL & 300=
- E
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- b g ' 'l - b y' 'I W S S F W S S F W S S F W S S F W 5 S F W S S F W 1973 1977 1978 1979 1980 1981 Figure 34. Mean density of live Spartina stems during 1973 preoperational and 1977-1981 operational monitoring, Crystal River Power Plant.
- Indicates a significant difference between control and discharge marshes.
2,000- 0 0 DISCHARGE {u.an
*** i1 **
O----O CONTROL 1,750 - D w 1,500-M th = . 1,250-N p' to "
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250-W S S F W 5 S F W S S F W S S FW S S F W5 S F W 1978 1979 1980 1981 1973 1977 Figure 35. Mean stem length of Spartina during 1973 preoperational and 1977-1981 operational monitoring, Crystal River Power Plant. (One standard error is always less than 3 cm).
- Indicates a significant difference between control and discharge marshes.
14 0 - e e DISCHARGE ,, 3 j O-----O CONTROL l 130- 1 i
. I\ !
1 11 .A4 T l t , f g S 120-I f t s'g\ jR f I f I d 1 E \ f\ /
/
2 110- # g / \. fg i I V \ i ! \ ! y I 100-E *./ \
\ l l \
\* 1 f *f I
\ ! g i 90- V \
80-70-NO DATA W S S F W S S F W S S F W S S F W 5 5 F W S S F W 1978 1979 1980 1981 1973 1977 Figure 36. Mean biomass of live Spartina during 1973 preoperational and 1977-1981 operational monitoring, Crystal River Power Plant.
- Indicates a significant difference between control and discharge marshes.
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NO DATA W S S F W S S F W S S F W S S F W S S F W S S F W 1973 1977 . 1978 1979 1980 19 81 Figure 38. Mean stem length of Juncus during 1977-1981 operational monitoring, Crystal River Power Plant. (One standard error is always less than 3 cm).
- Indicates a significant difference between control and discharge marshes.
w e ,e r l 0 0 DISCHARGE 1 3,000- {u..n
^
Cu O----O CONTROL ; l E
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NO DATA (C) W S S F W S S F W S S FW S. 5 F W S S F W S S F W 1978 1979 1980 1981 1973 1977 Figure 39. Mean biomass of live Juncus during 1973 preoperational and 1977-1981 operational monitoring, Crystal River Pcwer Plant.
- Indicates a significant difference between control and discharge marshes.
e
- 0 DISCHARGE
{*Meani1 ^ 25- O-----O CONTROL . ,, t *
- 20 )_ -- ..
h- f .. e
- 15- ?
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ws s F ws s F ws s F w s' s F W s s F W s s F W 1973 1977 1978 1979 1980 1981 Figure 40. Mean density of periwinkles in Spartina marshes during 1973 pre-operational and 1977-1981 operational monitoring, Crystal River Power Plant.
- Indicates a significant difference between control and discharge marshes.
l 0 0 DISCHARGE y ,,,, 3 j I standard error a 25 - O----O CONTROL s o U 20-l \ 15 - - y . l >- . 10- , ' .] ( '
.* (L\
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W S S F W S S F W S S F W S S F W S S F W S S F W 1973 'i977 1978 1979 1980 1981 Figure 41. Mean Idensity of periwinkles in Juncus marshes during 1977-1981 operational monitoring, Crystal River Power Plant.
- Indicates a significant difference between control and discharge marshes.
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0 0 DISCHARGE y g,,, 3 j 450- I standard error < > O----O CONTROL ago_ ,
^
N 350- " ' l
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50- 1 h NO DATA W S S F W S S F W S S F W 5 S F W S S F W S S F W 1973 1977 1978 1979 1980 1981 Figure 43. Mean density of fiddler crab burrows in Juncus marshes during 1977-1981 operational monitoring, Crystal River Power Plant.
- Indicates a significant difference between control and discharge marshes.
TABLE 1 OPERATIONAL CAPACITIES OF CRYSTAL RIVER UNITS 1, 2 AND 3 CRYSTAL RIVER POWER PLANT Nameplate Became Unit Fuel capacity (MW) operational 1 fossil 440 October 1966 2 fossil 524 November 1969 3 nuclear 890 March 1977 CRYRIVI TABLE 1 E 89
l 1 ll t re 1 1 7 1 7 1 7 2 7 4 7 4 7 4 7 4 7 4 7 ot 7 pa 9 9 9 9 9 9 9 9 9 9 ed 1 1 1 1 1 1 1 1 1 1 R p p p p . a a a a p P1 P4 P6 P7 a0 I 1 I 1 1 1 1 1 1 P2 t . . . . . T r f . f . f . f . .. l l l l l N o oo oo oo oo oo o o o o o A p rN rN rN rN rN V V V V V L e P P P P P P R . . . . . , R r Rr R r Rr Rr C C C C C R N e N e N e Ne Ne P P P P P E DS DS DS DS DS F F F F F W O P m s R s r r d m i E l e e n sf l V a r t t a i o o I t es a a l b R e t n tr ae wsy wsy e r oe a m e da da u br au t e L d wt A e e m ,s nb nb t tt m T i c e y a a c ecs y S d a g so r r u mul V u rs n e ce ce r ra t R t tr i tn in it t ntn i C s
,t e p m
ai r hn ti hu to s msa u c n u E s ys i bs n n y l y m H r ty el ef ef t ote m T e i o , ta bo bo i ci g o 2 t l s rt n nr c F e an e ee dm dm u rua E O m a ui q t a vm n ns ai ns ai m m emh tmc l as L B Y r s r ie l l o aos tk A T a re b e oc yo yo c wci oe T I P ed e a ra tb tb d te N ti t g cr ia ia f dc r I ac r l at lt lt em nid dc I C wi
,t e
v a m, ae um ae um es ri ahn ta n al V s n c ,y q q ro l cn a se i i s st n n iee sd E H h ep o r h t h e ei hl rm eu rm eu eb ta hbk t a ht ei T sd c n s sa tl tl st ndt s i n a e i iu ao ao ye enn if N I F a M B F Fq Wc Wc Om Bai Fo D E a T n C o U i D t N a O z R R R R R G G G G G C i N N N N N E E E E E n D D D D D S S S S S S a E g I r D O U n T i S a t n dd u s nl o r . ae M o l v t a rd d a ee n r g t ge a n i e nr i a t s iB s a l n s e s d e t h l a r e m n in m n t e m p e v i o ea i u i K h m m n r y tV r o m c e e o I G L S G M S M L K H l l
n .. . . . .. . 7 TABLE 2 (continued) STUDIES CONDUCTED IN THE VICINITV 0F THE CRYSTAL RIVER POWER PLANT Report Investigators Organization a Parameters studied Report date Young SEG Salt marsh community structure and FPC, Vol. II 1974 metabolism i Kemp et al. SEG Ecosystem trophic relationships and FPC, Vol. II 1974 energy flow Impingement FPC, Vol. II 1974 Snedaker RMS Cottrell RMS Sediment composition and distribution FPC, Vol. II 1974 Macrophyte comunity structure FPC, Vol. II 1974
$ Van Tine RMS Evink and Green RMS Benthic macroinvertebrate and benthic FPC, Vol. III 1974 fish community composition Adams RMS Fish biomass FPC, Vol. III 1974 Adams et al. RMS Impingement effects on blue crabs FPC, Vol. III 1974 Klausewitz et al. DMS Natural heating in salt marshes FPC, Vol. III 1974 Rodgers et al. DMS Bathymetry and bottom types in FPC, Vol. III 1974 discharge basin j Maturo et al. UFML Copepod entrainment FPC, Vol. IV 1974a Maturo et al. UFML Zooplankton comunity structure FPC, Vol . IV 1974b l
Maturo and Drew UFML Zooplankton entrainment FPC, Vol. IV 1974 l
TABLE 2 - (continued) STUDIES CONDUCTED IN THE VICINITY OF THE CRVSTAL RIVER POWER PLANT Report Investigators Organization a Parameters studied Report date Gibson et al. DMS Water quality, phytoplankton com- FPC, Vol. IV 1974 munity structure Cottrell UM Analysis of suspended sediments in FPC Spec. Sur-discharge basin veillance Study, 1978 Append. C Florida Power Corp. FPC Intake velocity determinations, FPC, Spc. Sur- 1978b Unit 3 veillance Study, Append. B E Klausewitz WVWC Thermal plume determination, Unit 3 FPC, Spec. Sur- 1979 veillance Study, Append. A Connell, Metcalf, CME Benthic macroinvertebrate and macro- FPC, Vol. I. 1978 and Eddy phyte community structure, oyster Parts I and II 1979 i reef community structure, zooplank- 1980 l ton community structure, water quality Metcalf and Eddy ME Benthic macroinvertebrate and macro- FPC, Vol. I, 1981 phyte community structure, oyster Parts I and II reef community structure, zooplank-ton community structure, water quality, sediments Caldwell and Odum SEEA Ecosystem metabolism of inner and FPC, Vol. II 1978 (Principal Investi- outer bays and salt marsh community 1979 gators) structure and metabolism 1980 1981
TABLE 2 (continued) STUDIES CONDUCTED IN THE VICINITY OF THE CRYSTAL RIVER POWER PLANT Report l Investigators Organization a Parameters studied Report date Applied Biology, Inc ABI Benthic macroinvertebrate and macro- FPC, Vol. I 1982a phyte community structure, oyster reef community structure, water quality, sediments and salt marsh community structure Ecosystem metabolism of inner and FPC 1982b l Knight and Coggins SEEA l outer bays and salt marsh comunity structure and metabolism 8 # 0rganizations conducting monitoring activities at the Crystal River Power Plant. DNR: Florida Department of Natural Resources, Marine Research Laboratory SEG: Systems Ecology Group, Department of Environmental Engineering Sciences, University of Florida. RMS: Resource Management Systems Program, Institute of Food and Agricultural Sciences, University of Florida. DMS: Department of Marine Science, University of South Florida. UFML: University of Florida Marine Laboratory. Ult: Rosenstiel School of Marine and Atmospheric Science, University of Miami. FPC: Florida Power Corporation, Environmental Affairs Department. WVWC: West Virginia Wesleyan College.
TABLE 2 (continued) STUDIES CONDUCTED IN THE VICINITV 0F THE CRYSTAL RIVER POWER PLANT Report Investigators Organization a Parameters studied Report date
' Organizations conducting monitoring activities at the Crystal River Power Plant. (cont'd)
CME: Connell, Metcalf and Eddy, Environmental Consultants. ME: Metcalf and Eddy, Environmental Consultants. SEEA: Systems Ecology and Energy Analysis Group, Department of Environmental Engineering Sciences, University of Florida. ABI: Applied Biology, Inc., Environmental Consultants. 2 y . m
* '
- r q \
TABLE 3
SUMMARY
OF BENTHIC SAMPLING PROGRAM CONDUCTED AT CRYSTAL RIVER POWER PLANT 1977-1981 Number of Number of Sampling Sieve Total sanples l ! Type of gear Biota sampled Data sets stations replicates frequency size annually 10-cm diameter Small macroinverte- Species 12 5 Quarterly 0.5 mm 240 corer brate infauna and composition epifauna viversity Abundance Biomass Suction dredge Large macroinverte- Species 12 1 Quarterly 0.3 cm 48 brate infauna and composition ; l e epifauna Diversity
- Abundance Biomass 50 x 50-cm box Macrophytes Species 12 3 Quarterly N/A 144 composition Biomass Transect 1-m2 Macrophytes Species Approxi- 5 Quarterly N/A Approximately composition mately 150 3000 quadrats Percentage coverage General condition 50 x 50-cm box Oyster reef fauna Species 9 2 Quarterly 0.2 cm 72 composition Diversity Abundance Biomass
TABLE 3 (continued)
SUMMARY
OF BENTHIC SAMPLING PROGRAM CONDUCTED AT CRYSTAL RIVER POWER PLANT 1977-1981 Number of Number of Sampling Sieve Total samples Biota sampled Data sets stations replicates frequency size annually Tyra of gear l Salt marsh grasses Abundance 2 S in Juncus Quarterly N/A 112 50 x 50-cm 9 in Spartina quadrats and epifauna Biomass General condition CRYRIVI g TABLE 3 l l l l
TABLE 4 AVERACE MDMTHLY FPC DISCHARGE (AD) MD INTAKE (AI) CANAL TEMPERATURES, MEAN MDNTHLY TEWERATURE DIFFERENTI ALS ("t) AND PERCENTAGE OF DAYS EACH MONTH THAT UNIT 3 WAS OPERATIPG (PO) CRYSTAL RIVER POWER PLANT 1977-1981 l 1977 1978 1979 1980 1991 Month AD Al "t PO AD Al "t PO AD Al *t PO AD Al *t PO AD Al "t PG January 12.7 10.4 2.3 t0 18.9 11.2 7.7 100 19.5 11.9 7.6 100 22.1 15.1 7.0 100 to 9.8 - 100 February 15.5 12.0 3.5 17 16.6 10.3 6.3 89 20.0 13.5 6.5 100 20.5 13.7 6.8 82 21.0 13.7 7. 3 39 March 24.3 20.0 4.3 90 21.1 16.0 5.1 6 22.1 18.1 4.0 52 21.8 18.3 3.5 0 23.7 17.1 6.6 3 April 28.1 22.7 5.4 95 27.1 22.7 4.4 0 27.8 24.5 3.5 to 25.3 22.2 3.1 0 28.0 22.7 5.3 59 May 31.0 25.3 5. 7 51 30.6 25.3 5.3 0 28.3 26.8 1.5 0 29.5 26.0 3.5 0 32.9 25.3 7.6 95 June 35.7 29.5 6.2 81 33.5 28.0 5.5 0 ND 28.7 - 0 32.3 28.7 3.6 0 37.9 30.3 7.6 95 July 36.2 30.0 6.2 100 33.3 29.1 4.2 0 to 30.9 - 74 33.3 30.0 3.3 0 36.1 30.1 6.0 59 August 34.0 28.7 5.3 54 33.3 29.8 3.5 0 34.4 30.4 4.0 to 36.2 30.0 6.2 67 37.5 29.6 7.9 100 September 35.5 29.6 5.9 to 31.8 29.4 2.4 16 33.5 28.7 4.8 100 36.7 29.1 7.6 100 35.5 28.0 7. 5 90 October 29.9 23.3 6.6 100 30.0 26.7 3.3 100 31.8 25.3 6.5 100 32.3 24.4 7.9 100 29.0 23.8 5.2 0 7.6 28.3 22.7 5.6 100 27.1 20.3 6.8 to 26.7 18.7 8.0 100 24.5 18.4 6.1 0 November 26.8 19.2 100 December 21. J 14.5 7.1 to 24.4 16.1 8.3 100 22.5 15.9 6.6 100 to 14.7 - 100 20.0 13.8 6.2 61 ND= Indicates data not available or only partial data available for the nonth. CRYRIVI TABLE 4 4 t ,
l l TABLE 5 POLYCHAETE TAXA COLLECTED IN AT LEAST 90 PERCENT OF THE SAMPLES TAKEN EACH YEAR IN DISCHARGE (D) AND CONTROL (C) BASINS CRYSTAL RIVER POWER PLANT 1981 - Frequency of 1977 1978 1979 1980 1981 domination Scientific name C D C D C D CD C D C D Aricidea philbinae x x x x x x x x x 0.80 1.00 A. taylori x x x x x 0.60 0.40 Axiothella mucosa x 0.20 0.0 Chone duneri x x 0.40 0.0 Exogone dispar x 0.20 0.0 Mediomastus x x 0.40 0.0 californiensis Notomastus latericeus x 0.20 0.0 Polydora websteri x 0.20 0.0 Prionospio x x x 0.40 0.20 heterobranchia Syllis sp. x x x 0.10 0.0 Tharyx sp. x x x x 0.80 0.0 Laeonereis culveri x x x 0.20 0.40 Onuphis nebulosa x x x 0.60 0.0 0.0 Fabricia sp. x 0.20 Lysilla alba x 0.20 0.0 Scoloplos rubra x x 0.40 0.0 Tharyx dorsobranchialis x 0.0 0.20 Streblospio bennidicti x 0.20 0.0 Capitella capitata x 0.20 0.0 Number of dominant polychaete species 11 2 5 2 7 2 5 2 5 3 Number of polychaete species attaining dominance once (yr) 9 2 Cumulative Number of polychaete dominants occuring in each basin 1977-1981 18 5 98 I i
TABLE 6 ONE-WAY ANOVA* APPLIED T0 QUARTERLY MACR 0 INVERTEBRATE DENSITIES AT SEVEN DISCHARGE (1-7) AND ONE CONTROL STATION (8) CRYSTAL RIVER POWER PLANT 1981 QUARTER 1 Source Sum of squares DF Mean square Total 2.849950 39 Groups 2.145940 7 0.3065620 Error 0.7040100 32 0.02200030 Calculated F Critical F 13.93440 2.680000 Significantly Different P(0.05 QUARTER 2 Source Sum of squares DF Mean square Total 13.21050 39 Groups 11.37930 7 1.625610 Error 1.831250 32 0.05722640 Calculated F Critical F 28.40660 2.680000 Significap;;1y Different P(0.05 - 99
TABLE 6 , (continued) l ONE-WAY ANOVA* APPLIED TO QUARTERLY MACR 0 INVERTEBRATE DENSITIES AT l AND ONE CONTROL STATION (8) SEVEN DISCHARGE CRYSTAL R (1-7)IVER POWER PLANT 1981 QUARTER 3 Source Sum of squares DF Mean square Total 14.01230 39 Groups 12.09320 7 1.727590 Error 1.919110 32 0.05997230 Calculated F Critical F 28.80650 2.680000 Significantly Different P(0.05 QUARTER 4 Source Sum of squares DF Mean square Total 2.388460 39 Groups 1.348210 7 0.1926010 Error 1.040250 32 0.03250790 Calculated F Critical F 5.924740 2.680000 Significantly Different P(0.05 OData were transformed using log 10(X+1). 100
TABLE 7 ONE-WAY ANOVA* APPLIED TO TOTAL NUMBER OF MACR 0 INVERTEBRATE l TAXA COLLECTED AT SEVEN DISCHARGE (1-7) AND ONE CONTROL STATION (8) CRYSTAL RIVER POWER PLANT . 1981 QUARTER 1 Source Sum of squares DF Mean square Total 0.8396300 39 . Groups 0.6412960 7 0.09161380 Error 0.1983340 32 0.006197930 Calculated F Critical F 14.78140 .2680000 Significantly Different P<0.05 QUARTER 2 Source 3um of squares DF Mean square Total 3.526440 39 Groups 2.907070 7 0.4152960 Error 0.6193690 32 0.01935530 Calculated F Critical F 21.45640 2.680000 Significantly Different P(0.05
<0.
101
TABLE 7 (continued) ONE-WAY ANOVA* APPLIED TO TOTAL NUMBER OF MACR 0 INVERTEBRATE TAXA COLLECTED AT SEVEN DISCHARGE (1-7) AND ONE CONTROL STATION (8) CRYSTAL RIVER POWER PLANT 1981 QUARTER 3 Source Sum of squares DF Mean square Total 3.569270 39 Groups 2.988170 7 0.4268810 Error 0.5810970 32 0.01815930 ' Calculated F Critical F 23.50760 2.680000 Significantly Different P<0.05 QUARTER 4 Source Sum of squares DF Mean square Total 0.7191200 39 Groups 0.4388310 7 0.06269020 l Error 0.2802890 32 0.008759020 Calculated F Critical F 7.157210 2.680000 Significantly Different P<0.05 OData were transformed using log 10(X+1). 102
TABLE 8 l DOMINANT MOLLUSC SPECIES ASSOCIATED WITH Crassostrea virginica REEFS OF DISCHARGE AND CONTROL ZONES CRYSTAL RIVER POWER PLANT 1977-1981 1977 1978 1979 1980 1981 Taxa Con Dis Con Dis Con Dis Con Dis Con Dis Ischadium recurvum x x x x Carditamera floridana x x x - Crepidula plana x x x Brachidontes spp. x x x x x x Ostrea equestris x x , Semele porficua x x Number of dominants 2 1 2 1 5 1 5 1 1 1 CRYRIVI TABLE 8 s L 103}}