e G. Ryan 

Envi $0 n m 8 ntal Scie nc 

‘\ 
L ____.__" ................... ..______..............._.__.___ - -... . .I___~__ 
ORNL/TM-I1926 

Environmental Sciences Division 

ECOLOGICAL EFFECTS OF CONTAMINANTS IN MCGOY BRANCH, 

1989-1990 

Editor 

M. G. Ryon 

Contributors 

R. L. Hinzman' 

M. J. Peterson2 

T. D. Richardson3 

M. G, Ryon 

J. G. Smith 

G. R. Southworth 

A. J. Stewart 

V. R. Tolbert 

Environmental Sciences Division 

Publication No. 3837 

'Oak Ridge Research Institute, Oak Ridge, Tennesscc 

2Automated Scicnces Group, Inc., Oak Ridgc, Tennessee 

3P0s tdoo toral Associate, Oak Ridge Associated Univcrsitics 

Date of Issue-January 1992 

Prepared for 

S. Walker 

Environmental Restoration Program 

Y-12 Plant 

Oak Ridge, Tenncssec 37831 

Prepared by the 

OAK RIDGE NATIONAL LABORATORY 

Oak Ridge, Tennessee 37831-6285 

managed by 

MARTTN MARIETTA ENERGY SYSTEMS, INC. 

for the 

U.S. DEPARTMENT OF ENERGY 

under contract DE-AC0.5-840R21400 MARTIN MAAICTTA ENERGY SYSTF#& LIBRIHIP'? 

3 4456 0352812 7 

LISTOFFIGURES ................................................ V 

LISTOFTABB ................................................. vii 

ACRONYMS ..................................................... ix 

ACKNOWLEDGMENT3 ............................................ xi 

EXECUTITVESUMMARY ........................................... xiii 

1 . INTRODUCTION ............................................... 1-1 

2 . DESCIUPTlON OF THE McCOY BRANCH WA'IERSHED 

(RLH~IE~~II) ................................................. 2-1 

2.1 GEOHYDROLOGY .......................................... 2-4 

22 WATERQUALlTY .......................................... 2-4 

22.1 Description and History of Discharges to McCoy Branch 

and Rogers Quarry ...................................... 2-4 

222 Characterization of the Contaminant Source .................. 2-5 

2.23 Temperature ........................................... 2-6 

22.4 Sediments and Groundwater ............................... 2-6 

3 . IDXICITY MONITBRING (A . L Stew art and T . D . Richardson) ........... 3-1 

3-1-1 Seven-Day Toxicity Tests .................................. 3-1 

3.1.2 Full Life-Cycle Tests ............................... .' ..... 3-1 

3.1.3 In situ Snail Tests ....................................... 3-2 

3.1.4 Seven-Day Snail Tat .................................... 3-5 

3.1.5 Chemical Analyse, of Water Quality ......................... 3-5 

3.2 RESULTS .................................................. 3-6 

3.2.1 Seven-Day Toxicity Tests .................................. 3-6 

3.2-2 Full-Life Ojcle Tests ..................................... 3-6 

3.24 Seven-Day Snail Test .................................... 3-10 

3.2.5 Chemical Analyses or Water Quality ......................... 3-10 

3.2 MATERIAL§ AND METHODS ................................. 3-1 

3.2.3 In Situ Snail Tat ....................................... 3-10 

3.3 DISCUSSION ............................................... 3-14 

3.4 FUTURESTUDIES .......................................... 3-16 

4 . BIOACCUNULATlON STUDIES (G . R Southworth and M . J . Peterson) .... 4-1 

4.1 XN?*RODUCTEON ........................................... 4-1 

4.2 METNODS ................................................. 4-1 

4.3 REBULTS AND DISCUSSION ................................. 4-2 

4-4 CONCLUSIONS ............................................ 4-9 

4.5 FWTURESTUDIES ......................................... 4-10 

... 

11 1 
CBmm (Continued) 

NT (U 6 . Ry~m) ..................... 5-1 

........................................... 5-1 

.................................... 5-1 

AND DISCUSSION .................................. 5-4 

.................................... 5-4 

.................................... 5-6 

...................................... 5-6 

...................................... 5-8 

CAOB ....................................... 5-8 

.................................. 5-8 

.................................... 5-10 

5.5 FU'TURESl'UDlES .......................................... 5-10 

(V . It Tolkrt and J ..................................... 6-1 

5.1 XNTRODIJ(JTXON ........................................... 6-1 

6.2 MATERIALSAND~VETHODS ................................. 6-1 

...................................... 6-3 

ition .................................. 4-3 

6.3 . 2 Density and Biomass ..................................... 6-3 

6-4 DIrnSSION ............................................... 6-11 

6-5 CONCLUSIONS ............................................. 6-15 

6.6 p;UTcRESTJDES ......................................... 6-16 

6-33 chammunity Structure .................................... 6-6 

7 . lxEm.EN(7m .................................................. 7-1 

APPENDIX A WATER QUALnrY DATA FOR MCCOY 

BRANCH WATERSHED FOR 19'74-1990 ................. A-1 

AJ?PEMNx B . 

I AND WHITE OAK CREE 

....................... B-1 

iv 
figure 

2-1 

2-2 

2-3 

2-4 

2-5 

26 

3-1 

5-1 

6-1 

6-2 

6-3 

6-4 

6-5 

6-6 

LET OF FIGURES 

PaJg 

Map of the Oak Ridge area showing locations of the reference sites ....... 2-2 

Map of the McCoy Branch showing the primary features and 

monitoring sites ............................................... 2-3 

Mean weekly values for sulfate in the water from McCoy Branch 

at Outfall 302, belmv Rogem Quarry, hm 1!%% to 1990 ................ 2-8 

Mean wekly values for arsenic in the water from McCoy Branch 

at Outfdl302, below Rogers Quarry, from 1886 to 1990 ................ 2-9 

Mean wcekly values for selenium in water from McCoy Branch 

at Outfall 302, Rogers Quarry, from 1986 to 1990 ..................... 2-10 

Weekly mean temperature for McCoy Branch, and for two 

reference sites, upper White Oak Creek and upper Frth Creek .......... 2-12 

Plot showing the number of snails recavered versus distane from 

the point of release for two sites in McCrry Branch and 

a noncontaminated site in Whitc Oak Creek ........................ 3-11 

Length-frequency histognams for bluegill. sunfish, green suniish, and 

bluntnose minnow for May 1989, October 1989, and May 1990 fiom 

McCoy Branch site. MCK 1.56 .................................... 5-9 

Mean scasonal density and biomass of benthic macroinvertebrates ' 

in McCoy Branch and White Oak Creek, April 1989 to January 1990 ...... 6-7 

Mcan seasonal density for selected taxa in McCby Branch and 

White Oak Creck, April 1989 to January 199Q.. ...................... 6-8 

Mean seasonal biomass for sclected taxa in McCoy Branch and 

White Oak Creek, April 1389 to January 1990.. ...................... 6-9 

Mean seasonal taxonomic richness oE benthic macrahmertebrates 

in McCoy Branch and White Oak Creek, April 1989 to January 1990 ...... 610 

Mean seasonal Ephememptcra, Plmptera, and Trichoptera richness 

in McCoy Branch and White Oak Crcck., April 1989 to January 1990 ...... 6-12 

Mean seasonal diversity of benthic macroinvertebrates in McCoy Branch 

and Whitc Oak Crwk, April 1989 to January 1991) .................... 613 

V 

LIST OF TABLES 

Table &!.E? 

2-1 Mean (standard error) for selscted National Pollutant Discharge Elimination 

System water quality parameters for Outfall 302 for 1986 to 1990 ......... 2-7 

2-2 Arsenic levels in McCoy Branch on March 15,1990 ................... 2-11 

3-1 Results of 7-6 toxicity (fathead minnow 1-i~ and Chidt~W dubia) 

of water from MCCQY Branch at MCK 1.92 .......................... 3-3 

3-2 Results of 7-d toxicity tats (fathead minnaW larvae and Cetidzlaphnia) of 

water from McCoy Branch at the spring near the base of the ash pond dam 

(spring) and from McCoy Branch below Rogers Quaq ................. 3-7 

3-3 Means of Ceriodaphrria survival and reproduction parameters for lifecycle 

tests with wntrol water, water firom McCoy Branch at the inlet to Rogers 

Quarry, and water fi-om East Fork Poplar Creek at the outfall of Lake 

Reality ..................................................... 3-8 

3-4 Analysis of variance results for Cenicdaphnia xife-cycle tests of control water 

and water from McCoy Branch at MCK 1-92 ......................... 3-8 

3-5 Analysis of variance results for Cetiudaphnia lif"-cycle tats of water from 

Lake Rcality outfall and McCoy Branch at MCK 1.92 .................. 3-9 

3-6 Mcans of pH, conductivity, alkalinity, and hardness for daily grab samples 

of water from McCi~y Branch at MCK 1-92? .......................... 3-12 

3-7 Means of nitrate, phosphate, and sulfate concentrations in daily drab 

samples of water from McCoy Branch at MCK 1.92 and the spring near the 

base of the ash pond dam ....................................... 3-13 

3-8 Means of pH, conductivity, alkalinity, and hardness for daily grab samples of 

water from McCoy Branch at MCK 1.60 (July 30-August 5, 1990) and the 

spring at the base of the ash pnd darn (April !5-11,1990) ............... 3-15 

4-1 Concentrations of metals in individual fish collected in Rogcrs Quarry, 

McCoy Branch ernbaymcnt, and a referens stream, Hinds Creek, 

July ......................................................... 4-3 

4-2 Mctal wncentralions in largemouth bass (Mitenu sa-) from 

Rogers Quarry and McCoy Branch embayment and sunfish (Lepmk aurihts 

and L. macrochliius) from Hinds Creek, a reference stream .............. 4-4 

vii 
LIST OF TAIBLES (Continu 

Tablc 

4-3 Concentrations of chlorinated pesticides and PCBs in fish from Rogers 

Quarry, and Hinds Creek July 1990 ................................ 4-8 

5-1 Length, mean width, mean depth, area, and pool-riEfle mtio of 

sampling sites on McCoy Branch and two referencc: stream, 

Grassy Creek and White Oak Creek, for each sampling date ............. 5-3 

5-2 Fish densities in McCoy Branch and in two reference stram 

Creck and Grassy Creek, for April-May 1989 to April-May 1 

5-3 Fish biomass in McCoy Branch and in two reference stream, White Oak 

Creek and Gray Creek, for April-May 1 to Apd-May 1 ......... 5-7 

6-1 Mean annual density, biomass, taxonomic richness, Ephemeroptcra, 

Plecoptera, and Trichoptera richncs, and diversity of benthic, 

macroinvertebrates in McCoy Branch and White Oak Crexk, 

April 1989 to January 1990 ..................................... 6-4 

62 Statistical comparisons of man annual benthic macroinvertebrate 

density, biomass, taxonomic richness, Ephemeroptera, Platoptera, 

and Trichoptera richness, and species diversity in McCoy Branch 

and the referencc strcam, White Oak Creek ......................... 6-5 

... 

Vlll 
ACRONYMS 

AA 

ACD 

ANOVA 

BMAP 

CPI 

DDE 

DDT 

DEM 

DO 

DOE 

EFK 

EWC 

EPA 

EPT 

ES 

ESD 

FDA 

G 

GCK 

GCECD 

GC/MS 

HESA 

HSRD 

LCT 

LOEC 

LR-0 

MAF 

MCK 

NOEC 

NPDES 

ORNL 

ORR 

PAH 

P/B 

PCB 

PGV 

PPM 

QA 

RCRA 

RFI 

RQ 

SD 

SE 

TDC 

TL 

TRC 

Atomic Absorption Spectroscopy 

Analytical Chemistry Division 

Analysis of Variation 

Biological Monitoring and Abatement Program 

Cohort production interval 

dichlorodiphenyldichloroethylene 

dichlorodip henyltrichloroethane 

Department of Environmental Management 

Dissolved oxygen 

Department of Energy 

East Fork Poplar Creek kilometer 

East Fork Poplar Creek 

US. Environmental Protection Agency 

Ephemeroptera, Plecoptera, and Trichoptera richness 

Emission Spectroscopy 

Environmental Sciences Division, ORNL 

U.S. Food and Drug Administration 

Value derived from a median test for multiple samples 

Grassy Creek kilometer 

Gas chromatography/electron capture detector 

Gas chromatography/rnass spectrophotometry 

Department of Health, Safety, and Environmental Affairs 

Health and Safety Research Division 

Life-Cycle Test 

Lowest observed-effect levcl 

Lake Reality outfall 

Mean annual flow 

McCoy Branch kilometer 

No observed-effect concentration 

National Pollutant Discharge Elimination System 

Oak Ridge National Laboratory 

Oak Ridge Reservation 

Polycyclic aromatic hydrocarbons 

Productionlbiomass 

Polychlorinated biphenyl 

Preliminary guidance values 

Parts per million 

Quality Assurance 

Resource Conservation and Recovery Act 

RCRA Facilities Investigation 

Rogers Quarry 

Standard deviation 

Standard error 

Tennessee Department of Conservation 

Total length 

Total rcsidual chlorinc 

ix 
TRE Toxicity reduction evaluation 

TSCA Toxic Substances Control Act 

TSS Total suspended solids 

TVA Tennessee Valley Authority 

WCK White Oak Creek kilometer 

WQC White Oak Creek 

X 
We thank D. K. Cox, W. C. Kyker, L. M. Stubbs, W. M. Harris, B. A. Carrico, E. M. 

Schilling, R. D. Bailey, P. W. Braden, L. S. Ewald, L. A. Kszos, G. P. Morris, and 

L. E Wicker €or their assistance in the laboratory and/or field. We thank M. Maskarinec, 

N. M. Ferguson, and other staff of the Oak Ridge National Laboratory Analytical 

Chemistry Division for sample analysis. We thank B. F. Clark, W. D. Dickinson, 

A. W. McWhorter, and J. A. Wojtowicz for processing the benthic macroinvertebrate 

samples. We are grateful to W. R. Hill of The University of Tennessee, Steve Walker of 

the Y-12 Plant, and R. R. Turner of ESD who reviewed an earlier draft of this report and 

provided many helpful comments. 

This work was funded by the Y-12 Plant Environmental Restoration Program. The 

Y-12 Plant and Oak Ridge National Laboratory are managed by Martin Marietta Energy 

Systems, Inc., undcr contract DE-AC05-840R2140Q with the U.S. Department of Energy. 

xi 

The 1984 Hazardous and Solid Waste Amendments to the Resource Conservation 

and Recovery Act (RCRA) required assessment of all current and former solid waste 

management units. Such a RCRA Facility Investigation (RFI) was required of the Y-12 

Plant for their Filled Coal Ash Pond on McCoy Branch. Because the disposal or coal ash 

in the ash pond, McCoy Branch, and Rogers Quarry was not consistent with the 

Tennessee Water Quality Act, several remediation steps were implemented or planned for 

McCoy Branch to address disposal problems. 

The McCoy Branch RFI plan included provisions for biological monitoring of the 

McCoy Branch watershed. The objectives of the biological monitoring were to: 

(1) document changes in biological quality of McCoy Branch after completion of a 

pipeline and after termination of all discharges to Rogers Quarry, (2) provide guidance on 

the need for additional remediation, and (3) evaluate the effectiveness of implemented 

remedial actions. The data from the biological monitoring program will also determine if 

the classified uses, as identified by the State of Tennessee, of McCoy Branch are being 

protected and maintained. 

BACKGROUND 

In connection with the coal ash disposal, McCoy Branch has been segmented into 

four basic areas: (1) the hcadwater sections of McCoy Branch and a large coal ash pond 

created by a 19-m earthen dam; (2) a section of frec-flowing stream that flows from under 

the dam into Rogers Quarry; (3) Rogers Quarry, a deep, steep-sided lake; and (4) a 

section of free-flowing stream that flows from Rogers Quarry into Mclton Hill Reservoir, 

with an associated cmbaymeiit area. Prior to May 1990, the major source of water for 

McCoy Branch was the coal-ash slurry pumped from the Y-12 Steam Plant. Initially 

(1955), the slurry was piped to the upper rcaches and was contained behind the earthen 

dam. As the area behind the dam filled in (1%5), the slurry was transferred by overflow 

to Rogers Quarry; at first through McCoy Branch and then in 1989 via a pipeline. Four 

measures were initiated in 19% to reduce thc volume of coal ash discharged to Rogers 

Quarry: (1) the Y-12 Steam Plant switched to a higher grade of washed coal; (2) the 

Steam Plant was converted to use natural gas as the primary fuel type in the winter of 

1988; (3) a dry ash handling system was installed to collcct fly ash in May 1990, after 

which, fly ash was no longer discharged to Rogers Quarry; and (4) the Steam Plant is 

scheduled to install a bottom ash dewatering system in 1993, at which time all discharges 

to Rogers Quarry will cease. 

. 

WATER QUALITY 

In 1986, coal ash slurry discharged from the Y-12 Steam Plant wds found to contain 

elevated amounts of aluminum, barium, hron, calcium, iron, magnesium, sodium, arsenic, 

strontium, potassium, total suspended solids, total phosphorous, sulfide, and sulfate when 

compared to background water concentrations. A comparison of water quality data from 

... 

XI11 
Rogers Quarry to data for the effluents from 14 ash ponds associated with WA coal-fired 

power plants revealed that Rogers Quarry effluent was similar to effluent from other coal 

ash disposal ponds in the Tennessee Valley. Water quality data collected from a National 

Pollutant Discharge Elimination System site below Rogers Quarry show a decrease in 

mean weekly levels of sulfate, arsenic, and selenium after the Y-12 Steam Plant converted 

from coal to natural gas as the primary fuel source. 

The results of the toxicity tests of water from McCoy Branch did not show much 

evidence for toxic conditions in this stream. In 7-d laboratory tests, survival and growth of 

fathead minnow larvae and survival and fecundity of C'eriodaphnin were generally high, 

although a few exceptions to this trend were evident. Similarly, in full life-cycle tests, 

Ceiioduphniu had significantly fewer broods and a slightly lower mean daily fecundity in 

McCoy Branch water than they did in the controls, but the number of neonates per brood 

tended to be greater than that in controls. Thus, the net effect of McCoy Branch water 

on Cen'odnphnia fecundity was small. In the in situ tests, snails apparently experienced 

more stress in McCoy Branch at McCoy Branch kilometer (MCK) 1.60 (below Rogers 

Quarry) than they did at either MCK 1.92 (above Rogers Quarry) or at White Oak Creek 

kilometer (WCK) 6.3 (reference stream). At MCK 1.60, the net movement of snails was 

downstream; whcreas, the net movement of the snails at the nther two sites was upstream. 

Typically, upstream movement of snails occurs in noncontaminate streams, and the net 

movement is downstream in contaminated streams. Snails may actively move downstream 

as an escape behavior or may be passively transported downstream by flow. In 7-d 

laboratory tests, snails consumed less food when testcd in water from McCoy Branch at 

MCK 1.60 than they did in water from either MCK 1.92 or WCK 6.3, but this difference 

was not statistically significant. The results of associated chemical analyses also suggest 

the stream is riot highly perturbed. 

BIOACCUMULATION srmm 

Concentrations of selenium, arsenic, and possibly thallium are elevated in largemouth 

bass from Rogers Quarry relative to bass from Melton Hill ResenToir and sunfish from 

Hinds Creek. Imels of selenium and possibly arsenic appeared to be elevated above 

background in bass from McCoy Branch embayment of Melton Hill Reservoir. Only 

arsenic exceeds conservatively based screening criteria; however, virtually all biological 

materials excecd this criterion for arsenic. Cessation of inputs of fly ash to the system, 

coupled with the rapid biological turnover of selenium and arsenic, should result in 

continuing decreases in concentrations of these elements In fish. The very low 

concentrations of mercury in fish from Rogers Quarry are consistent with findings of other 

research on interaction between selenium and the bioaccumulation of mercury, and 

suggest research arcas for possible remediation of local mercury-contaminated systems. 

Some fish from Rogers Quarry had deformed bony structures. 'I'hese effects were not 

described in literature on effects of selenium or arsenic; although the age of the fish 

indicated they were exposed in the period of higher concentrations. Bioaccumulation of 

organic: contaminants was not indicated in the McCoy Branch discharge. 

xiv 
The fish community of McCoy Branch was evaluated using qualitative samples above 

Rogers Quarry and quantitative samples below Rogers Quarry at MCK 1.56. 

Electrofishing samples were made in May 1989, October 1989, and May 1990 to provide 

population estimates. Results from the fish assessments indicate that McCoy Branch was 

undcr severe stress. No IisR populations wcre found above the quarry. This suggests past 

ash disposal practices were lethal to fish; current conditions could not be evaluated 

because repopulation of this section of McCoy Branch is prevented by Rogers Quarry. 

The community below Rogers Quarry, although permanent, appears stressed and greatly 

influenced by the proximity to Melton Hill Reservoir, The species composition is not 

typical for a small stream, and those species that Inhabit the stream are generalty more 

tolerant of degraded conditions. Additionally, abnormalities such as deformed heads and 

eroded fins that are typically infrequent in a normal stream population occur in a 

substantial percentage of the sunfish population. These dcformities are the same types 

that were reported by the bioaccumulation studies. 

The structure and composition of the benthic macroinvertebrate community in 

McCoy Branch arc indicative of moderate strcss, Maximum impact within this stream 

occurs upstream of Rogers 

substantial incrcases were 

Ephemeroptera, Plecoptera, and 'I'richoptcra (EPT) richness during the October and 

January sampling periods compared with April and July sampling, which suggests water 

quality improvement, but may also rctlech seasonal impacts. Rogers Quarry acts as a 

settling basin for coal ash and rcduccs the impact of ash osition on the benthic 

community downstream of the quarry. Although Rogers rry appears to reduce these 

impacts, it may also alter the physical and chemical cazviroiiincjnt downstream, which in 

turn alters the invertebrate community. Some improvement in water quality was evident 

downstream of thc quarry, as demonstrated by significantly fiighcr density and biomass at 

MCK 1.40. Howcver, taxonomic richncss, EPT richness, and diversity were significan tly 

lower at this site, cornparcd to the reference site, indicating that the invertebrate 

community was impacted. The benthic community at MCK 1.40 did not exhibit the 

temporal increases in density, biomass, or taxommic and EFT richness shown by 

MCK 2.03, indicating this community is not experiencing similar changes in water quality. 

Thc stress on thc benthic macroiiivcrtehrate community in McCoy Branch appears to be 

habitat alteration as a result of ash deposition within the stream channel and possibly 

leaching of potential toxicants (e.g., arsenic and selenium) from the ash. As stresses to 

McCoy Branch are further reduced or eliminated, a steady recovery of the benthic fauna 

at MCK 2-03 should occur; howevcr, thc rccovcry at MCK 2.03 may be slowed by the loss 

arry as is excrnplified by MCK 2.03. At MCK 2.03, 

wed in density, biomass, taxonomic richness, and 

of supplemental flow to McCoy Branch. 

xv 
Quarterly ambient toxicity tests will continue at MCK 1.60 and MCK 1.92 to monitor 

changes in water quality. Snail release studies are planned to determine whether snails 

can survive and grow in upper McCoy Branch. Largemouth bass from Rogcrs Quarry and 

McCoy Branch embaymcnt will be sampled and analyzed to determine whether metal 

concentrations decrease as expected. A more detailed investigation of bony structure 

deformities will also be conducted. Fish populations will be surveyed at MCK 1-56 twice a 

year, with qualitative surveys conducted annually in upper McCoy Branch. An additional 

reference site will be added for comparison with the fish community data and additional 

qualitative surveys will be made to assess immigration potential. Long-term plans will be 

made to reintroduce fish into upper McCoy Branch. Benthic communities will continue to 

be sampled quarterly at the current sites, and an additional reference site will be added to 

evaluate differences related to the absence or presence of snails. 

xvi 
1. ON 

The 1984 Hazardous and Solid Waste Amendmcnts to the Resource Conservation 

and Recovery Act (RCRA) required assessment of all current and former solid waste 

management units. Such an asscssment car RC Facility Investigation (RFI) was 

required of the Y-12 Plant for their Filled Co h Pond (Murphy 1988). The Filled 

Coal Ash Pond (referred to as thc "ash pond" in this report) was constructed in the 1950s 

on thc upper portion of the McCoy Branch watershed. It received coal ash through a 

pipeline in a slurry from the coal-fired steam plant at Y-12. Because disposal of coal ash 

in the ash pond, and later In McCoy Branch and Rogcrs Quarry, was not consistent with 

the Tennessee Water Quality Act, several rernedi 

Rogers Quarry) were implemented or planned fo 

problems. Thc initial RFI plan examined the as 

disposal concerns. An expanded RR plan was also written to assess remediation in 

McCoy Branch and some downstream components of this waste management unit (e.g., 

Rogers Quarry) (Murphy and bar 1988). 

n steps (e.g., extending pipeline to 

Coy Branch to address disposal 

(Murphy 11988) and associated 

The McCoy Branch RH plan included provisions for biological monitoring of the 

McCoy Branch watershed. The objectives of the biological monitoring were to: 

"( 1) documcnt the degree of ini~r~vcm~nt in biological quality of McCoy Branch after 

completion of thc pipeline and after a18 ash discharges to Rogcrs Quarry are terminated; 

(2) provide guidance on the need for additional re~e~iat~on~ and (3) evaluate the 

effectiveness of the remedial aciions that arc implemented. The data from the biological 

monitoring program will also be sufficicnt to determine if thc classified uses of McCoy 

Branch, as identified in the State of Tennessee Water Quality Management Plan for the 

Clinch River Basin (TDPN 1978), are bcing adequately protccted and maintained" 

(Murphy and Loar 1988). 

The overall strategy for the biological assessment was based on four considerations: 

(1) Because remediation efforts are phased tem~o~al~y, the biological monitoring would 

also bc implemented in stages with increascd monitoring as the system recovered. (2) The 

size of the stream restricted the applica ticsn of assessment techniques to ccrtain areas. 

(3) The fauna of McCoy Branch appearcd dcpauperate; thcrcfore, somc constraints werc 

necessary on the paranieters to be mieasured, and the need was recognized for a limited 

number of reference sitcs. and (4) Because the time framc for rcaching hydrologic 

equilibrium following renxcdiation is unhmw11, the biological monitoring must consider 

changes in hydrologic regime and improvement in water quality (Murphy and bar 1988). 

Therefore, to address these coiisiderations, the biological monitoring applied to McCoy 

Branch consisted of an integrated multitiered program. The program included four 

primary task: (1) toxicity monitoring, (2) bioaccumulation assessments, (3) Gsti community 

assessments, and (4) benthic community assessments. 

The initial results of these four task?; arc prcscnted in this report. Thc results focus 

on the period from 1989 to 1 

presented. 

, hut some previous data from 1974 to 1989 are also 

2 DES ON OF Y BRANCH WATERSHED 

The McCoy Branch watershed is located south of the Y-12 Plant (Fig. 2-1) within the 

Department of Energy’s (DOE) Oak Ridge Reservation (ORR). The ORR is located in 

the Valley and Ridge physiographic province, which is characterized by southwestnortheast oriented, parallel ridges of sandstone, shale, and cherty dolomite, separatcd by 

valleys of less resistant limestone and shale ~~urphy 1938). The watershed drains Fanny’s 

Knob on the southern slope of Chestnut 

Reservoir. Land use in the watershed includes grass covered slopes and fields, selected 

marshy pockets in the floodplain, agricultural buildings, roads, and heavily forested slopes. 

idge and supplics water to Melton Hill 

The eastern branch of McCoy Branch has been extcnsively modified for coal ash 

disposal purposes. (This report will deal only with the eastern branch.) In connection with 

the coal ash disposal, McCoy Branch (Fig. 2-2) has been segmented into four basic areas 

(1) the headwater sections of McCoy Branch and a large coal Wed ash pond created by a 

19-m high carthen dam; (2) a section of free-flowing stream that flows from under the 

dam into Rogers Quarry and that, after rain, is supplemented by flow over the top of the 

dam; (3) Rogers Quarry, a deep, stccp-sided lake; and (4) a section of free-flowing stream 

that flows from Rogers Quarry into ill Reservoir, wit an associated embayment 

area. The western branch of McCoy Branch also enters this cmbayment. 

Thc headwaters of 

discharge (Turner et al, 

Y-12 to the ash pond is located betwccn thesc t 

these three sources combined in the ash pond, 

early years of disposal. The cban 

surface of the ash to the earthen 

reached the dam and were transported downstream via the overflow spillway on the 

eastern sidc of the dam. 

Coy Branch consist of two intcrmittent streams with minimal 

1. A large pipe that was used io transfer coal ash slurry from 

treams. In the past, the flow from 

contains the ash slurry from thc 

B in the pond was shallow and meandered over the 

m. During ash sluicing and high storm runoff, flows 

Water in McCoy Branch below the darn dcrives piimarily from sevcral large springs. 

The spring at the base of the dam is heady vegetated and is fed by groundwater 

discharges. From the darn the stream ilows a ~r~~i~~a~~~y 0.9 km to Rogers Quarry and is 

typically narrow (about 0.5 to 2.0 m in width) nd fast-flowing, consisting of a series of 

runs and riffles. Just above Rogers uarry lies a marshy area with a large spring between 

McCoy Branch (tu the east) and thc municipal sludgc farm to the west. This is whcre 

McCoy Branch flowed bcfore being diverted to fill. Rogers Quarry (Murphy and bar 

1988). 

Rogers Quarry is a 4-hectare lake locatcd about midway in McCoy Branch. It was 

used as a source of stone in thc 194 

in the 1950s (Boglc and Turncr 1989). After Icaving Rogcrs Quarry the stream flows 

through Bethel Valley, to the McCoy Branch Embaymen1 on the Melton Hill Reservoir. 

The stream below the quarry is heavily vegetated and also receives flow from several 

spring-fcd tributaries. 

and was abandoned when it began to fill with water 

2-3 

ORNL DWG 91M-109 

Fig. 2-2. Map of the McCoy Branch showing the primary features and monitoring 

sites. 
2-4 

McCoy Branch is geographically separated from the Y-12 Plant by Chestnut Ridge. 

The distance from the ash slurry pipe on top of the ridge to the discharge into Melton 

Hill Reservoir is approximately 1.5 km. The elevation at the ash slurry pipe at the top of 

the ridgc is about 335 m; elevation at the point whcrc McCoy Branch discharges into 

Melton Hill Reservoir is approximately 244 m. The watershed has a drainage area of 

about 148 hectarcs above Rogers Quarry, 63 ha of which lie above the earthen dam 

located in the headwaters. 

2.1 GEOHYDROIDGY 

McCoy Branch is underfain by the Knox group, a highly crystalline dolomite 

interbedded with shale and qudstone beds, a few veiy thin sandstone beds, aphanitic 

limestone lenses, numerous calcite and quartz filled fractures and cavities, and chert beds 

and nodules (Murphy 1988). Ketelle and Huff (1984) found that water movemcnt in the 

bedrock of the Knox Group on Chestnut Ridge is controlled by the location and 

orientation of the cavities. Primary orientation of cavity systems are controlled by thc 

local bedding Orientation and orientation of penetrative joints and fractures, which are 

widened by dissolution. The actual groundwater flow paths in thc bedrock are expected to 

resemble trellis drainage patterns, flowing parallel to strike and diverted by shorter crossstrike channels to other strike-controlled zones or ernana ted in surface streams. Within 

both the soil and bedrock aquifers, flow is from the higher topographic areas toward the 

lower areas, with gradients indicating flow toward the nearest perennial surface water 

features (Ketelle and Huff 1984; Murphy 19%). 

The major source of water for the upstream reach of McCoy Branch is spring flow 

and precipitation. Craig and Tschantz (1986) estimated the combined base flow of these 

springs to be in the range of 0.42-0.53 million liters per day. For a more comprehensive 

characterization of the geology and hydrology of the ash pond see Murphy (1988), Joncs 

and Mishu (1986), and Turner et a]. (1986). 

2.2 WATER QUALITY 

Water quality of McCoy Branch has been primarily affected by coal ash discharge. 

The ash sluice water was enriched with total suspended solids, sulfates, phosphorous, and 

various metals (Turner et al. 1986). Sluicing of the ash was intermittent, with seasonal 

variation in the amount of ash discharged from about 0.76 million liters per day in summer 

to 3.8 million liters per day in winter (Murphy 1988; Rogle and Turner 1989). 

2.2.1 Description and History of Discharges to McCoy Branch and Rogers Quarry 

Prior to May 19W, the major source of water for McCoy Branch was the coal-ash 

slurry pumped from the, Y-12 Steam Plant. The Steam Plant, built in 1954, has undergone 

several renovations and upgrades including conversion to a baghouse-type fly ash 

collection system in 1985 (Turner et al. 1986). The plant consists of four boiler units that 

used pulverized coal as the sole fuel source from 1954 to 1988. In the winter of 1988, the 

plant was converted to use natural gas as the primary fuel source and coal as a secondary 
source. When burning coal, thc steam plant produces two types of ash. Historically, fly 

ash (dry ash) generated at the Y-12 Steam Plant was removed by a wet collection system, 

and bottom ash (ash collected from the bottom of the boiler in wet form) was removed by 

high pressure water jets. The ash was then sluiced (pumped) in series: first. the fly ash 

and then the bottom ash, as a slurry over the crest of Chestnut Ridge. Gravity flow 

carried the effluent to the ash pond, a broad earthen retention basin of about 8 hectares, 

which provided sedimentation for the ash slurry before discharge into McCoy Branch 

(Turner et al. 1986; M. A. Kane, Y-12 Plant, personal communication). Tfne pond was 

expected to hold 20 years of Y-12 Steam Plant ash, but was filled to within almost 1 m of 

the top of the dam by July 1967 ~~urphy 1988). Subsequently, flow from McCoy Branch 

was used to channel the slurry to Rogers Quarry. Since 1962, Rogers Quarry has been 

used for the disposal of ash slurry from the Y-12 Plant. However, between 1965 and 1981 

the quarry was also used for the disposal of weapons related and classified items (Table 5 

in McCauley 1986; Bogle and Turner 29139). For a wmpkte description of Rogers Quarry 

see Bogle and Turner (1989). In November 1989, ash slurry discharge to the uppcr 

reaches of McCoy Branch was tcrminatcd by cxtending the pipeline directly to Rogers 

Quarry, which has an estimated life expectancy for ash disposal of 65 to 11 5 years 

(Murphy 19%; M. A. Kane, Y-12 Plant, personal communication). 

Discharges into McCoy Branch and uarry are in violation of thc Tennessee 

Water Quality Act. Several interim actions have takcn place, or are anticipated, to assure 

compliance by July 3, 1993, when all discharges to Rogers Quarry must be terminated 

(Murphy and Imir 2988). Four measures were initiated in 19%; to reduce the volume of 

coal ash discharged to Rogcrs Quarry. (1) The "-12 Stearn Plant switched to a higher 

grade of washed coal, increasing efficiency and decreasing the total volume of coal utilized 

in 19%. (2) The Stcam Plant was ccmverted in the winter of 1988 to use natural gas as 

the primaiy fuel type. The targeted yearly ratio of energy derived from gas compared to 

that from coal is approximately 5 to 1, with a highcr percentage of coal being used in 

winter months. (3) A dry vacuum systcm was installed in May 1990 to collect dry fly ash. 

Fly ash is now put in a landfill, and all fly ash sluice watcr discharge to Rogek Quarry has 

been terminated. (4) Present discharges to Rogers Quarry include only bottom ash sluice 

water and steam plant washdown 

bottom ash dewatering system in 

washdown water will be processed through the Stcam Plant's wastewater treatmcnt facility. 

r. The Y-12 Steam Plant is scheduled Lo install a 

at which time bottom ash will be landfilled and 

2.2.2 Characterization of the Cantaminant Source 

In a study by Bulliam (198Sa,b) watcr upstream from Rogers Quarry had higher levels 

or most metals than did water samples taken downstream of Rogers Quarry (Appendix A, 

Table A-1). These data were supprtcd by results in ERDA 1975 (Appendix A, 

Table A-2). In a study by Turner et al. (1986), coal ash sluicc water discharged from thc 

Y-12 Steam Plant was found to contain elevated amounts bf aluminum, barium, boron, 

calcium, iron, magnesium, sodium, arsenic, strontium, potassium, to tal suspended solids, 

total phosphorous, sulfide, and sulfate when cnmparcd to background water 

concentrations (Appendix A, Tables A-3, A-4, A-5, and A-6). Turner et al. (1986) also 

noted that the filled ash pond providcd little or no treatment, did nut remove suspendcd 

solids, and the flow of McCoy Branch was so small that it was incapable OC providing 

appreciable dilution to the ash sluice water. Turner et al. (1986) also compared water 
quality data from Rogers Quarry to data for the effluents from 14 ask ponds associated 

with Tennessee Valley Authority (TVA) coal-fired power plants. The comparison 

revealed that Rogers Quarry effluent was similar to effluent from other ash disposal ponds 

in the Tennessee Valley. Notable differences included higher concentrations of total 

phosphorous and arsenic-,, and lower concentrations of aluniinurn and iron, than in effluent 

from the 'l"V.4 ash ponds. Turner et al. (1 

compounds were below analytical detection limits in all samples. 

) also reported that nearly all organic 

AT part of the recent RFI for McCoy Branch, more surface water quality data were 

taken from McCoy Branch during dry weather (July 30, 1990) and during wet weather 

(after a 4.5-cm rain event) on October 8, 1990 (Appendix A, Tables A-7 to A-13). 

Under both conditions, lower levels of sulfate, selenium, and arsenic were seen in 

comparison with historical wa tea quality data measured when the slurry was being 

discharged to upper McCoy Branch. More substantial decreascs were seen in levels of 

suspended solids and lead, but increased levels of magnesium arid potassium were also 

noted. Values for most volatile and semivolatile organic compounds in surface water 

were below detection limits. 

Water quality data collected from a National Pollutant Discharge Elimination System 

(NPDES) site below Rogers Quarry (Outfall 302) show a decrease in mean weekly levels 

of sulfate, arsenic, and selenium (Table 2-1 and Figures 2-3, 2-4, and 2-5) after the Y-12 

Steam Plant coriverted from coal to natural gas as the primary fuel source (R. R. Turner, 

Environmental Sciences Division, QRNL, personal communication). At the time of 

publication, tlicrc are no water quality data availablc for current ash sluice discharges into 

Rogers Quarry. Recent data collected by the Off-site Environmental Restoration Program 

indicate a peak in arsenic levels below the discharge from Rogers Quarry and exhibit a 

dilution effect downstream in McCoy Branch embaymcnt (Table 2-2). 

2-23 Temprature 

Temperature data for McCoy Branch before December 1989 are limited. Turner et 

al. (1986) reported that ash sluicing did not appear to affect temperatures in McCoy 

Branch, presumably because untreated (except for chlorination) Clinch River watch was 

used for sluicing. Current temperature data show little difference between temperatures 

in McCoy 'Branch above Rogers Quarry, upper White Oak Creek (WOC), arid upper Fifth 

Creek (Table A-14 and Figure 2-6). Mean weekly temperatures in McCoy Branch below 

Rogers Quarry arc similar to rcfcrence streams in winter but up to 10°C higher in 

summer months. Elevated summer temperatures may be explaincd by thermal layering in, 

and epilimnetic discharges from, Rogers Quarry. 

Ash deposits, which occurred when the crcck's flow overtopped its banks, vary greatly 

along the stream. In a preliminary study, Murphy (1988) found that immediately 

downstream of the ash pond darn, the deposits cover the entirc valley through which 

McCoy Branch flows. Further downstream, the deposits are limited to no more than a 

couple of rnetcrs horizontally from the edge of the creek. 
Table 2-1. Mean (standard emr) for selected National Pollutant Discharge Elimination System water quality parameters 

for Outfall 302 for 1986 to 1990 (data for 1990 through week 26)” 

Arsenic 

(mgiL) 

Flow 

(Us) 

Iron 

(m&m 

PH 

(pH units) 

Selenium 

@wv 

(mgiz) 

(mi$? 

Sulfate 

Total Suspended Solids 

p& 

0.21 

(0.007) 

55.2 

(8-5) 

(0.33) 

(OW 

(0.002) 

(12.5) 

0.48 

8.4 

0.019 

90.9 

4.5 

(0.36) 

1987 

0.26 

- 

(0.007) 

(3.7) 

(0.01 j 

as 

38.2 

0.13 

(0.07) 

0.025 

(0.0008) 

75.8 

(1.2) 

4.4 

(0.59) 

- 1988 

0.19 

(0.006) 

33.9 

(3.0) 

0.13 

(0.02) 

8.1 

(0.07) 

0.02 

(0.001) 

(6.3) 

(0.43) 

92.0 

3.6 

- 1989 

0.07 

(0.006) 

(5.3 j 

46.6 

0.14 

(0.04) 

8.3 

(0.07) 

0.006 

(0.W) 

(2.5) 

50.6 

4.4 

(0.78) 

- 1990 

0.04 

(0.003) 

43.1 

(6.1) 

(0.02) 

(0.06) 

(O.oOO2) 

(0.9) 

(0.28) 

0.10 

8.3 

z 0.004 

32.3 

3.3 

?Data are derived from mean weekly values. Source: R. R. Turner, Environmental Sciences Division, ORNL, 

personal communication. 
t 
0.4 

0.3 

0.2 

0.1 

0-0 

ORNL-DWGB1- 17422 

i 

1986 19137 1988 

YEAR 

1989 1990 

Fig- 2-4. Mean weekly values for arsenic in the water from McCoy Branch at Outfall 302, bekrw Rogers Quarry, hm 1986 

to 1990. Source: R. R. Turner, Environmental Sciences Division, Oak Ridge National Laboratory, personal communication. 
3 

0.01 

1 
2-1 1 

Table 2-2. Arsenic levels io McCoy Branch on March 15,lW 

Station Location Total As 

(Pa) 

MCK 1.92 Weir above Rogers Quarry 2.9 

MCK 1.71 Below Rogers Quarry 29.5 

MCK 0.69 Upstream of culvert 5.3 

MCK 0.65 Downstream of culvert 1.2 

MCK 0.30 McCoy Branch Embayment 0.05 

Wata collected by the Off-site Environmental Restoration Program, Clinch River 

Remedial Investigation. Source: James T. Byrd, Skidway Institute of Oceanography, 

Savannah Georgia, personal communication. 
0 

U 

2 

1 

E 

1 

5 
2-13 

Sediment analysis for McCoy Branch from 1974 to 1975 (ERDA 1975) showed 

elevated levels of some metals (Appendix A, Table A-15). In accordance with the RCRA 

Facilities Investigation (RFI), an assessment is being conducted of the impact that coal ash 

deposits may have had in the area immediately adjacent to McCoy Branch (Murphy 1988). 

Phase I of the assessment will be to determine the extent, both horizontal and vertical, of 

coal ash deposits in the McCoy Branch floodplain from the point of discharge at the dam 

to the point of discharge of McCoy Branch into Rogers Quarry. Phase If will include 

sampling the ash and underlying soil to determine the extent contaminants from the coal 

may have migrated into the soil. For a more detailed description of the methodology for 

the sediment analysis see Murphy (1988). Initial analyses of these ash and sediment 

samples collected during 1990 from McCoy Branch show elevated levels of Cd, Mn, Ba, 

Ca, Fe, K, Mg, Na, and Ni (Appendix A, Tables A-16 and A-17) compared to data 

collected in 1974-1985 (Table A-15). The only analyzed elements occasionally falling 

below detection limits were niobium and selenium. Levels of oil and grease were ~0.1% 

for all sediment sites. Lcvels of radioactivity for each site arc given in Appendix A, 

Table A-18. 

Coal ashes typically exhibit leachability of ash constituents. Groundwater may be a 

receptor of contaminants from the coal ash disposal system and may act as a pathway for 

contamination migration near the Y-12 Plant (Murphy 1988). Groundwater sampled in 

October 1987, February 1988, May 1988 (Murphy 1988, Table 7-l), and October 1990 

(Appendix A, Tables A-19 and A-20) showed no evidence of contamination above 

regulatory standards or above expected background. 

3. TOXICITY MONITORING 

Biological tests can be used reliably to detect water quality problems that may not be 

evident with routine chemical analyses. For this reason and because remedial actions are 

driven ultimately by the need to protect living organisms and ecological processes from 

hazardous chemicals, biological tests are gaining acceptance for making regulatory 

decisions about water quality and environmental remediation. 

To obtain data for such decisions, bioassays were used periodically to assas water 

from three sites in McCoy Branch. Four types of biologica! tests were used: (1) a series 

of 7-d tests with fish larvae (the fathead minnow; Pimephalespromelas) and a 

microcrustacean (Ceriodaphnia dubia); (2) a full life-cycle test (LCT) with C. dubia; (3) an 

in situ test with snails (Elimiu sp.); and (4) a 74 laboratory test with Elimia sp. The 

methods used for each of these tests and the sites evaluated with particular tests are 

described in Sect. 3.1. 

3.1 MATERIALS AND ME'"€IODS 

3.1.1 Seven-Day Toxicity Tests 

Seven-day tests with fathcad minnow larvae and Ceriodaphnin are U.S. 

Environmental Protection Agency (EPA) approved, static-renewal bioassays; tests with 

these two organisms arc commonly used to estimate acute and chronic toxicity of 

wastewaters and freshwater receiving systcms (Weber et al. 1989). The fathead minnow 

test estimates toxicity by comparing survival and growth of larval fish in water samples 

being tested with the survival and growth of larvae in control watcr known to be of high 

biological quality. Relative to this control, reductions in fish survival or growth can be 

attributed to the presence of toxicants. The Cetioduphnia test is fundamentally similar lo 

the fathead minnow test but uses survival and fecundity, rather than survival and growth, 

as endpoints. The procedures used to conduct the 7-d minnow and Ceriodaphnia tests of 

water from McCoy Branch are given in Stewart et al. (1990) and Kszos and Stewart 

(1991). 

This report gives thc results of 7-d minnow and Cetiodaphnicr tests for seven test 

periods; the first period started on January 5, 1989, and the last ended on August 6, 1990. 

In the first test period, only Ceriodaphnin was tested. In the remaining six test periods, 

fathcad minnow larvae and Ceriodophnia tests were conducted concurrently. The 7-d 

minnow and Cer-iod~iphnia tests were used to evaluate water from the outfall of Rogers 

Quarry (MCK 1.60), at the quarry's inlct (MCK 1.92), and from a spring near the base of 

the ash pond dam. 

3.1.2 Full Life-Cycle Tests 

The second type of bioassay consisted of Ceriodaphnia full LCTs. LCTs are 

considered to be more sensitive than 7-d tests because they substantiaily extend the 

exposure period, thereby providing more time for the organisms to accumulate and 
3 -2 

respond to materials potentially present in solution. Relative to 7-d tests, Ceridaphnia 

LCTs are not used frequently in water quality assessments. LCTs are substantially more 

intensive and, thus, expensive than the 7-d tests; thcy require 35-40 d for completion and 

need more replicates (e-g., 50 versus 10) for satisfactory statistical analyscs, 

The procedures used in the Ceriodaphnia LCTs were identical to those in the 7-d 

Ceriodaphnia tests, including feeding and daily renewal of test solution. HOW~V~K, the 

LCTs differed from the 7-d tests in three ways: (1) Although water samples were 

collected fresh daily for the 7-d tests, samples for the 1,C”IT”s were collected on Tuesdays 

and Fridays. Between collection events, ECT water samples were stored in a refrigerator 

at 7°C; however, the daily subsamples were warmed to 25 * 1°C before use. (2) LCTs 

evaluated only full-strength water. Thc 7-d tests, in contrast, employed various 

concentrations of McCoy Branch water; typically 100, 80, 60, and 40% of full strength 

(Table 3-1). (3) The LCTs used 50 replicate beakers (1 neonate per beaker) for each 

watcr type, but the 7-d tests used only 10 replicates per concentration. 

An LCT to evaluate water from McCoy Branch at MCK 1.92 was started on July 28, 

1990. Simultaneously, an LCT was initiated to evaluate water quality from East Fork 

Poplar Creek at the outfall of Lake Reality (LR-0). Water from LR-o provided a 

contaminated reference suitable for establishing a contrast with McCoy Branch. ‘4 set of 

SO beakers containing diluted mineral water was included as a negative control for these 

two LCTs. The LCTs continued until September 5, 1990 (a 404 period), when the last 

animal died. 

Analysis of variance (ANOMA) was used to analyze survival and reproduction data 

from the LCTs (SAS 1985a,b). Three sites [McCoy Branch at Rogers Quarry inlet 

(MCK 1.92), East Fork Poplar Creek at LR-0, and controls] yyywere included in the 

analysis. Seven dependent variables were inspected to determine how well their variance 

patterns could be attributed to site. The variables were (1) Ceriodayhnia life span (in 

days); (2) the total number of offspring produced by each animal for all animals that 

produced any offspring; (3) the numbcr of broods produced per female; (4) the mean 

number of offspring per brood (Lee7 brood size); (5) the number of offspring in the largest 

brood of each female; (6) the brood-to-brood variability (expressed as the coefficient of 

variation, CV%) in numbers of offspring produced per female; and (7) mean daily 

fecundity (the total number of offspring produced by a female divided by that female’s 

reproductive life span). Ceriodnplznia dubia neonates are not reproductively active for the 

first 3 d of their life. Thus, a female’s reproductive life span was computed by subtracting 

3 d from her total life span. 

3.1.3 In situ Snail Tats 

Prcvious studies have shown that pleurocerid sriails (cg., Ehia clavaefonnis) tend 

naturally to move upstream and that this behavior can be significantly affccted by the 

presence of contaminants (Burris et al, 15VO). Based on these findings, 150 snails (E. 

clavaefomis) were collected from upper White Oak Creek (WCK 6.3) on July 23, 19%. 

Each animal was marked by placing a dot of fingernail polish on the shell. The animals 

were all of similar size and were acclimated, stepwise, over a 7-d period, from field 

tcmperature (about 17°C) to testing temperature (25°C) before use. The snails were fed 
Table 3-1. Results of 7-6 toxicity tests (fathead minnow larvae and Ceriodaphnia dubia) 

of water from McCoy Branch at MCK 1.92 (inlet to Rogers Quarry)” 

Date Concentration Minnow Minnow Ceriodaphnia Ceriodaphnia 

(%I survival growth survival fecundity 

(%I (mg dry wt/minnow) (W (neona tes/female) 

5 Jan 1989 

6 Apr 1989 

7 Jul1989 

Control 

100 

80 

60 

40 

20 

Control 

100 

80 

60 

40 

Control 

100 

80 

60 

40 

Control 

100 

13 Oct 1989 80 

60 

40 

72.5 * 18.9 

47.5 * 5.0 

52.5 * 9.6 

65.0 * 12.9 

32.5 * 17.1 

100.0 * 0.0 

87.5 * 15.0 

87.5 * 5.0 

85.0 rt30.0 

97.5 * 5.0 

97.5. * 5.0 

97.5 * 5.0 

97.5 * 5.0 

92.5 * 15.0 

77.5 * 26.3 

0.30 * 0.03 

0.48 * 0.05 

0.39 * 0.05 

0.32 * 0.05 

0.53 * 0.24 

0.51 * 0.05 

0.52 * 0.11 

0.51 * 0.04 

0.45 rt: 0.07 

0.45 * 0.03 

0.48 * 0.09 

0.47 * 0.06 

0.59 * 0.07 

0.50 * 0.08 

0.53 * 0.06 

100 

100 

90 

70 

100 

100 

100 

100 

90 

100 

100 

90 

90 

80 

100 

100 

90 

90 

90 

80 

90 

20.2 * 2.6 

13.2 * 6.2 

20.0 * 3.6 

18.3 f 4.0 

17.0 rt 3.6 

20.5 * 5.6 

Y 

‘4 

21.5 * 1.8 

19.2 * 3.2 

22.2 2 2.7 

23.9 * 2.4 

23.2 * 2.6 

24.2 * 2.8 

26.2 * 3.7 

26.0 * 4.0 

28.0 * 2.9 

27.4 * 1.9 

24.7 * 2.2 

23.0 * 1.8 

22.1 * 2.7 

24.4 * 3.0 

24.1 * 3.4 
Date Concentration. 

iw 

Control 

100 

4 Jan 1 80 

60 

40 

5 

Control 

100 

80 

# 

40 

Control 

108 

80 

68 

40 

52.5 1 5.6 

47.5 f 25.0 

65.0 f 25.2 

60.0 rt 28.3 

42.5 f28.7 

90.0 f 10.7 

40.6) s32.7 

30.0 * 14.1 

27.5 2 17.1 

__- 

0.49 -f 0.02 

0.56 rt 0.88 

0.56 f 0.03 

0.50 f 0.10 

0.59 f 0.15 

0.55 I 0.09 

0.47 & 0.10 

0.44 * 0.11 

0.52 * 0.13 

22.5 i 3.7 

26.3 f 2.7 

23.5 d 5.0 

28.8 f 5.2 

25.4 ~t 3.3 

19.7 * 2.3 

22.4 f 5.7 

22.4 f 2.8 

19.9 * 3.8 E ___ 

24.0 * 3.4 

11.1 f 8.1 

11.5 f 9.7 

21.0 f 9.0 

15.6 a 8.6 

Values are means 2 SD for four replicates (minnow test) or ten replicates (Ceridapkirnia) in each test period. 
3-5 

comrncrcial lcttuce leavcs during the: ~~~li~~t~o~ pc 

marked snails wcre rcleased at cach of thrcc sites: 

Quarry (MCK 1-92], McCoy Branch at MCK 1.64) (below Rogers Quarry), and Whitc Qak 

Creek at WCK 6.3. Forty-eight hoi~rs alter the snails had been released, each site was 

surveyed for the snails. The searctmcs were initiated 10 an downstrcarn of the release point 

and continued upstream beyond the release pint for 20 m. The position of each marked 

snail, rclative to the release point, was nieaured to thc ncarest centimeter. A median test 

for multiple samples was used to determine if the median distance the snaiis moved 

upstream differed ammg thc thrce sites (Steel and Torrie 1980). 

A 7d static-renewal test with snails WBS used to determine if the snails' feeding rate 

, and acclimated as described in Sect. 3.1.3. 

was affected by water frcdrn two sitcs in McCoy Branch (MCK 1.92 and MCK 1.60). Snails 

were collected from WCM 6.3 on 

Test chambers consisted of 600-mL beakers.. Each bcakcr containcd 12 snails and 

250 mZ, of watcr; 4 replicate beakers were used for each treatment. Treatments consisted 

of full-strength wt\t~ 'brr~m e~h of fh~~ sitas: McCoy Branch at MCK 1.92, McCoy 

hite Oak Creek at WCK 6.3. Thc 

contents of the beakcrs wcre maintain 

bath. Two ~r~-w~~~~~~,d Ic=tt~~c leafdi 

start of the test. After 24 h and daily thereafter, She remains of the discs were removed, 

new discs were artdcd, and thc water was changed. The remnants of the discs taken lrom 

each beaker wcrc blotted dry with per tow& and weighed to the ncarcst 0.1 mg. The 

diffcrence betwccn initial weight a final weight of the discs in each beaker was used to 

estimate the wct mass of Icttucc leaf eatcn aa'ity by the snails in that rcplicatc. 

the test by a water 

cd to each beaker at the 

iffcrcnccs among feeding rates :mv.mg tseatncnts were analyzed using SAS-CLM 

with a repealed-mcasurcs subroutinc (SA$ 198Sah). 

A majority of water sairiples collected for use in any oE tbc tests described abovc 

were analyzed chemically for p , conductivity, ~~~~~~~~(EPA method 130.1 ), and 

hardness (EPA method 130.2). Thc mcthods use for cadi of these analyscs are 

described by Mszos ct al. (19%). 

During one 7-d tcst period (April 5-1 1. 1 

(NCK 1.92 aid the large spring at the base of 

orthophosphate and sulfate (EPA methods 365.1 and 375.2, respectively). During another 

were analyzed for nilratc, 01 thopho hatc, and sulfiitc. 

two McCoy Branch sites 

) was analyzed for 

7-d pchi~d (J1.d~ 7-13, 1989), SEUTI~~~ COIICC~C~ &illy from McCoy Branch at MCK 1.92 
3.2.1 

The results of the CePdodaphnia and fathead 

McCoy Branch at MCK 1.92 are summarized in ‘I’ 

two species applied to water from McCoy Branch at MCK 1.a and at the spring near the 

base of the dam at the ash pond are summarized in Table 3-2. 

nnow toxicity tests of water fro 

6- 3-1; the results of tests with these 

Overall, the 7-d tests provided little consistent evidence for Pisxicity to either species. 

On three occasions, specific problems with test conditions were suggested. First, in the 

tcst started 011 January 5, 1989, fecundity of Ceridaphnia reared in water from McCoy 

Brarich was unusually low and variable (13.2 + 6.2, mean + SD) relative to controls 

(20.2 f 2-61. The high variability in fecundity for the animals in McCoy Branch water in 

this Lest (C.V. = 47%) is difficult to interpret biologically, Second, thc minnow test 

conducted during April 6-13, 1989, appeared flawed. Survival and growth rates of fish in 

the controls and in McCoy Branch water were both unusually low, suggesting inadequate 

food. Survival and reproduction of Cehduphnia in this test were high both fix controls 

and for water from McCoy Branch. Third, survival (but not growth) of the fish was low in 

McCoy Brznch water in the tests that started on January 4, 1990, and April 5, 1 

3-1). During these two test periods no evidence of toxicity was detected using 

Ceiodaphnkz. Additionally, no conspicuous relationship between fish survival and 

concentration of McCoy Branch water in either of thcse tests (Table 3-1) was detected. 

These considerations suggest that the ‘toxicity’ in McCoy Branch during each of these 

three test periods was probably artifactual. 

, 

3-22 Full-Life @)rck Tests 

Mean values for each of the 7 dependent variables for Cerioduphptin in each of the 

three water types are given in Table 3-3. The ~nean tiumber of broods by Ceiiodaphnira 

tested in McCoy Branch water was lower than that of Cerbdaphnia in the control (10.1 

versus 12.4 offspring per female, Table 3-3). The mean daily fecundity of C~~daphnin in 

McCoy Branch water was also substantially lower than that of controls (5.3 versus 6.1 

offspring per female per day, Table 3-3). The overall difference in total fecundity of 

Cenodaphnia in controls versus McCoy Branch water, though, was not very great (122 

VerSiiS 109.3 offspring per female, Table 3-3) because Ceiiodnphnia in McCoy Branch 

water tended to have slightly larger broods than Cen’oduphnia in the control (10.7 versus 

9.8 offspring per brood, Table 3-3). 

Separate sets of one-way ANOVAs were conducted to contrast reproductive patterns 

of Cei-iodaphnio tested in MCK 1.92 to control water (Table 3-4) and water from EW-O 

(Table 3-5). These analyses showed that the contrast in reproductive patterns of 

Ceriiodaphnia testcd in water from MCK 1.92 versus LR-ca (Table 3-4) was similar in two 

important respects to the contrast between water from MCK 1.92 versus control watcr 

(Table 3-5). First, the number of broods and the mean number of offspring per brood 

tended lo be among the more dynamic parameters in both cnmparisons, based on the 

magnitude of change in p (about 123-fold for the number of broods and 8.6-fo1d foe the 

number of offspring per brood, Tables 3-4 and 3-5). The number of broods and the mean 
Table 3-2 Rsu1t.s of 7-6 toxicity tests (fathead minnow larvae and Cet.iodaphnia) of water from McCoy Branch at the spring 

near the base oE the ash pond dam (spring) and from McCoy Branch below Rogers Quarry (MCK 1-60)” 

Site Dateb Concentration Minnow Minnow Ceriodaphnia Ceridaphnia 

(%I survival growthc survival feeunditf 

P> mg dry wt/minnow (W 

90.0 0.55 * 0.09 100 19.7 * 2.3 

100 77.5 0.57 * 0.09 80 25.6 ~f: 2.7 

80 825 0.59 f 0.03 90 25.9 f 2.5 

Spring 5 Apr 1990 Control 

MCK 1.60 30 July 1990 Control 100.0 0.53 *om 90 24.0 * 3.4 

100 100.0 0.64 * 0.04 90 18.3 * 10.8 

80 97.5 0.60 *0.11 --- --- .b.3 

“Values are mean * SI). 

’When each 7-d test was started. 

Tomputed as increase in weight. 

dCeriodq$min fecundity is computed using females that survived all 7 d, and their young. 
3-8 

Parameter Control LR-0 MCK 1.92 

Lifc span (days) 

Number of broods 

No. of offspringbrood 

Total No. of offspring 

Largest brood 

Variability in fecundity 

Daily fecundity 

23.1 25.6 24.3 

12.4 9.7 10.1 

9.8 12.0 10.7 

122.0 114.7 109-3 

17.8 19.7 18.5 

56.7 51.8 56.2 

6.1 5.5 5.3 

Dependent variable Model Error 

DF DF w2 E; P 

Lifc span 

Number of broods 

No. of offspringibrood 

Total No. offspring 

Largest brood 

Variability in fecundity 

Daily fecundity 

1 98 0.0055 0.54 0.4634 

1 96 0.0809 8.45 0.0045 

1 96 0.0257 2.54 0.1 146 

1 96 0.0173 1.69 0.1967 

1 96 0.0101 0.98 0.3240 

1 95 0.0199 1.93 0.1685 

1 97 0.0394 3.98 0.0489 

Thc probability (p) that the difference between means of paramcters for controls versus 

McCoy Branch was due to chance alone is given for each parameter; the p values were 

obtained by onc-way analysis of variance tests. K2 is the proportion of the total variation that 

can be explained by the difference in water iype. 
3-9 

Table 3-5. Analysis of variance results for cc?Jiodaphrua e life-cycle tests of water from 

Lake Reality outfall and McCoy Branch at MCK 1.92 

Dependent Variable Model Error 

DF DF R2 F P 

Life span 1 98 0.0070 0.69 0.4068 

Number of broods 1 97 0.0036 0.35 0.5553 

No. of offspringhrood 1 97 0.0615 6.35 0.0133 

Total No. offspring 1 97 0.0054 0.52 0.4715 

Largest brood 1 97 0.0351 3.53 0.0634 

Variability in fecundity 1 96 0.0203 1-99 0.1620 

Daily fecundity 1 97 0.0023 0.22 0.6366 

The probability @) that the difference between means of parameters €or Lake Reality 

outfall water versus McCoy Branch water was due to chance alone is given for each 

parameter; thc p values were obtained by one-way analysis of variance tests. R2 is the 

proportion of the total variation that can be explained by the difference in water type. 
3-10 

number of offspring per brood were inversely related as well, whcreas, lifespan was more 

constant (cf Tablc 3-3). These points suggest that these daphnids are flexible 

reproductively, in that they "trade off' brood size and number per brood, This in turn 

suggests that reproduction is a major energetic expense to these animals, which supports 

the idea that Ceriodnphnia reproduction (over a fured number of broods) should be a 

scnsitivc endpoint for toxicity assessments. It also suggests the hypothesis that 

reproduction may control longevity of these animals in predator-€ree situations. The 

second, and perhaps more important finding from the two sets of ANQVAs, was that the 

different water types did not affect any of the reproductive parameters very strongly: the 

proportion of variance in any parameter that could be explained by differences in water 

type never exceeded 8.1% (Tables 3-4 and 3-5). This consideration, in conjunction with 

the tendency for the animals to trade off brood size and nun-nbct per brood, indicate that 

water from MCK 1.92 was not toxic. It also strongly suggests that food-related aspects of 

testing ambient waters with Ceriodaphnia may need to be addressed more carefully, both 

in effluent and ambient testing situations. 

3-23 kt Situ Snail Test 

Snail movement patterns differed significantly among the threc sites (G = 22.95, 

p < 0.001). Fcwer than 25% of the snails released at MCK 1.60 moved upstream, 

whercas, >'E% moved upstream at MCK 1.92 and WCK 6.3 (Fig. 3-1). In 48 h, the 

maximum downstream movcment of the snails at MCK 1.60, MCK 1.92, and WCK 6.3 was 

2.80, 0.60, and 1.88 n. respectively. Median distances that snails moved upstream did not 

appear to differ between MCK 1.92 and WCK 6.3 (G = 4.045, 0.05 > p > 0.020), but did 

differ between MCK 1.60 and MCK 1.92 ((3 -- 22.132, p < 0.001), and between WCK 63 

and MCK 1.60 (G = 13.718,~ < 0.001). Beeausc of multiple testing, a conservative Type 

I error rate (0.020) was used. More than 58% of the marked snails were recovered at 

each of thc McCoy Branch sites; 27% of the snails that had been marked and released 

were recovered from WCK 6.3. 

The feeding rates of the snails in water from WCM 5.3 and McCoy Branch at 

MCK 1.92 were quite similna (56.3 + 5.3 and 54.3 f 6.4 mg wet mass consumed per day, 

respectively; means f standard error); snails in water from MCK 1-60, in contrast, had 

feeding rates that were about 25% lower than those tested in water from the other two 

sites (Le., 40.9 I 5.3 rng wet mass per day). The feeding rates did not, however, differ 

statistically based on ANOVA 0, = 0.215). Feeding rates differed among dates (ANOVA, 

p = O.OOOl), and the rates increased uniformly towards the en3 of the experiment. The 

feeding rates showed no signilkant site X date interaction (ANOVA, p = 0.3222). 

Daily analyses of pM, conductivity, alkalinity and hardness were. conducted for six of 

the 7-d toxicity testing periods (Table 3-6). Conccntrations of nitrate, phosphate, and 

sulfate were measured in water from McCoy Brarnch at MCM 1.92 during two of the 7-d 

test periods (Tablc 3-7). During April 5-11, 1 , the phosphate levels at the upstream 
ORNL-DWG 91 -1 01 55 

100 

75 

50 

25 

0 

AB A' m0 

r I 

I /= 

/ 

/ I A 

e 

I 

I 

MCK 

MCK 

WCK 

2 

1.60 

1.92 

6.3 

-3 -2 -1 0 1 2 3 4 5 6 7 

DISTANCE UPSTREAM (m) 

Fig. 3-1. Plot showing the number of snails reoovered (cumulative percent) versus distance from the point of retcaSe for two 

sites in McCoy Branch and a nomn&ated site in White Oak Creek (MCK = McCoy Branch kilometer and WCK = White 

Oak Creek kilometer.) 
21-E 
TabIe 3-7. Means (* SD) of nitrate, phosphate, and sulfate croncentrations in daily grab samples (7d period) of water from 

McCoy Branch at MCK 1.92 and the spring near the base of the ash pond dam 

Test Dates Nitrate 

(ma) 

Phosphate 

(d) 

Sulfate 

(mg/L) 

~~~~ 

MCK 1.92 

MCK 1.92 

Spring 

~~ ~ ~~ ~ ~~ 

July 7-13, 1959 0.364 * 0.055 

April 5-11. 1990 NAa 

April 5-11, 1990 NA" 

~ 

6.1 * 1.6 

8.3 f 1.6 

13.6 * 3.0 

27.9 * 10.2 

40.9 * 9.2 

19.7 2.9 

"NA = not analyzed. 

P 

CI 

W 
3-14 

spring site were higher than those at MCK 1.92, whereas, the sulfate values were lower 

(Table 3-7). 

Water saniples during July 3Q-August 5, 1W, from McCmy Branch at MCK 1.60 

were analyzed for pH, conductivity, alkalinity an hardness. During April 5-11, 1990, 

samples from the spring at the base of the ash pond were also analyzed for these 

parameters. The results of these ~WO sets of analyses arc summarized in Table 3-8. 

The resrnlts of the biological tests of water from McCoy Branch reported here did not 

show much cvidence for toxic conditions in this stream. In 7-d laboratory tests, survival 

and growth of fathead minnow larvae, and survival and Eeeundity of C~idaphnia was 

generally high, although a few exceptions to this trend were evident. Similarly, full LCTs 

with Cetiodnphnin, which should he considerably more sensitive than 7-d tests, also failed 

to show much effect of McCoy Branch water. LcJps also showed Ceriodaphnin had 

significantly fewer broods and a slightly loaves mean daily fecundity in McCoy Branch 

water than they did in the controls, but the number of neonates per brood tendcd to be 

greater than that in controls. Thus, the net effect of McCey Branch water on 

Ceriodaplinin fecundity was sinall. Longevity of Ceriodaphnia in McCoy Branch water was 

also very similar to that for the controls (24.3 d for animals in McCoy Branch water versus 

23.1 d for controls. Table 3-3). 

In the in situ tests, snails apparently experienced more stress in McCoy Branch at 

MCK 1.60 than they did at either MCK 1.92 or at WCK 63. ,4t MCK 1-60, the net 

movement of snails was downstream; whereas, the net movement of the snails at the other 

twc sites was upstrcam. Studies of snails in noncontaminated streams have indicated that 

an upstream msvcnient of snails is typical (Crutchfield 19%; Iloup 1970; Burris et al. 

1990). Conversely, when healthy snails were placed in contaminated streams, thc nct 

movement was downstream (Burris et al. 1990). Snails may actively move downstrcam as 

an escape behavior or may be passively transported downstream by ilow. 

In 7-d laboratory tests, snails consumed less food when tested in water from McCoy 

Branch at MCK 1.60 than thcy did in water from either MCK 9.92 or WCK 4.3, but this 

diffcrcncc was not statistically significant. 

During the surnmer, the. water in McCoy Branch at MCK 1.m is warmer than that at 

MCK 1.92 or WCM 6.3 (see Table A-S), primarily because MCK 1.60 receives epilimnetic 

flow Irom the quarry. Bccausc Elimia are not very heat tolerant (Ross and Ultscla ISSO), 

warmer temperature could account for the difkrences in sirail behavior between 

MCR 1.60, and MCK 1.92 and WCK 6.3. However, heat stress is unlikely to account for 

differences seen in the laboratory where tcmperature was controlled. 

The mean ratio of alkalinity to hardness (AM) for MCK 1.92 was 0.811, and the 

mean conductivity was 284 pV.m (Table 3-5). 'I'he A:H and conductivity values for 

hlCK 1.92 are within the 95% coiifidence bounds for those rcported for reference sites in 

upper WOC, First Creek, arid Fifth Creek (Stewart 1WO). Similarly, the AH for samples 
3-15 

Table 3-8. Means (* SD) of pH, amductivity, alkdinity, and hardness for daily grab 

samples (74 periods) of water fbm McCay Branch at MCK 1-60 (July 30-August 5, 

1990) and the spring at the base of the ash pond dam (April 5-11,1990) 

Factor MCK 1-60 Spring 

PH 

(standard units) 

Alkalinity 

(mg/L) 

8.5 i 0.1 

233k 4 

83* 2 

125* 6 

7.5 f 0.2 

351 i 54 

151 f 20 

174* 11 
3-14 

from MCK 1.60 was 0.664; whereas, AH for the spring at the base of the ash pond dam 

was 0.868 (Table 3-8). TIPUS, as for other streams, the overall trend was for a decline in 

A:M with distance downstream, but thc rate and total extent of decline was not very great. 

Phosphate, which tends to be biologically quite reactive, was also present at relatively ~QW 

concentrations in water from the spring at the base of the ash pond dam and from 

MCK 1.92 (Table 3-7). 9Xs element is often elevated by a factor of 10 to 100 in streams 

that receive industrial effluents. Thus, the results of the chemical analyses suggest that 

the stream is not highly perturbed. This conclusion is in good general agrcerncnt with the 

results of toxicity tests. 

3.4 mrCmE STrnFS 

MCK 1.60 and MCK 1.92 to monitor possible changes in water quality that occur in 

McCoy Branch. Snail release studies will also be continued to determine if these grazers 

can persist and grow if transferred into McCoy Branch sites upstream from Rogers 

Quarterly tests with Cere'odaphnia and fathead minnow larvae will be conducted at 

Quiarry. 
4. BIOACcuMuLAnoN STUDEB 

4.1 TNTRODUCITON 

McCoy Branch received discharges of coal ash effluents From Y-12 (Sect. 2.2.1). 

Metals and hydrophobic organic chemicals in these discharges (Sect. 2.2) may accumulate 

in the biota of McCoy Branch, Rogers Quarry, or downstream in Melton Hill Reservoir to 

levels that may diminish the value of these resources. The primary objectives of 

contaminant monitoring in McCoy Branch biota were to (1) identify any substances that 

accumulate to levels exceeding those observed in biota from nearby, uncontaminated 

reference streams and (2) evaluate the extent and significance of contamination by those 

substances in McCoy Branch and downstream aquatic systems. Secondary objectives were 

to assist in locating sources of contaminants that accumulate to unacceptable levels, and to 

evaluate the relative importance of present vs. past discharges in determining contaminant 

levels of biota. 

Initial surveys of McCoy Branch indicated that only a limited area of the stream 

contained enough fish to sample for bioaccumuiation potential in aquatic biota, and this 

area was open to immigration from Melton Hill Reservoir. 3ecause Rogers Quarry 

contained suitable fish populations that are virtually isolated from immigration from 

Melton Hill Reservoir, the collections were made from this site to evaluate 

bioaccumulation concerns associated with the coal ash discharge. McCoy Branch 

embayment of Melton Hill Reservoir was sampled to provide a basis for evaluating if fish 

from the quarry contained elevated concentrations of certain contaminants, and also to 

ensure that no public health concerns were associated with the ultimate discharge of 

McCoy Branch water to that portion of the reservoir. 

4-2 h4ETHODS 

Largemouth bass (Micropterns salmoides) were collected from Rogers Quarry and the 

adjacent McCoy Branch embayment of Melton Hill Reservoir in July 1990 by angling and 

electrofishing. The fish were placed on ice and returned to the laboratory where they 

were weighed and measured. The bass wcre filleted and skinned, and samplcs of the 

anterior dorsal portion of the fillet was removed for analysis for mercury, arsenic, 

selenium, other trace metals, chlorinated organic pesticides, and PCBs at the ORNL 

Analytical Chemistry Division (ACD). Mercury was analyzed by cold vapor atomic 

absorption spectrophotometry after digestion in a mixture of perchloric and nitric acids 

(EPA Methods 3050 and 245.5 for preparation and analysis, respectively, EPA 1986). 

Following digcstion in nitric acid, arsenic, beryllium, and uranium wcre analyzed by 

inductively coupled plasma mass spectrometry; and antimony, cadmium, chromium, copper, 

lead, nickel, selenium, silver, thallium, and zinc were analyzed by inductively coupled 

plasma optical emission Spectrometry (EPA Methods 3050 and 6010, EPA 1986). A 10-g 

sample of the fish fillet was extracted by ultrasonic disruption in methylene chloride, 

cleaned up by column chromatography, and analyzed for PCBs and chlorinated pesticides 

by gas chromatography with electron capture detection (EPA method 8080, EPA 1986). 
4-2 

Quality assurance (QA) was maintained using a combination of (1) blin 

analyses; (2) split sample analyses between the EPA Environmental Sehviees Laboratory, 

Athens, Georgia, and the ACD Laboratory; and (3) the analyses of biological reference 

standards and uncontaminated fish. Recoveries of PCBs, selected metals, and organics 

were verified by spiking uncontaminated fish with known amounts and atialyzing them. 

Statistical evaluation of the data was conducted ming linear regression, analysis of 

variance (ANOVA), hvenes test for homogenei 

(SAS 1985a,b). All comparisons used alpha -- 0.05. 

of variances, and analysis of covariance 

Concentratioirs of elements in individual largemouth bass from Rogers Quarry and 

McCoy Branch embaynrent are listed in Tablc 4-1. Mean concentrations of most metals 

(antimony, beryllium, cadmium, chromium, copper, lead, mercury, nickel, silver, uranium, 

and zinc) in bass from Rogers Quarry. and McCoy Branch embayment were similar to 

concentrations in reference stream sunfish (Table 4-2). The concentrations in McCoy 

Branch bass were also similar to those found in various species from other sites both 

locally and nationwide (WA 1985; Dycus and Hickman 19%; Dycus 1989; bwe et 

al. 1985). The mean concentrations of elements were all below concentrations used by 

EPA (EPA, personal communication) and others (Hoffman et al. 1984; @. C. Travis, 

Health and Sa€ety Division, ORNL, personal communication) to screen for levels of 

contamination that pose no threat for human consumption (Table 4-2). Only arsenic was 

present at concentrations above screening criteria; however. the screening concentration 

for arsenic is below the detection limit fnr arsenic in fish, and also well below 

coilcentrations typical of most biological materials (Bowen 1979). 

Thallium was dctected in seven of eight bass from Rogers Quarry, but not in fish 

from McCoy Branch embayment. However, the concentrations were at or near the 

analytical detection limit and, therefore, must be regarded cautiously. hlthough data 

suggest that thallium may be elevated above background levels in Rogers Quarry, 

evaluation with nicsre sensitive analytical methods is needed for verification. 

Cormmtrations of two elements, selenium and arsenic, in bass from Rogers Quarry 

were significantly (ANOVA) elevated above concentrations in bass from McCoy Branch 

einbayment (Tablc 4-2). The mean concentration of arsenic in bass Crom the quarry was 

0.29 I 0.02 pg/g, about twice the amount (0.14 * 0.02 pdg) found in fish from the 

reservoir. Selenium was also substantially higher in the bass from Rogers Quarry, 

averaging 3.00 

in bass from the quarry; however, concentrations were too near the detection limit to 

regard this result as conclusive. Mercury concentrations in fish from the quarry were 

among the lowest observed in largemouth bass in the United States and substantially lower 

than concentrations in fish from Melton Hill Reservoir. 

0.11 pg/g versus 1.00 + 0.29 pdg. Thallium also appeared to be elevated 

The mean concentrations of arsenic in the bass from McCoy Branch embayment may 

bc elevated above typica! background levels. Arsenic has never been found to exceed the 

detection limit (0.05 p,dg) in sunfish analyzed for biological monitoring programs at 
ROGQUA 

ROGQUA 

ROGQUA 

KOGQUA 

ROGQUA 

ROGQUA 

ROGQUA 

ROGQUA 

ROGQUA 

MCYBRU 

MCYBRD 

MCYBRD 

MCYBRD 

MCYBRD 

MCYBRD 

MCYBRD 

MCYBRD 

MCYBRD 

LMBASS 

LMBASS 

LMRASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMBASS 

LMRASS 

5578 

5879 

5494 

5495 

5496 

5497 

5498 

5499 

878Sd 

5477 

5478 

5479 

5480 

5481 

5484 

5455 

084SC 

5482 

M 

F 

M 

F 

F 

M 

M 

F 

467 

299 

217 

515 

180 

193 

315 

194 

BO8 

292 

135 

582 

452 

328 

547 

303 

51.4 

29.1 

26.2 

32.2 

24.2 

25.0 

29.2 

25.3 

0.30 

0.26 

0.24 

0.24 

0.27 

0.24 

0.37 

0.36 

0.34 

41.0 0.09 

31.4 0.11 

22.4 0.23 

36.4 0.09 

32.6 0.13 

30.5 0.14 

36.4 0.19 

30.3 0.15 

0.09 

<0.003 

10.003 

c0.003 

C 0.003 

<O.DoJ 

0.004 

C0.003 

<0.003 

c 0.003 

c0.003 

<0.003 

~0.003 

< 0.003 

<0.003 

<0.003 

c 0.003 

0.007 

0.003 

3.2 

2.9 

3.3 

2.4 

3.3 

3.1 

3.0 

2.7 

3.6 

0.03 

0.02 

0.03 

CO.02 

0.03 

0.03 

0.03 

0.03 

0.03 

3.0 CO.02 

1.0 c0.02 

0.54 c0.02 

0.65 c0.m 

0.54 e0.02 

0.64 < 0.02 

0.77 < 0.02 

0.83 e0.02 

0.72 <0.02 

0.005 

<0.003 

< 0.003 

<OM3 

c0.003 

e0.003 

< 0.003 

< 0.003 

<OB03 

<0.003 

< 0.003 

~0.003 

e0.003 

<0.003 

<OB03 

< 0.003 

c0.003 

C0.003 

4.8 0.024 

5.2 0.011 

5.4 0.010 

5.0 0.027 

6.1 0.010 

6.0 0.009 

5.7 0.010 

6.7 0.008 

4.8 0.028 

5 .O 

7.7 

6.1 

6.5 

6.8 

4.8 

5.8 

6.9 

6.1 

0.069 

0.079 

0.027 

0.058 '4 

0.083 

0.109 

0.038 

0.134 

0.118 e 

HINDSCR BLUGIL 5464 F 81.2 16.8 C0.05 0.004 4.43 e0.02 CO.003 63 0.054 

HINDSCR REDBRE 5469 M 82.5 16.6 <0.05 0.005 <0.46 < 0.02 c0.003 4.8 0.075 

llle following metals were below the respective limits of detection: Ag, e0.18; a, eO.18; Cr, ~0.44; Cu, <0.44; Ni, CO.41; Pb, ~0.44; Sb, <0.44. 

bROGQUA = Rogers Quarry, MCYBRU = McCoy Branch embayment upstream from culvert at Bull Bluff Road, MCYBRD = McCoy Branch embayment downstream from 

ZMBNS = largemouth bass (Microptencs sulmoik) BLUGIL = bluegill sunfish (kpmis mucrrohirus) REDBRE = redbreast sunfish (f..epm& awincS). 

dDuplicate for 5878. 

auplicate Cor 5480. 

culven at Bull Bluff Road, HINDSCR = Hinds Creek, Anderson Co., TN. 
4-4 

Rogers McCoy Branch Hinds 

Metal ~~arayb Embaymentb CreeV IVk usmsc PGVf EPM 

~.. 

Antimony 

Arsenic 

Rcrjillium 

Cadmium 

Chromium 

(=opp"i 

Lead 

Mercury 

Nickel. 

Selenium 

Silver 

'Thalliuiii 

Uranium 

Zinc 

<0.44 

0.29 

(0.02) 

<0.003 

CO.18 

<0.44 

<0.44 

<0.44 

0.014 

(0.002) 

<0.44 

3.00 

(0.11) 

<0.18 

0.03 

(0.00) 

~0.003 

5.6 

(0.22) 

<0.44 

0.14 

(0.02) 

<0.003 

~0.18 

q0.44 

~0.44 

<0.44 

0.073 

(0.011) 

<0.44 

1 .00 

(0.29) 

<0.18 

<0.02 

< 0.003 

6.2 

(0.35) 

<0.44 

q0.05 

0.005 

(0.005) 

<0.18 

e 0.44 

<0.44 

<O.M 

0.065 

(0.011) 

<0.44 

c0.45 

<0.18 

<0.02 

<0.003 

5.6 

(0.80) 

c2 

0.14 

<0.02 

0.02 

0.82 

1.2 

0.06 

0.30 

<l.O 

0.28 

< 0.2 

<1 

___ 

9.2 

--- 

0.16 

-__ 

0.04 

___ 

0.86 

0.19 

0.11 

.._ 

0.46 

___ 

.__ 

_-_ 

25.6 

5.2 

0.0007 

0.004 

1 .o 

1.8 

36 

1.8 

0.42 

5.2 

12 

0.29 

0.66 

1.6 ' 

180 

43.1 

0.0062 

0.0025 

10.8 

10800 

--- 

.-. 

1 .o 

215 

5.4 

2.48 

5.71 

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

Tabular values for these sites are mean and SE (in parentheses). Additional data are refeience concentrations from 

other studies ('Tennessee Valley Authority, United States Fish and Wildlife Seavice) and risk hascd criteria (Preliminary 

Guidance Value, Environmental Protection Agency). 

bN = 8. 

'N := 2. 

'kompositc largemouth bass, N = 10 (Dyciis 1989 Uycus and Hickman 1986). 

?~we et al. 1985. 

fPieliminary Guidancc Values (Hoffman et al. 1984; C. C. Travis, Health and Safety Division, ORNL, personal 

Environmental Protection Agency, pe'sonal communication. 

comuiunication). 
4-5 

ORNL, Y-12, and K-25 (Southworth 1999; @. R. Southworth, Environmental Sciences 

Division, ORNL, pcrsonal communication); however, all the largemouth bass collected 

from McCoy Branch embaymcnt contained measurable arsenic concentrations (Table 4-1). 

The mean concentration of arsenic found in McCoy Branch embayment bass was similar 

to the nationwide mean concentra Lion found in the National Cantaminant Biomonitoring 

Program (Lawe et al. 1985) sampling various species (Table 4-2). The McCoy Branch 

mean was also similar to the mean concentration found in composite largcmouth bass 

samples from sewn sites in the TVA region (Table 4-2) in screening studies conducted by 

TVA (Dycus and Hickman 1%; Dycus 1989). The criterion wed to indicate a need For 

follow-up sampling in the TVA screening studies is 0.5 &g for arsenic. 

The mean selenium concentration in bass from McCoy Branch embayment exceeded 

the mean concentrations observed in both the National Contaminant Biomonitoring 

Program (hwe et al. 1985) and the TVA investigations (Dyeus and Hickman 1986; Dycus 

1989) (Table 4-2). Typical concentrations observed in sunfBh in thc ORR Biological 

Monitoring Programs were 0.4 to 0.6 pg/g (Southworth 1991; 6. R. Southworth, 

Environmental Sciences Division, ORNL, personal communication). Thus, selenium 

concentrations in bass from McCoy Branch embayment are clearly clevated. Although 

they are well below concentrations used to screen for human health concerns in fish 

consumers (Table 4-2), the mean concentration is equal to the criteria used by TVA to 

initiate follow up studies (Dycus 1989). 

The presence of elevated concentrations or selenium and arsenic in fish from Rogers 

Quarry was not surprising, because surface water in McCoy Branch contained high 

concentrations of these substances for several years prior to the reduction of coal burned 

at the Y-12 Steam Plant in 1988 and subsequent elimination of fly ash discharges to 

Rogers Quarry in 1990 (Fig. 2-5). Average concentrations of these elements measured by 

NPDES monitoring in McCoy Branch were much lowcr, averaging 46 pg/L arsenic and 

4.3 &L selenium in the year preceding the fish sampling (Sect. 2.2.2, Figs. 2-4 and 2-5). 

Several recent studies have suggested that adding selcnium to waters in which 

mercury bioaccumulation in fish is excessive could amcliorate the problem (Rudd et 

al. 1980, Turner and Rudd 1983, Turner and Swick 1983, Bjornberg et al. 1988). 

However, a recent study by Curvin and Furness (1988) found that simultaneous exposure 

of minnows to dissolved mercury and seknium resulted in more rapid accumulation of 

mercury than was observed in the absence of selenium. Thcy also note the positivc 

corrclation be tween tissue concentrations of mercury and selenium in large oceanic fish. 

The mean mercury concentration in largemouth bass from Rogers Quarry, 

0.014 * 0.002 &g, was much lower lhan that in fish from the adjacent reservoir, 

0.073 i 0.011 &g (Table 4-2). A positivc correlation betwcen fish size and mercury 

concentration is commonly found in fish from the same site, which complicates 

comparisons of mercury concentrations among fish from difFerent sites, because the mean 

weight of the fish sampled from Rogers Quarry was smaller than that of fish from McCoy 

Branch embayment. In this case, fish from Rogers Quarry exhibited a statistically 

significant relationship between fish weight and mercury concentration: 
4-6 

[Hg] = 5.48 x (w@) - 0.002 (4-1) 

A similar relationship was found in the McCoy Branch ernbaymerit fish, but the slope of 

the relationship did not differ significantly from zero: 

[Hg] = 8.11 x (wg) 1- 0.038 (4-2) 

Because slopes of the two relationships did not differ significantly from each other, 

mercury concentiations could be compared in a straightforward fashion using analysis of 

covarimce. The results of such a comparison in icaaed that the di€fcrem@s: in mercury 

concentrations in fish between the two sites was indeed statistically significant. If Eq. 1 is 

used to estimate the mercury concentration in Rogers Quarry fish of mean weight (430 g> 

equal to the mean weight in the Melton Hill Reseavoir collection, the difference remains 

very large, 0.025 versus 0.073 ,ug/g. 

Mercury conceritrations in largemouth bass from Rogers Quarry are among the 

lowest reported for this species. Concentrations measured by TVA in bass from 11 other 

sites in the upper Tennessee Valley all equaled or exceeded 0.2 pg/g (Dycus and Hickman 

1986; Qcus 1989). The lowest mean concentrations observed in an extensive survey 

(95 sites) of lakcs and streams in Florida were 0.04 and 0.07 &g in two highly eutrophic 

lakes (Hand and Friedman 1990). Concentrations at other locations typically excceded 

0.2 pg/g in that study, with most exceeding 0.5 pg/g. Only one of 39 composite 

largemouth bass samples analyzed in the National Contaminant Riomonitoring Program, 

1978-1981, contained 0.02 ,ug/g or less of mercury (Lowe et al. 1985). 

Although mercury conccgntrations in fish from Rogers Quarry were far lower than 

those typically found in largemouth bass, similar concentrations have been observed 

previously in bass from Melton Hill Reservoir. Largemouth bass collected in 1975 

averaged 0.02 pg/L (Elwood 1984). Monitoring conducted from 1979 to 1983 by ORNL 

found mercury concentrations in single composite samples of largemouth bass to range 

from 0.01 to 0.10 pgJg, averaging 0.05 pglg (Martin Marietta Energy Systems 1985). 

Analyses of individual fish were conducted in 1984 and 1985, and reported mean 

concentrations of 0.02 and 0.05 pg/g9 respectively (Martin Marietta Energy Systems 1986). 

Sampling by TVA in 1984 reported a mean conccntration of 0.12 pg/g for 10 fish (TVA 

1985). Bass collected in fall 1989 from two sites on Melton Mill Reservoir averaged 0.10 

fig/g (n = 8) (S. M. Adam, Environmental Sciences Division, ORNL, personal 

communication). ‘Ihus, it appears that mercuiy concentrations measured in bass from 

Melton Mill Reservoir in the past have been quite low and not unlike those observcd in 

fish from Rogers Quarry. However, it also appcars that measurements of mercury in 

Melton Hill Reservoir bass made since 1984 indicate that concentrations much higher than 

those observed in fish from Rogers Quarry are now typical gf this lake. 

The fact that very low concentrations of mercury have been observed in Melton Hill 

Reservoir fish in the past suggest that the low concentrations found in? Rogers Quarry fish 

may result not from the presence of elevated concentrations of selenium in water and 

biota, but rather from unusually low concentrations of mercury in the water or some other 

factor limiting the production of methylmercury in this system. While it is impossible to 

disprove this hypothesis with the limited monitoring data presented here, NPDES 
4-7 

monitoring of aqueous mercury co~~~~~~at~~~~~ in Branch suggest that this stream 

has occasionally contained elevated niercury conc ns in the past (Rogers et al. 1988, 

1989). Thus, it is unlikcly that the low ~~n~n~ra~~~n~ of mercury in Rogers Quarry fish 

are a result of unusually low concentrations of mercury in the quarry water, and it is likeIy 

that the quarry actually contains higher cmccntr f mercury than unmntaminated 

natural waters. It appears that the presence of selenium En Wlltcr jn Rogers 

Quarry reduced the natural ~cc~~u~a~~~~ sa1bstantiaP ami~unt, in 

agreement with speculation of Turner and 

The measurements of ~~~~~~u~ and ascnic c~~~~~~~~~~o~iin fish and water from 

Roger Quarry can also be used to calculate ~~o~~~~c~~~r~t~~n factors for these two 

elements. Although a simple ratio cannot ade ately describe or predict bi~~~~u~ul~tio~ 

of inorganic substances such as these because 

homeostatically regulated in fish, (2) may not exhibit a linear relationship between 

aqueous phasc and biotic concentrations, and (3) may bc accumulated significantly via 

food as well as direct aqueous uptake; ~~~ert~e~~ss, such ratios can be useful in 

extrapolating to similar circumstances and pcrhaps in providing additional indices for 

evaluating the potential of ~~~~rni~ant~ to ~~~~~~c~~~la~~Bioconcentration factors were 

calculated for thesc two compounds by di 

quarry by the mean aqueous phase coface 

prceeding year. Results of this calculatio ~i~~~~~~~~~factors for selenium 

and arsenic oC 940 and 6.3, respectively. aris~j~, ~~~~~~~

factors used in 

I'cmnulating EI'A water quality criteria for thcsc two elcnacnts were 6 and 44 for selenium 

and arsenic, respectivcly. The 1 e lo the fact that 

ingestion of selenium-contamina accumulation sE 

this element in fish (H 

quality criteria are bas 

: (I) "'$y tQ Some 

the mcan ~~~~ce~~~~tin fish in the 

n in thc quarry measured over the 

screpahncy far selcni 

factors as used in EPA water 

irect uptake frrrsm ayeacsus 

Concentrations of pcsticides and CBs in ~~~~~v~~~~~~ bass from Rogers Quarry are 

listed in Table 4-3. In all cases, the ice^^^^^^^^^ were far below the estimatkd detection 

limits (Table 4-31, but extrernciy tow c~~~~~~~r~~of four pcsticidcs and pesticide 

metabolites (heptachlor, DDT, DDE, and chlordane) werc, nevcrthelcss, estimated in 

some individual fish. These cstimated c~r~~~nt~~~t~~~~s were well below EPA water quality 

critcria screening levels (EPA 1990) listed i 

EPA Integratcd Risk ~~for~a~iQ~ System ( 

concentrations of organic ~nta~~~~a~~s ca 

compounds arc in fact prcscnt in the Cis 

kh were calculated using thc 

remcly low estimated 

y infer that these 

Two of eight fish collccted in sgers Quarry hr contwaniaant analysis were 

deformed. Observed abnormalities i1nuoPved bony sts-uct tires of the €ish including skull, gill 

opercula, fins, and scales. Each fish had s~verc erosion or incomplete development oC the 

skull, giving it il misshapen, concave head. The bony portions of most fins wcrc missing or 

eroded, and pclvic fins were missing. Tbe bony portion of the outer gill covccs was 

malformed or incotnplcte in both fish. Lateral line scalcs wcre missing in one fish; in the 

other, somc latcral line scales werc atsscnl, and the rcrnaining scales had a pronounced 

ridge. Both deformed fish weie older than the remaining six fish collcctecti in Rogers 

Quarry, with age estimated from scale annuli at 2 and 4 years, vemis I year for the normal 

appearing [ish ('Table 4-2). A~~it~~~~a~ fish werc captured anid rcleased in Rogers Quarry 
4-8 

ROGQUA 

KOGQUA 

ROGQIJA 

ROGQUA 

ROGQUA 

KOGQUA 

KOGQUA 

ROGQUA 

ROGQUA 

LMRASS 

XMBASS 

LMDASS 

LMBASS 

LMRASS 

LMBtiSS 

LMBASS 

LMBASS 

LMBASS 

5878 

5879 

54?4 

5485 

54% 

5497 

5499 

54% 

8785d 

M 

F 

M 

F 

F 

M 

M 

F 

467 

299 

21 7 

515 

180 

193 

315 

194 

.____I_ 

34.4 0.0002 

29.1 O.ooo11 

26.2 0.0003 

32.2 <0.012 

24.2 <0.012 

25.0 <0.012 

29.2 <0.0!2 

25.3 <0.012 

<0.012 

0.0084 

0.0010 

<0.022 

<0.024 

<0.024 

<0.024 

< 0.024 

CO.024 

0.0016 

< 0.018 

0.0007 

3.86K)§ 

0.W2 

O.OOO4 

0.W 

< 0.024 

< 0.024 

0.0001 

0.0003 

0.O002 

<0.012 

10.012 

c0.012 

<0.012 

<0.012 

0.0004 

HINDSCR BLUGII, 546.5 F 82.7 17.0 <0.025 <0.049 4.049 20.025 

EPA IRIS SCREENING CRITERIA' 0.0024 0.032 0.032 0.008 

"All other pesticides and PCBs below limit of defection. 

Compound 

ALPHA-BHC <0.012 

BETA-RHC <0.012 

DELTA-BHC <0.012 

GAMMA-BHC <0.012 

HEPTACHLOR <0.012 

ALDRIN C0.012 

I-?EPTACHl,OR EPOXIDE C0.012 

ENDOSULFAN I <0.012 

DIELDRIN <o.ozA 

ENDRIN < 0.024 

ENDOSULFAN I1 <0.02% 

4,4'-DDD < 0.024 

ENDOSULFAN SULFATE <0.024 

4,4'-DDT <0.024 

ENDRIN KETONE <0.024 

ME1'HOXY CHLOR ~0.024 

TOXAPHENE. <0.024 

ARCHLOR 1016 <0.024 

ARCHLOR 1221 <0.024 

ARCHLOR 1232 <0.024 

ARCHLOR 1242 <0.024 

ARCllLOR 1248 c0.024 

ARCHL,OR 1254 < 0.024 

ARCHl,OK 1260 < 0.021 

Detection limit (j@g wet wt.) 

4,4'-DDE < 0.024 

When analytes are not detected, the Oak Ridge National I-aboratory, Analytical Chemistty Division 

Organics Analysis lab repons values as Im than the quanlitation limit. Concentrations bWeh than the 

quantitation limit can be detected, hut with lower accuracy and precision than is required to define the 

quantification limit. The detection limit used in this table was estimated by dividing thc reported 

quanlification limit by a factor of ten. In some cases, the laboratory reported even lower concentrations to 

be dctectcd. These values are reported, but are unlikely to actually indicate the presence of the specified 

analyte. 

bLMBASS = largemouth bass; BLUGITa = bluegill sunfish. 

"Sum of alpha and gamma chlordane. 

dDuplicate for 5878. 

'%PA, person:11 communication. 
4-9 

because the collection efhst was ~~t~~~t~to collect ~n~~v~du~~s rcpresentixag a broad 

range of sizes and ages. All fish released 

appearance to the six undeforrned fish in 

or observed in McCoy Branch embaymen 
4-10 

Largemouth bass in Rogers Quarry and McCoy Branch embayment will be sampled 

and analyzed for metals again in 1991 to ascertain whether or not concentrations of 

arsenic, sclenium, and thallium decrease as expected. Largemouth bass will also be 

collected from a reference site more similar to Rogers Quarry, such as Lambert Quarry. 

At the same time, a more extensive survey of the incidence of bony structure deformities 

will be carried out. Further review of the scientific literature for possible agents that 

cause abnormalities similar to those found in Rogers Quarry bass will be conducted. 
5.1 XNTRODUCTlCTiON 

Fish populatiran and community studies can be uxx.i ta assess the ecologicd effects of 

water quality and habitat. ncsc studies offer several a~~a~ta~es wer ot er indicators of 

cnvironmental quality (Karr et al. I and are relevant to any evaluation of 

the biotic integrity of streams such h. Fish ~~~~un~t~~~, for example, 

comprise several trophic levels with species t at, or near, thc end of food chains. 

Consequently, they integratc the direct effects of water quality and habitat changes on 

primary producers ~~ri~h~~~) and ~~~~~er~ ~~n~~~~ ~~~~rte~~ate~), which are used fnr 

food. Because of thesc trophic interrelationships, the ng af fish ~~~~~~~~01has 

often been used as an index of water quality (Weber 1 eesm et at. 1977; Karr et ai. 

1986). hioreover, statements about the condition of thc fish ~~~~un~ty are better 

understmd by the general public (Karr 1981). 

The initial objectives of the fish ~~)rn~~~n~t~ mtmitoring task were to (1) characterize 

spatial and temporal patterns in distrihution and abundance of fishes in McCoy Branch, 

and (2) document my efkcets on fish ~~~rn~~~~~y structure and function rcsulting from 

implementation of the remedial actions as discicusse 

and Loar 1988). 

cCoy Branch RFI (Murphy 

5.2 DS 

The fish community in McCoy Brarnc was evaluated at one area upstream and one 

area downstream from Rogers Quarry (Fig. 2-2); both areas arc p~~te~~~~~~y impacted by 

coal ash effluent (Sect. 2.2.3). The upstream area was ~a~i~~~~ qualitatively over a lung 

stream reach to dctermine absence or presence ol fish. e ~~own~~re~~ arm was 

sampled quantitatively at McCoy Branch kilonietcr ( CK) 1.56 to measure population 

parameters. Similar quantitative saniples were made 

Creek kilometer (GGK) 2.4 and White Oak Creek klliometcr ( CK) 6.81 Ibr comparison 

of population parameters (Fig. 2-1). No attempt was macle to survey the quasay itsell. 

two nearby rerererace sitcs [Grassy 

Both qimalitativc and quantitative sampling was epamducted using a ~~~~~“~0t Model 

c pulse frequency and the 

1SA backpack electrofishcr. The unit has a ~~~f-c~~t~i~~~, ~~~~~~~n~-power~~ generator 

capable of delivering up to 120 V of pulsed, direct. current. 

output voltage can bc varied, but generally a pulse f1hequenc-y of 90-120 Hz and ti voltage 

of less than 400 V was used. 

For yualitativc sampling, onc clcctsofisbcr and onc nchter made a single 

electrofishing survey upstream through the stream, A majority of the stream and all major 

tributaries were sijmplcd. Two surprey~ (1 1 May 998 the 

upstream. Anothcr, supvcy (14 Decernhes 1987) w 

the earthen darn. Stunncd fish were to be kcpt an 

stream from thc Rogers Quarry inkt (MCK 1.92) t 2.65) 

e of the strcam scctiorrs above 

Ificd to specks. 
5-2 

For quantitative sampling, a 0.64-cm mesh seine waq placed across the upper and 

lower boundaries of the fish sampling site to restrict fish movement. The sampling site 

(MCK 1.56) varied between 46-50 m in length (Table 5-1) for the three sampling surveys. 

A quantitative sample involved one electrofisker and one or two netters, This sampling 

team electrofished upstream through the site, collecting stunned fish for three separate 

passes. The fish were separated by pass in buckets prior to processing. Depending upon 

the turbidity of the water, the consecutive passes could not always be made immediately. 

Rather, fish were processed after each pass to allow sufficient time for the water to clear 

before another pass was started. 

Following the electrofishing, fish were anesthetized with NS-222 (tricainc 

methanesulfonate) and processed. ‘To process the fish, they were identified, measured to 

the nearest 0.1 cm (total length), and weighed to the nearest 0.1 g (for fish < 100 g) or 

grain (for fish > 100 g> using Pesola spring scales. At sites with high fish densities, 

individuals were recorded by l-cm size classes and species. After 25 individuals of a 

species-size class werc measured and weighed, additional members of that size class were 

only measured. Length-weight regressions were later used to estimate weight for 

unwcighed fish (Railsback et ai. 1989). Other data recorded (if possible to determine), 

included sex, reproductive state, disposition @e., dead or kept for laboratory idcntification 

and inclusion in a reference collection), and the presence of any abnormalities (e.&, 

external parasites or skeletal deformities). After processing fish from all passes, the fish 

were allowed to fully recover from the anesthetic and were returned to the stream within 

the sampling site. Any additional mortality occurring as a result of processing was noted 

at that time. 

In addition to data on individual fish, data on selected physical and chemical 

parameters and the sampling effort were recorded. An Moriba Model U-7 Water Quality 

Checkcr was used to measure pH, temperature, dissolved oxygen, and conductivity. An 

€IF Instruments Model DR’T-15 turbidimeter was used to measure turbidity. The duration 

of the electrofishing effort was recorded for each pass, and a visual cstimate was made of 

percent cloud cover. Following completion of fish sampling, the length, widt 

intervals), and depths (at 3 points on the width transect) of the sampling reach were 

measured at each site. 

Species population estimates were calculated using the three-pass removal method of 

Carle and Strub (1978). Biomass was estimated by multiplying the population estimatc by 

the mean weight per individual. ‘rota1 numbers and biomass wcre divided by the surface 

arca (m2) of the sampling site to calculate values per unit arca. For each sampling date, 

surface area was estimated by multiplying the length of sampling reach by the mean width 

based on measuremcnts taken at 5-m intervals (Fable 5-1). 

The population structure of the three most abundant species was examined by length 

frequencies. The lengths of the estimated fish population were separated into 1- or 2-cm 

size classes, depcnding on the maximum size of the species. These frequencies indicatcd 

whether the population included young and adult individuals and if any unusual mortality 

had affected a size class. 
5-3 

Table 5-1. Length, mean width, mean depth, mea, and pl-rBk ratio (PiR) of fish 

sampling sitcs on McCoy Branch and two reference stream, Grassy Creek 

and White Oak Creek, for each sampling date 

MCK 1.56 05/1 1/89 4.6 1.6 18.6 74 0.4 

18/27/89 50 0.9 10.5 45 0.4 

05/16/90 50 0.9 13.6 45 0.5 

GCK 2.4 04/06/89 60 1.9 13 114 0.8 

10/23/89 61 1.4 9 85 1.8 

0411 9/90 61 1.6 8 98 0.8 

WCK 6.8 04/20/89 60 2.3 6.3 138 0.4 

1 01'3 1/89 fio 2.0 8.1 1 2Q 0.7 

94/03/90 55 2.5 7.7 138 NMb 

"MCK = McCoy Branch kilometer; GCK = Grassy Creek kilometer; WCK = White 

b~~ = not metisured. 

Oak Creek kilometer. 
5-4 

The procedures used for calculating density, biomass, and length frequency arc given 

in inore detail in Railsback ct al. (1989). 

Condition factors nieasure the degree of plumpness of a fish as a measure of relative 

health (Bennett 1970). A condition factor (K) was calculated for individual fish by site 

using the following formula: 

whcre the weight is in grams and total length in centimeters (Hile 1936). Fish without 

measured weights were not used in the calculation of condition factors" A comparison of 

condition factors bctween sampling periods was mads: with an analysis of variance 

(ANOVA) on untransformed data (SAS 198%) because the condition factors exhibited 

homogeneity of variance (SAS 19853). If the ANOVA indicated significant differences in 

condition factors between groups, thc Tukey test was performed to identify those groups 

that were significantly different (alpha = 0.05). 

Suweys of upper McCoy Branch above Rogers Quarry failed to locate any fish. 'fie 

three surveys at MCK 1.56 indicated the stream below the quarry had a permancnt fish 

community. At MCK 1.56, species richness (total numbcr of species) ranged from 9 to 

11 specics for the three surveys made from May 1989 to May 1990 (Table 5-2). The total 

number of species taken during this period was 14, but only 4 species were taken in all 

surveys. Specks richness in McCoy Branch was considerably higher than the 3-5 species 

found in the reference sites. 

'Ihe variability in species number and composition in McCoy Brarich is related to 

proximity of the site to Melton Hill Reservoir. The closeness of the reservoir allows 

species to be found in McCoy Branch that are atypical for a stream the size of McCoy 

Branch. Only blacknose dace (Rhiniciithys atratulus), central stoneroller (Cumpostomn 

nnamnlum), redbreast siirifish (Lepomis nurifus), and saaubnosc darter (Etheostomn 

sirnoterum) are typical inhahitants of similar-sized streams in this area (Kyon and LBar 

1988). Comparisons with the reference streams indicate that sevcral species expected to 

occur in streams of this size wcre missing. These species include creck chub (Semotihs 

ntromaculntus). striped shiricr (Luxilus chrysocephalus), white sucker (Catostonzus 

conzmcrsotzi), and banded sculpin (Cottus cnroliaae). The absence of these species may 

reflect past extermination by coal ash discharges and prevention of recolonization from 

Melton Hill Reservoir. The variable association of fish species and the presencc of fish 

atypical for a stream of this size suggest that the comtnunity contains many individuals that 

move in and out from the reservoir. 

'Ihc fish community at MCK 1.56 contained four species [green sunfish (L. 

cyanellus), carp (Cyprfnus cmpio), ycllow bullhead (,4nreiums natnlis), and spotfin slminer 

(Cyprirzelln spiloptrrn)] that are considered to be insensitive to many habitat and water 
5-5 

Table 5-2 Fish densities (number fiSWrn3 in McCoy Branch and in two reference slreams, 

White Oak Creek and Grassy Cnxk, for April-May 1989 to April-May 1990 

Species April-May October April-May 

1989 1989 1990 

Blacknose dace 

Bluntnose minnnow 

Spotfin shiner 

Stoneroller 

Bluegill sunfish 

Green sunfish 

Largemouth bass 

Red breast sunfish 

Redear sunfish 

Warmouth 

Greenside darter 

Snubnose darter 

Yellow bullhead 

Total number species 

Total density 

Blacknose dace 

Creek chub 

Stoneroller 

Banded sculpin 

Total number of species 

Total density 

Blacknose dace 

Creek chub 

Striped shiner 

Grecn sunfish 

White sucker 

Banded sculpin 

Total number of species 

Total density 

0.5 

0.1 

0.1 

<o. 1 

5.2 

0.3 

0.1 

<O.l 

<0.1 

<0.1 

<0.1 

11 

6.4 

1 .O 

0.1 

0.2 

3 

1.3 

0.1 

0.1 

c0.1 

cO.1 

4 

0.2 

K0.1" 

0.7 0.1 

0.4 

0.9 

0.1 

0.2 

<0.1 

0.1 

0.1 

0.2 

10 

2.7 

1.4 

0.8 

c0.1 

<0.1 

<0. 1 

<0.1 

<0.1 

0.1 

9 

2.6 

1.9 1.1 

0.2 <0.1 

0.3 0.3 

<0.1 

4 3 

2.4 1.4 

2.2 0.9 

0.5 0.3 

<0.1 

co.1 

KO. 1 c0.1 

cQ.1 c0.1 

5 5 

2.8 1.3 

"Value of <O.l indicates species was present at very low densities. 
5-6 

quality stressors. They would be considered tolcrant species in an impact assessment 

methodology such as the Index of Biotic Integrity (Mar et a]. 19%). Only two species 

were found that woiild bc considered slightly intolerant or sensitive to stress, the 

Tennessee snubriose darter and greenside darter (E, BIenazE'des), and thesc specks were 

represented by only a few individuals. This pattern suggests that McCoy Branch is a 

stressed system. 

Trophic composition of the community can indicate further stress on the system. A 

noaimpacted stream will have mailgr benthic insectivores, few gcneralist feeders, and a 

stable piscivore population. The fish community of McCoy Branch included many 

omnivores or generalist feedcrs, few benthic insectivores, and kwes piscivores. Generalist 

feeders are readily able to switch prey items and are more successful in stressed stream 

systcnas (Leonard arid Orth 1986). In McCoy Branch the generalist feeders included the 

blacknssc dace, carp, blucgill sunfish (L. macrmhin~s). warmouth (L. $EC~OSW), and ycll~w 

bullhead. Bcnthk insectivores are specialized feeders that are limited in tine prey items 

they can eat, are more successful in undisturbed streams (kmnard and Orth 1986), and in 

McCoy Branch, included ody the two darter species, The largemautb bass (Mzcropten~s 

salmoidcs) was the mly piscivore; it was present in low numbm ('I'able 5-2) and only at 

small sizes. 

Densities at MCK 6.56 for the three: sampling periods ranged from 2.6 to 64 fish/m2 

(Table 5-2). The density in May 1989 of 6.4 fish/m2, included 5.2 blucgill/m2. Later 

samples did not have such a strong component of bluegills, and the densities were much 

lower. Compared with reference strcarns, MCK 1.56 densities were gcnerally higher than 

either dcnsities at GCK 2.4 or WCK 6.8. 'The high densities may be affected by 

immigration from Meltsn Hill Reservoir and/or Rogcrs Quarry. 

The densities of individual species were p~ropnrtionally similar for each sar~pling 

pcriob. The community density was dominated by blumtnose minnow, bluegill, and green 

sunfish; however, none of these species occurred in the reference streams. Conversely, 

thc dominant species in the referefice streams, blacknose dace and creek ch~h, were 

present in low numhcrs oi absent altogether from McCoy Branch. 

Fish bioriiass values (g wet wt/m') paralleled the trends obscwed icp population 

density (Table 5-3). The initial sample in May 1989 had a11 extremely high biomass of 

107.5 g wet wt/m? and was due to the presence of several large carp and a substantial 

numb@;- of sunfish. The sample in October 1989 had a much lower biomass (17.4 g wct 

wh/rn2) than in May due to the abscncc of many large sunfish. However, the mmmunily 

bio~nass reboundcd in May 195% (50.3 g wet wt/m2), when more large sunfish returned to 

the site. The biomass in McCoy Branch was 2-100 timcs higher than the values found in 

the refercace streams (Tablc 5-31 at comparahlc sampling dates. 

The domirnant species (excluding carp), in tcrms of biomass, were bluegill, green, and 

redbreast sunfish. Most of the biomass for bluegill and green sunfish came from large 

numbers of several intcrmcdiate size classes, while the biomass of the redbrcast sunfish 
5-7 

Table 5-3. Fish biomass (g kh/m2) in McCoy Branch and in tw, reference streams, 

White Oak Creek and Grassy Creek, for April-May 1989 to April-May 1990 

Species April-May October April-May 

1989 1989 1m 

Blacknose dace 

Bluntnose minnnow 

Spotfin shiner 

Stoneroller 

Bluegill sunfish 

Green sunfish 

Largemouth bass 

Redbreast sunfish 

Redear sunfish 

Warmouth 

Greenside darter 

Snubnosc darter 

Yellow bullhead 

Carp 

Total biomass 

Blacknose dace 

Creek chub 

S toncroller 

Banded sculpin 

Total biomass 

Blacknose dace 

Creek chub 

Striped shiner 

Grcen sunfish 

White sucker 

Banded sculpin 

Total biomass 

1.7 

73.6 

0.5 

0.1 

20.1 

3.9 

6.1 

0.2 

0.1 

c0.1 

0.2 

107.5 

White Oak Cmek k3onmer 6.8 

1.3 

0.4 

2.7 

0.2 

0.4 

0.1 

0.2 

0.9 

0.1 

0.9 

3.1 

1.8 

0.8 

6.7 

0.5 

0.9 

0.2 

2.4 

17.4 

8.4 

0.3 

<0.1 

1.2 

9.9 

1.5 

2.3 

0.7 

0.2 

0.6 

5.1 

0.2 

35.8 

6.2 

0.3 

2.3 

0.6 

0.3 

0.1 

4.5 

50.3 

1.2 

0.1 

0.9 

2.2 

1.1 

1.6 

0.5 

0.3 

€0.1 

3.5 
5-8 

was based on a few large individuals. The dominance by sunfish of the community 

biomass reflected the influence of Melton Hill Reservoir. 

The length-frcqucncy histograms for the three most abundant species reflected their 

reproductive patterns and any potential stress from coal ash on these patterns. The most 

abundant spies, the bluegill sunfish, showed a strong dominance by the 4- to 7.9-cm size 

classes in the spring 1989 sample (Fig. 5-1). However, thc fall 1989 sample docs not show 

any small size classes, suggesting a lack of bluegill reproduction in McCoy Branch Also 

the general bluegill population declined. In 1980, the population remained small with a 

shift towards more large individuals in the site. 

The green sunfish showed a morc balanced pattern, with large numbers of small- to 

medium-sized individuals and a few large individuals at all sample dates (Fig. 5-1). In Eke 

fall 1989 sample, the two smallest size classes had substantial numbers of fish. This 

suggests a relatively stable reproductive effort. 

The bluntnose minnow had a much narrower size range, which was dominated by 

larger size classes in the spring samples (Fig. 5-1). The smaller individuals in the fall 1989 

sample are an indication of some reproduction (or immigration from nearby embayment 

areas). 

Comparisons of condition factors (M) should provide information on the relative wellbeing of the fish, because those with more weight per length have a higher condition 

factor (Everhart et al. 1975). Data were not available for a statistical comparison of 

condition factors between MCK 1.56 and the reference sites because there was so little 

species overlap. Whcn compared with condition factors of redbreast and bluegill sunfish 

in other areas of WOC (M. G. Ryon, Environmental Sciences Division, QRNL, personal 

communication), condition factors of these species at MCM 1.56 were within thc range of 

values. Scasonal comparisons of condition factors in McCoy Branch werc made for nine 

species. Three species, bluegill sunfish, green sunfish, and bluntnose minnow 

demonstrated statistically greater condition factors in spring samples than in fall samples. 

Six other species did not show any significant differences. 

As part of the normal processing procedure for population estimates, observations of 

abnormalities or attached parasites are madc of the fish specimens. Usually, these 

abnormalities are limited to less than 1-596 of the population in a minimally stressed 

system; a highly stressed system would have 5% or more abnormalities (Karr et al. 1986). 

Suck abnormalities may include spinal deformities, open skh lesions, fin rot or erosion, or 

distended eycs (‘popeye’). The number of such observations made in McCoy Branch 

seemed unusually high. 
5-9 

ORNL-DWG91-17425 

250 

-I 

d 

w 200 w 

m 8 150 

LT 

W 

3 

$100 

P 

50 

0 

2-3.9 4-5.9 6-7.9 8-9.9 10-17.9 12-13.9 14-1 5.9 16-17.9 18-19.9 

25 

=j' 20 

G 

z 

3 fn 

Z 15 w 

w 

[r 

8 

B 10 

5 

U 

W 

m 

25 

0 

2.39 4-59 6-79 8-99 10-11 912-13914-15916-17918-199 

4-49 5-5.9 6-6.9 7-7 9 8-8.9 9-9.9 10-10 9 

LENGTH (cm) 

Fig. 5-1. Length-frequency histograms for bluegill sunfish, green sunfish, and 

bluntnose minnow for May 1W, October 1989, and May 1990 frcirn McCoy Branch site 

MCK 156. 
5-18 

In the May 1989 sample, 27% oE the green sunfish (6.3-15.7 rnrn TI,) and 73% of 

the redbreast sunfish (10.9-17.5 mrn TI,) had one abnormality, extremely eroded fins. 

The pelvic, pectoral, and anal fins were often missing or reduced to mere fin rays without 

any membrana and tipped by an enlarged knob. The occurrence of abnormalities 

decreased substantially in the October 1989 fish population sample (2%). However, the 

May 1996) sample again demonstrated severe abnormalities. Eroded fins were found in 

8% of the green sunfish (9.1-14.5 mm TL) and 13% of the bluegill sunfish. Also, 11% of 

the bluegill (9.2-18.1 rnrn TL) showed anothcr abnormality. a misshapened head that 

appeared to be a skull deformity. Similar deformities were noted in largemouth bas 

taken in bioaccumulation sampling of Rogers Quarry (Sect. 4.3). The reference streams 

did not have any specimens with either erode fins or dcformed heads during these 

ds. "lie presence of the deformities suggests an extreme stress in McCoy 

s related to the high levels of arsenic or selenium in McCoy Branch water 

(Sect. 2-22 and 4.3). 

5.4 CON@EUSIONS 

Data on the fish populations of McCoy Branch demonstrated the stream has received 

considerable stress from the coal ash operations. The total lack of species above the 

quarry indicate that conditions were lethal to fish in that section. The cessation of the 

coal ash sluicing through that section after November 1989 should have reduced that 

stress. However, Rogers Quarry effectively acts as a migration barrier to species that 

might repopulate upper McCoy Branch. 

The fish community below Rogers Quarry, although permanent, demonstrates a lesser 

degree of impact than that of upper McCoy Branch. The stress is related to both coal ash 

discharges and the impacts of Melton Hill Reservoir. The speeics composition, and the 

most abundant species, reflect conditions inappropriate for a stream the size of McCoy 

Branch. Species that should occur in such a stream are missing and have been replaced by 

those from the adjacent reservoir. Even those species demonstrate several degrees of 

stress. The species occurring in the stream include those most tolerant of degraded 

conditions. This applies to both tolerance of physical and chemical stress and a flexibility 

in feeding requirements. Finally, substantial numbers of individuals within the community 

demonstrate severe physical abnormalities only rarely found in other systems. 

The future plans for assessing the fish community in McCoy Branch will continue the 

twice a year (spring and fall) sampling schedule. Until fish populations arc found in upper 

McCoy Branch, sampling in that area will be restricted to qualitative surveys. An 

additional reference site will be sampled quantitatively. This selected site will more closely 

approximate the species and the conditions of MCK 1.56. For example, the site will be 

situated close to an embaynient or main section of Melton Hill Reservoir. During the 

quantitative processing, additional attention will be given to assessing abnormalities. 
5-1 1 

Because immigration of individuals and species into McCoy Branch from Melton Hili 

Reservoir is occurring, further qualitative sampling will be conducted to assess 

immigration. If possible, additional qualitative sampling will include the quarry; this may 

be a cooperative efFort with sampling for the bioaccumulation task. 

Long-term plans for McCoy Branch studies may include the reintroduction of fish 

species into upper McCoy Branch above Rogers Quarry. The fish would be species 

expected to occur in such a stream (e.g., blacknose dace) and population dynamics would 

be monitored after the reintroduction, 

6.1 INTRODUCIlON 

Benthic macroinvertebrates arc those organisms which live on or in the substrate of 

flowing and nontlowing bodies of water and are large enough to be seen without the aid 

of magnification. Their limited mobility and relatively long life spans (a few months to 

more than a year) of most taxa make them ideal for evaluating the ecological effects of 

effluent discharges to streams (Platts et al. 1983). Thm, the composition and structure of 

the benthic community reflect the relativcly recent past, and they can be considerably 

more informative than alternativc methods that rely solely on water quality analyses but 

miss the potential synergistic effects often associated with complex effluents. The 

objective of the initial phase of this study is to provide a detailed spatial and temporal 

characterization of the benthic invertebrate community oE McCoy Branch. These data will 

be used as a baseline from which the effectiveness of major remedial actions within the 

McCoy Branch watershed can be assessed. The data will also be used to provide direction 

for future studies. 

6.2 MA'l33UAI-S AND iMETHODS 

Benthic macroinvertebrates were sampled at approximately quarterly intervals 

beginning in April 1989 through January 1990 at two sites in McCoy Branch (Fig. 2-2). 

Because an unimpacted reference site was not available on McCoy Branch, a relatively 

unimpacted reach of upper WOC served as a rcference site. Upper WOC is similar in 

size to McCoy Branch, and is located just north of ORNL, approximately 3 Km west of 

McCoy Branch (Fig. 2-1). Three random quantitative samples were collected from a 

permanently rnarkcd riffle at each site with a Surber bottom sampler (0.09 m2) fitted with 

a 363-pm-mesh collection net. To obtain additional information on taxonomic richness, a 

qualitative sample consisting of collections from riffle and nonriffle habitats (e.g., pools, 

leaf packs, detritus, and snags) was taken from each site in spring 1989. Qualitative 

samples were collected with a D-Erame aquatic dip net (mesh of 800 pm x 900 pm). All 

samples were placed in prelabcled, polyurethane-coated glass jars and preserved in 80% 

cthanol; the ethanol was replaced with fresh ethanol (80%) within 10 d of collection. 

Supplemen tal informa tion on water quality and stream characteristics was recorded at 

thc time of sampling. Temperature, conductivity, dissolvcd oxygen, and pH wcre 

measured with an Horiba Model U-7 Water Quality Checker. Water depth, location 

within the riffle area (distance from permanent headstakes on the stream bank), visual 

determination of relative strcam velocity (very slow, slow, moderate, or fast), and substrate 

type [visual determination based on a modified Wentworth particle size scale (Loar 1985)] 

were recorded for each sample. 

All samplcs were washed in the laboratory using a U.S. Standard Scries No. 60 sievc 

(250-pm mesh) and placed in an 8- x 10-inch white, plastic tray fox sorting. Organisms 

werc removed from the dcbris with forceps and placed in labeled vials ccmtaining 80% 

ethanol. Organisms were idcntified to the lowest practical taxonomic level using a 
6-2 

stereoscopic dissecting microscope. After chironomid larvae were sorted into groups 

based on morphological similarities, one or more representativcs of each group were 

mounted on a slide in CMC-10 mounting medium and identified using a compound 

microscope. The remaining chironomid larvae ere then identified at a magnification of 

5OX to lOOX with a dissecting microscope. '4 blotted wet weight of all individuals 

combined in each tamn was determined to the nearest 0.01 mg on a Mettler analytical 

balance. 

Slides of mounted chironomid larvae were retained in slide boxes, and individuals of 

the remaining taxa from a given site and sampling date were preserved in separate vials 

containing 80% ethanol. A reference collection of these specimens will be maintained at 

ORNL. 

The Shannon-Weincr index (W') was used to calculate the taxonomic diversity of 

benthic macroinvertebrates at each site (Pielou 1977): 

where P* is the proportion of the benthic invertebrate community made up of species j. 

H' values of 3 or greater are typical of clean water, whilc values of 1-3 are usually 

associated with moderate pollution, and values of less than 1 characterize heavily polluted 

water (Platts et al. 1983). 

J 

All data analyses were done with the Statistical Analysis System (SAS 1985a,b). 

Mean values for density'; biomass'; number of taxa per sample (taxonomic richness); 

number of Ephemeroptera, Plecoptcra, and Trichoptera taxa per sample (EPT richness); 

and taxonomic diversity were compared separately with a one-way analysis of variance 

(ANOVA) on quarterly sampling period-specific data with site as the main effect; all 

analyses were based on three replicatcs per site and date. Prior to performing the 

ANOVA, data were transformed 

log10(X+d) (6-2) 

where X = individual values for density, biomass, etc. (Elliott 1977). Where significant 

differences were found betwecn sites, treatment means were compared using a Tukey 

standardized range test (= = 0.05) to discriminate these differences. 

'Comparisons between sites in density and biomass were made both with and without 

Mollusca (snails and mussels) and Decapoda (crayfish) since these taxa arc typically very 

heavy but numerically unimportant and can thus suppress the importance of the weight 

changes of the other organisms. Therefore, unless otherwise noted, trends presented in both 

spatial and temporal patterns in density include both Decapoda and Mollusca, while trends 

in biomass exclude these two groups. 
6-3 

6.3.1 Taxonomic Composition 

A checklist of the bcnthic invertebrates collected from McCoy Branch and a 

reference site at WCK 6.8 from April 1959 through January 1990, is prcscnted in 

Appendix B, Tablc B-1. A total of 163 distinct taxa, 145 of which were insects, were 

collected in quantitative samples from the designated sampling sites in the two streams. 

Nine ordcrs of insects, including Collembola (springtails), Ephemcroptera (mayflies), 

aleoptera (beetles), Diptera (true flies), Kemiptcra (true bugs), Mcgaloptcra (alderflies, 

fishflies, and dobsonflies), Odonata (dragonflies and damselflies), Plecoptera (stoneflies), 

and Trichoptera (caddisflies), were collected from these streams. Thc order Diptera was 

the most taxonomically rich group with 76 representative taxa, 50 of which were from the 

family Chironomidae (truc midgcs). Of the remaining insect orders, Trichoptera, 

Ephemeroptera, and Plecoptera had the greatest number of taxa with 23, 20, and 16 taxa, 

respectively. Thc numbers of taxa from thcse three orders wcre greater from the 

reEerence sile than from either of the two McCoy Branch sites. Of the nine insect orders 

rcpresented in the quantitative samples, Megaloptera wcre ahscnt from MCK 1-40, and 

Hemiptera were absent from MCK 2,OX 

In addition to insects, taxa representing ken other major taxonomic groups wcre 

collected including Amphipodi~ (siduswimmers), Copepoda (copepods), Decapoda 

(crayfish), Gaslropodd (snails), Hydracarina (water rnitcs), Ncmatoda (roundworms), 

Oligochaeta (aquatic earthworms), Ostracoda (wed shrimp), Bivalvia (mussels and clams), 

and Tricladida (planaria or flatworms) (Appendix €3, Tablc B-1). Copcpoda and 

Ostracoda were collected only from McCoy Branch. 

Twenty-seven additional taxa were collected from McCoy Branch and 25 from WOC 

in qualitativc samples (Appendix B, Table B-1). Decapods, amphipods, and water mites 

were found in McCoy Branch only in the qualitative samples (Appcndix B, Table El). Of 

the additional taxa collected from McCoy Branch, only one belonged to thc order 

Ephemcroptcra. In the WCK 6.8 sample, there were 11 additional taxa of 

Ephemeroptera, Plecoptera, and Trichoptera. The group containing the greatest number 

of additional taxa was the dipterans (7 from WCK 6.8 and 23 from the MCK sites). 

6.3.2 Density and Biomass 

The annual means for density and biomass of the benthic macroinvertebrates at each 

sampling site are presented in Table 6-1. The density of invertebrates (including and 

excluding mollusks and decapods) at MCK 1.40 and WCK 6.8 was almost twicc that at 

MCK 2.03 (Table 6-1); these differences were statistically significant (Table 6-2). Thc 

biomass of macroinvertebrates (all taxa) at WCK 6.8 was more than 13 times higher than 

at MCK 2.03, and almost 6 times higher than at NGK 1.40 (Table 6-1). When mollusks 

and decapods were excluded, the biomass at WCK 6.8 was similar to the biomass at 

MCK 1.40 but still was almost 2.5 limes higher than at MCK 2.03. Statistical comparisons 

showed that the biomass at MCK 2.03 was significantly lower than at MCK 1.40 and 

WCK 6.8 (with or without the mollusks and decapods), while the biomass at NCK 1.40 

differed from WCK 6.8 only whcn all taxa wcre considered (Table 6.2). 
Taxonomic EPT 

Sitesb Densitpd Density ~iornassq ~iomassJ richnessg richness' Diversity" 

MCK 1.40 669.5 662.7 473.1 442.6 25.6 4.9 2.90 

(186.7) (185.0) (104.2) (109.3) 43.0) (0.8) (0.08) 

MCK 2.03 388.9 385.0 206.8 187.4 23.8 5.5 3.02 

(248.9) (247.0) [ 112.5) (57.2) (7.01 (3- 4 (0.24) 

WCK 6.8 714.1 675.1 275 1.2 452.0 45.8 15.7 3.98 

(194.1) (194.2) (568.3) (117.8) (2.3) (1.41 (0.20) 

e 

a 

'Values in parentheses are I 1 SE. 

'MCM = McCoy Branch kilometer; WCK = White Oak Creek kilometer. 

TQ. of indivictuaW8. 1 m2. 

dZncludes all taua. 

'Excludes Mollusca and Decapoda. 

&pressed as mg wet wti0.P m2. 

%pressed as No. of tasra/sarnple. 

'Expressed as No. of EPT taxa/sarnple. 

'E?rpressed as H'; the Shannon-Weiner index (H') was used to calculate the taxonomic diversity using the equation 

P- log:! Pj, where P. is the proportion of the benthic invertebrate mmmunity made up of species j. H' 23 indicates values tyyical 

o i clean water, 1 s H' <3 are moderate pollution, and €3' <I indicates heavily polluted water. 1 
6-5 

Table 6-2 Statistical oornparisrans“ of meam annual benthic rnacmhvertcbrate density, 

biomass, taxonomic richness, Ephemeroptera, Plectopte~~ and Tricboptcra (EPT) 

richness, and species diversity in McCoy Branchb and the reference stream, 

Wbite Oak Cree 

___~ - 

Eliensity (4 -1 

WCK 6.8 MCK 1.40 MCK 2.03 

Density (excluding Mollusca and Decapods) 

WCK 6.8 MCK 1.40 MCK 2.03 

~~~ (dt taxa) 

WCK 6.8 MGM 1.40 MCK 2.03 

Biomass (excluding Mollusks & hpoda) 

WCK 6.8 MCK 1.40 MCK 2.03 

WCK 6.8 

WCK 6.8 

€&hness 

MCK 1.40 MCK 2.03 

EPT Richness 

MCK 1.40 MCK 2.03 

Divetsity 

WCK 6.8 MCK 1.40 MCK 2.03 

“Sites not joined by lines are significantly different (a = 0.05), based on Tukcy’s 

bMcGoy Branch kilometer = MCK 

White Oak Creek kilometer = WCK. 

studcntized range test (HSD). n = 12 for each sitc. 
6-6 

Temporal patterns in density of macroinvertebrates at MCK 1.40 and WCK 62 werc 

similar with the highest density at both sites occurring in July 1989 (Fig. 6-1). In contrast, 

the greatest density at MCK 2.03 occurred in January 195% when the density was four 

times grater than during thc previous three sampling periods. During each sampling 

period, chironomids and colcopter2ns were generally the most alxmdant taxa at 

MCM 1.40, although a July peak in density was primarily the result aE a substantial 

increase in the numbers of trichopterans and rmonchironomid dipterans. Chironomids, 

ephemeropterans, and plecopterans were consistently the most a~~~~~~taxa at WCK 6.8. 

'I'he July peak in density at this site resulted primarijy from an increase in the nu~n 

pterans and nonchironomid dipterans and to a lesser extent plecopteran 

ds (Fig- 4-2). Chironomid densities were generally higher than the dcmities of 

other taxa at MCK 2.03; however, ephemeropterans (primarily Baelis) were responsible 

for a dramatic increase in density at this site in January. 

Seasonal trends in biomass were similar to those of density, with the highest values 

for biomass at MCK 1.40 and WCK 6.8 occurring in July, and the highest value at 

MCM 2.03 occurring in January (Fig. 6-1). Seasonal changes in biomass at MCK 1.40 

largely reflected the seasonal changes of Trichoptera, while at MCK 2.03 and WCM 6.8 

several taxa, particularly Trichoptera and Diptera, contributed to the seasonal chan-~ges 

(fig. 6-3). 

'ne number of taxa collected per sample at WCM 6.8 was almost two times greater 

than at either McCoy Branch site; this difference was statistically significant (Tables 6-1 

and 6-2). Taxonomic richness at the two McCoy Branch sites was similar, although the 

much higher standard error at MCK 2.03 dcmonstrated that fluctuations in richness 

between sampling periods were considerablc. In contrast, richness at MCK 1.40 and 

WCK 6.8 remained relatively stable. 

Temporal changes in taxonomic richness were similar at MCK 1.40 and ZVCK 6.8 

with each site exhibiting both increases and decreases throyh time (Fig. 6-4). In contrast, 

taxonomic richness at MCK 2.03 increased considerably through tirnc with the January 

1990 value being four times as high as the value than in April 1989. Notwithstanding 

these between-site differences, all three sites exhibited peaks in richness in January. 

Mean Ephemcroptera, Plecoptera, and 'I'richsptera (EPT) richness for all sampling 

periods was significantly greater in WOC than in either McCoy Branch site (Tables 6-1 

and 6-2). The mean number of EPT taxa at the WCK 6.8 site was three times that of 

either McCoy Branch site. Mean EPT richness at the two McCoy Branch sites was 

similar, although variability between sampling periods was considerably greater at 

MCK 2.03. 
6-7 

1200 

800 - 

II 

- 

" 

400 - 

- 

- 

0 

ORNL-DWG9 1 - 1 7426 

0 MCK 1.40 

0 MCK 2.03 

V WCK 6.8 

1500 T 

- 

0 MCK 1.40 

- 0 MCK 2.03 

- V WCK 6.8 

- 

_------ 

MONTH 

Fig. 6-1. Mean seasonal density (all taxa) and biomass (excluding Mollusca and 

Decapoda) of benthic macroinvcrtcbrates in McCoy Branch and White Oak Creek, April 

1989 to January 1990- Vertical bars are f 1 SE. MCK = McCoy Branch kilometer and 

WCK = Whitc Oak Creek kilornetcr. 
6-8 

ORMC--OW691- 17427 

MCK 1.40 

Ckironomidat 

v Other Diptera 

v Coleoptera 

a Trichoptera 

700 

c 

b 

1 QO 

6 hironomidae MCK 2.03 

0 8 Ephemeroptero 

a Trichoptera 

908 

- 6610 

E 

N 

Chirononidae 

$" Other Diptera 

V Coleoptera 

0 Epherneroptera 

A Plecoptera 

0 irichoptera 

WCK 6.8 

-4 . 

MONTH 

Fig 6-2. Mean se m3 for s'ated ma 

McCoy Branch and White Oak Greek, Ap 

Branch kilornetcr and WCK = White Oak Creek kilometer. 

MCK =z McCoy 
6-9 

MCh 1.40 

Chironomidce 

Other Diptera 

0 Trichoptero 

N" 

E 

0 

0 Ephemercpte-c 

MCK 2.03 

- 200 m -. 

fA 

=l 3 100 m 

.a ". \- / .i 

JUL OCT JAN APR 

0 Chironomidoe 

t Other Oiotcro 

V Coleoptera 0 E hernewptero A P LCO p t e KY 

0 Trichoptero 

WCK 6.8 

MONTH 

Fig 6-3. Mean seasonal biomass (mg wet wt.B.1 m2) for selected taxa in McCoy 

Branch and White Oak Creek, April 1989 to January 1990. MCK = McCoy Branch 

kilometer and WCK = White Oak Creek kilometer. 

...........-. ........... ....................... ....................... 

.- . . 
0 

aMCK 2.03 

WCK 6.8 

T 

i 

T 

T 

PW JUL QCT 

T 
6-11 

EPT taxa were collected from all sites during all sampling periods (Fig. 6-5). The 

richness of these taxa was particularly low at MCK 2.03 in April and July when an average 

of fewer than two EPT taxa were collected in each sample. As with taxonomic 

richness,the mean number of EPT taxa from WCK 6.8 was always higher than at either 

McCoy Branch site. The number of EPT taxa remained relatively stable through time at 

WCK 6.8 and MCK 1-40, while the greatest variability between sampling periods was 

exhibited at MCK 2.03. 

6.3.3.3 Species Diversity 

Spatial patterns in taxonomic diversity (H') were similar to those observed for 

taxonomic and EPT richness (Table 6-1); diversity was significantly higher at WCK 6.8 

than at either McCoy Branch site while at the two McCoy Branch sites diversity was 

similar (Table 6-2). Also, as for taxonomic and EPT richness, diversity was highest at 

WCK 6.8 during all sampling periods (Fig. 6-6). Temporally, MCK 1.40 exhibited less 

dramatic fluctuations in diversity than the other two sites, staying close to 3.0 in all 

sampling periods (Fig. 6-6). The other two sites exhibited similar magnitudes of 

fluctuation between each sampling period although not the same patterns. 

6.4 DISCUSSION 

The benthic invertebrate community of McCoy Branch, which historically has 

received fly ash and bottom ash sluiced from the steam plant at the Oak Ridge Y-12 

Plant, exhibited evidence of moderate degradation of water quality and/or physical habitat. 

Relative to the rcference site on White Oak Creek (WCK G.8), both McCoy Branch sites 

exhibited significantly lower values for taxonomic and EPT richness, and diversity. 

Additionally, both density and biomass were significantly lower at MCK 2.03 than at 

WCK 6.8 and MCK 1.40, suggesting that a greater degree of degradation exists upstream 

of Rogers Quarry- The most notable differences between the reference site and both 

McCoy Branch sites were in taxonomic and EPT richness; taxonomic richness was two 

timcs higher and EPT richness at least three times higher at WCK 6.8. The greater 

number of EPT taxa at WCK 6.8 is indicative of the overall health of this site, because 

EPT taxa generally tend to he very sensitive to alterations in water quality and physical 

habitat (Wicdcrholm 1984; Lenat 1984; Lenat 1988). 

Smith (1991a) found that the most highly-stressed invertebrate comrnunitics in 

streams on or near the ORR are almost exclusively comprised of chironomids and/or 

oligochaetes, while less pollution- tolcrant EPT taxa are virtually absent. While EPT 

richness was reduced in McCoy Branch relative to WCK 6.8, EPT taxa were collected 

during each sampling period from both sites. Although the EPT values from the McCoy 

Branch sites are consistently lower than for sites in other relatively undisturbed streams 

that drain the south slopc of Chestnut Ridge near ORNL (J. G. Smith, Environmental 

Sciences Division, ORNL, personal communication), the EPT values are comparable to 

those of a relatively undisturbcd reach of Mitchell Branch (MEK 1.43) located just east of 

the Oak Ridge K-25 Site (J. G. Smith, Environmental Sciepces Division, ORNL, personal 

communication). This suggests that the degrec of stress to the benthic macroinvertebrate 

community in McCoy Branch is relatively moderate. Greater stress at MCK 2.03 relative 
GRNL-DWGSI -17430 

MCK 1.40 

MCK 2.03 

WCK 6.8 

T T 
mMCK 1.40 

aMCK 2.03 

mWCK 6.8 

5 

ORNL-DWG91-17431 

n 

I 

W 

>- 

Im 

E 

w 

). 

- 

- 

n 

I T 

APR 

T 

JUL 

T 

OCT 

MONTH 

JAN 

Fig. 6-6. Mean seasonal diversity (I%') of benthic macroiuvertebrates in McCq Branch and White Oak Creek, April 19$9 

to Jmuargr 1990. Vertical bars are * 1 standard error. MCK = McCoy Branch kilometer and WCK = White Oak Creek 

kilometer, 
6-14 

to MCK 1.10 is implied by the significantly lower values for density and biomass. 

However, all. parameters exhibited substantial increases at MCM 2.03 during the last two 

sampling periods which suggests that recovery related to improvements in water quality 

and/or physical habitat may have begun. These community changes may have bccn the 

result of several measures taken at the Y-12 steam plant sine 1988 which have improved 

the water quality and reduced the quantity of coal ash discharged to McCoy Branch 

(Sect. 2.2.1 and 2.2.2). Continued monitoring should determine if this trend at MCK 2.03 

is the rcsult of remedial actions or is a response t other unidentified environmental 

factors, 

Relatively high conductivity measurements, > 500 fi/crn, in McCoy Branch 

(J. G. Smith, Environmental Sciences Division, ORNL, personal rmnmunication) in April 

1989 suggcst that the concentration of dissolved solids may have been clcvated. Lower 

conductivity values in McCoy Branch after April may reflect a reduction in the use of coal 

and subsequently, the quantity of ash produced at the Y-12 steam plant starting during 

upon the flow, some flushing af deposited ash may have occurred downstream of the ash 

pond such that the concentration in thc stream has decreased with time. Further sampling 

will verily if a trend toward lower conductivity exists. 

with a further seasonal reduction by April 1989 (Sect, 2.2.2), Depetding 

The composition and structure of the benthic mmmunity in McCoy Branch 

downstream of the ash pond appear to be responding to both physical and chemical stress, 

Suspcnded solids resulting from ash transport downstream of thc ash pond may be a major 

pcrturbation at MCK 2.03. Within Rogers Quarry, settling occurs so that the downstream 

load of suspended solids is reduced. Consideraklc deposits of coal ash were evident along 

and within the streambed at MCK 2.03 at the beginning of this project, while the presence 

of coal ash in lower McCoy Branch was much less evident (Sect. 2-24.; J. G. Smith, 

Environmental Sciences Division, ORNL, personal observation). Deposited solids can 

adversely affect organisms either directly by obstructing food collection and/or respiration, 

or indirectly by reducing food availability (Hynes 1990). Suspended solid depdsition and 

sediment accumulation havc been shown to both decrease the density and biomass of 

bcnthic invertcbrates by as much as 60% (Gammon 1970) and reduce diversity by 

eliminating stress-sensitive taxa (Mackenthun 1973; Wiederholm 1984). Thc dcposition of 

finegrained inaterial also can provide a substrate favorable for coloriization by taxa 

tolerant of thcse conditions such as chironomids (Wiederholm 1984). This may partially 

explain the prevalence of chironomids at MCK 2.03 compared to the other two sites. 

In addition to deposited solids, some metals have historically occurred in elevated 

concentrations in McCoy Branch with higher levels above Rogers Quarry (Scct. 2.2.2, 

Tables A-3, A-4, A-5, and A-6, Fig. 2-4 and 2-5). Of the metals measured, arsenic and 

selenium have the greater potential for impacts on aquatic life. 

Studies by Elwood in the 1970s (R. R. Turner, Environmental Sciences Division, 

OMNL, personal communication) showed elevated levels of arsenic in aquatic insects in 

McCoy Branch. Water quality samples taken between July 1986 and July 1Wl sliow that 

levels of arsenic in McCoy Branch exceeded the recommended maximum Concentration 

(50 p@) for protection of aquatic life (EPA 1976) from July 19% until approximately 
6-15 

July 1989. Levels of arsenic in McCoy Branch above 50 ClglL also occurred periodically 

from January 1990 through approximately May 1990 (Fig. 2-4). 

Levels of selenium in McCoy Branch consistently exceeded 10 pgjL, from July 1986 

through approximately January 1989. Maximum levels for protection of aquatic life are 

260 pg/L for acute exposure and 35 yg/L for chronic exposure; however, concentrations of 

5 pg/L have been shown to adversely effect hh production (RFI 1987). From April 1989 

to January 1990 levels of selenium in McCoy Branch ranged from near zero to 10 pg/L 

with an average of approximately 5 & (Fig. 2-5). It is possible that one or both of 

these metals could have an adverse effect on the benthic community in McCoy Branch. 

The low density and richness of sensitive taxa, particularly mayflies, which are generally 

very sensitive to metal pollution (Wiederholm 1984), and the relatively high percent 

composition of chironomids indicate the benthic macroinvertebrate community in McCoy 

Branch may be responding to long-term exposure to elevated levels of these or other 

potential toxicants. 

Finally, the magnitude of seasonal change of all parameters was most similar between 

MCK 1.40 and the reference site (WCK 6.8). This implies that environmental conditions 

were more stable at MCK 1.40 than at MCK 2.03, which may be a reflection of Rogers 

Quarry functioning as a settling basin for both sediments and associated chemical 

contaminants. However, impoundments have been shown to alter chemical and physical 

conditions of streams, which in turn, alter the benthic invertebrate community (Ward and 

Stanford 1979). Thus, while rcducing the impacts associated with coal ash, the quarry 

itself alters natural conditions which lead to alterations in the benthic invertebrate 

community. Future changes in the benthic community at MCK 1.40 in response to 

remedial actions may be mediated by the presence of the quarry. 

6.5 CONCLUSIONS 

The structure and composition of the benthic macroinvertebrate community in 

McCoy Branch are indicative of moderate stress. Maximum impact within this stream 

occurs upstream of Rogers Quarry as was exemplified by the significantly higher density 

and biomass at MCK 1.40 compared to MCK 2.03. Somc improvement in water quality 

was evidcnt downstream of the quarry, as demonstrated by significant increases in density 

and biomass of the benthic community at MCK 1.40. However, significantly lower values 

for taxonomic and EPT richness, and divcrsity at this site compared to the reference site, 

indicate somc impact. At MCK 2.03, substantial increases were observed in density, 

biomass, and taxonomic and EPT richness, particularly during the October and January 

sampling periods, suggesting that improvements in water quality may be occurring. The 

cause of the stress on the benthic macroinvertebrate community in McCoy Branch, at least 

upstream of Rogers Quarry, is most likely thc result of several factors related to the 

long-term discharge of coal ash from the Y-12 steam plant. The bcnthos, particularly 

upstream of the quariy (MCK 2.03), appears to be responding to habitat alteration as the 

result of ash deposition within the stream channel and possibly to leaching of potential 

toxicants (e.g., arsenic and selenium) from the ash. The benthic community at MCK 2.03 

should recover as coal fines arc removed from the streambed; however, recovery may be 
6-16 

slowed by the loss of supplemental RQW in the upper reaches of McCoy Branch which may 

increase the time required for natural cleansing of the stream. 

Rogers Quarry acts as a settling bassin far coal ash trans reed downstream from time 

ash pond, thereby diminishing the impact. of ash deposition on the benthic community 

downstream of the quarry. The benthic mmmunity at MCK 1.40 did not exhibit the 

temporal trends in increased density, biomass, or taxnxarmornk and EPT richness shown by 

MCK 2,03, suggesting this community may not be experiencing similar changes in water 

quality. Although Rogers Quarry appears to reduce the impacts associated 

deposition, this impoundment likely alters the physical and chemical environment 

downstream, which in turn alters the invertebrate community. Finally, the direct discharge 

of ash to the quarry (initiated in May 1990) may cause the quarry to act as an immediate 

source of toxicants through leaching of metals from the ash. This may impact the benthic 

community at MCK 1.40. 

The current sampling program for benthic rnacrainvertebratcs will continue. As for 

WCK 6.8, the snail EIitnia is a prominent membcr of the benthic macroinvertebrate 

communities of several streams that drain the south slope of Chestnut Ridge and the 

ORR (Smith 1991b). However, SQKE relatively undisturbed strcams in these same areas 

do not contain snails (Smith 1991b), and no historical data on the benthic 

macroinvertebrates of McCoy Branch exists. Thus it is not known if Ehia have ever 

occurred in this stream. Therefore, an additional refercnce stream without snails (Fifth 

Creek, F'lX 1.0) will be included in future analyses that will allow comparisons of McCoy 

Branch to reference streams with and -without snails. This sampling rograrn will provide a 

comprehensive characterization of the benthic community in McCoy Branch and an 

extensive data base that will allow documentation of the response of thc. benthic 

comm~mity as water quality changes occur as a result of remedial actions. The continued 

sampling program will provide further comparison of the benthic corrnmunity at MCK 1-40 

before and after direct discharge of bottom ash to Rogers Quarry and will document the 

response of the benthic community at MCK 2.03 to the absence of ash discharge Eroni the 

Y-12 Plant. 
Bennett, G. W. 1970. Management of Lakes and Ponds. Van Nostrand Reinhold, New 

Bjomberg, A, L. Hakanson, and K. Lundberg. 1988. A theory on the mechanisms 

Bogle, M. A., and R. R. Turner. 1989. Rogers Quarry water balance January 1, 1987 

York. 

regulating the bioavailability of mercury in natural waters. Envirm. Pollut. 4953-61. 

through June 30, 1988. YITS-506. Oak Ridge National Laboratory for Y-12 Plant, 

Oak Ridge, Tenn. 

Bowen, H. J. M. 1979. Environmental Chemistry of the Elements. Academic Press, 

London. 

Burris, J. A., M. S. Bamford, and A. J. Stewart. 1990. Behavioral responses of marked 

snails as indicators of water quality. Environ. Tox. Chem. 959-76. 

Carle, F. L., and M. R. Strub. 1978. A new method for estimating population size from 

removal data. Biometrics 34:621-630. 

Craig, P. M., and B. A. Tschantz. 1986. Preliminary seepage residual study by water 

balance method for Rogers Quarry. Y/SUB/86-1819/2. Y-12 Plant, Oak Ridge, 

Tenn. 

Crutchfield, P. J. 1966. Positive rheotaxis in Goniobasis proxima. Nautilus 79930-86. 

Cuvin, M. L. A., and R. W. Furness. 1988. Uptake and elimination of inorganic mercury 

and selenium by minnows, Phoxinus phoxinus. Aquat. Toxicol., 13205-216. 

Dycus, D. L. 1989. Results of Fish tissue screening studies from sites in the Tennessee 

and Cumberland Rivers in 1987. TVA/wR/AB - 89/5. Tennessee Valley Authority, 

Chattanooga, Tenn. 

Dycus, D. L., and G. D. Hickman. 1986. Concentrations of PCBs, DDTr, and metals in 

fish from Tellico Reservoir. TVA/ONRED/AWR-S7J25. Tennessee Valley Authority, 

Knoxville, Tenn. 

invertebrates. Freshwater Biological Association, Ambleside, England. Sci. Pub. 

No. 25. 

Elwood, J. W. 1984. Mercury contamination in Poplar Creek and the Clinch River. 

ORNLKM-8893. Oak Ridge National Laboratory, Oak Ridge, Tenn. 

ERDA (Energy Rescarch and Development Administration). 1975. Preliminary draft 

environmcntal analysis report. Oak Ridge Operations, Volume VI. Oak Ridge, Tenn. 

Everhart, W. H., A. W. Eipper, and D. W. Youngs. 1975. Principles of Fishery Science. 

Cornel1 University Press, Tthaca, New York. 

Gammon, J. R. 1970. The effect of inorganic sediment on stream biota. Water Pollution 

Control Research Series, 18050DWC12/70, Water Quality Office, US. Environmental 

Protection Agency, Washington, D.C. 

for collection and analysis of aquatic biological and microbiological samples. Book 5, 

Chapter 4A, pp. 1-332. In US. Gcological Survey, Techniques of Water-Resources 

Investigations or the United States Geological Survcy. U.S. Government Printing 

Office, Washington, D.C. 

preliminary report. Florida Department of Environmental Regulation, Tallahassee, 

Ha. 

Elliott, J. M. 1977. Some methods For the statistical analysis of samples of benthic 

Greeson, P. E., T. A. Ehlke, G. A. Irwin, 3. W. Lium, and K. V. Slack. 1977. Methods 

Hand, J., and M. Friedman. 1990. Mercury, largemouth bass, and water quality: A 
Hilq R. 1936. Age and growih of thc cisco, Leueich'hys a#qedi (LeSeur), in the lakes of 

the northcastem highlands, Wisconsin. U.S. Bur. Fish. Bull. 482 I 1-317. 

Wodsow, P. V. 1990. Indicators of ecosystem health at the species lewl and the example 

of selenium effects on fisk. Environ. Monitor. Assess, 15:241-254. 

Hoffman, F. 0, B. G. Blayllock, C. C. Travis, K E. Daniels, E. L. Etnicr, K E. COWS~F, 

and C. W. Weber. 1984. Preliminary screening of contaminants in sediments. 

OWNE/TM-93 70. Oak Ridge National Laboratory, Oak Ridge, Tenn. 

Houp, K. W. 1978. Population dynamics of Pfeurocem mufa in a central Kentucky 

limestone stream. Am. Midl. Nat. 83814. 

Hynes, H. B. N. 1978. The Ecology of Running Water. University of Toronto Press, 

Toronto. 

Protection Agency, Office of Research and Development, Washington, D.C. 

coal ash dam. Y-SUBi86-479701-1, prepared by Geotek Englnecring Co. for the Oak 

Ridge Y-12 Plant. Oak Ridge, Tenn. 

Karr, J. R. 1981. Assessment of biotic intcgaity using fish communities. Fisheries. 

621-27. 

Karr, J. R. 1987. Biological monitoring and assessment: A conceptual framework. 

Environ. Manage. 1 13249-256. 

Karr, J. R., K. D. Fausch, P. L. Angermcier, P. R. Yant, and I. J. Scldosscr. 1986. 

Assessing biological integrity in running wateis: A method and its rationale. Illinois 

Natural History Survey Special Publication 5. Urbana, 111. 

Site. ORNLRM-9229. Oak Ridge National Laboratory, Oak Ridge? Tenn. 

minnow (Pkephales promelas) and Ceriodaphnin dubia toxicity tests. Ernvironmcntal 

Toxicology Chemistry (in press). 

Sciences Division Toxicology H aboratory standard operating procedures. OWN?,/TM11 194, Oak Ridge National I.aaboratory, Oak Midge, Tenn. 

Tmat, D. W. 1984. Agriculture and stream water quality: A biological evaluation of 

erosion control practices. Emviron. Manage. 8333-344. 

Tznat, D. R. 1988. Watcr quality assessment of streams using a qualitative collection 

method for benthic rnacroinvertebratcs. J. North hpn. Bemthol. Soc. 7222-233. 

Lxonard, P. M. and D. J. 01th. 1986. Application and testing of an Index of Biotic 

Integrity in small, coolwater streams. Trans. Arner. Fish. Soc. 1 15401-414. 

Lmar, J. M. (ed.). 1985. Application of habitat evaluation models in southern 

Appalachian trout streams. ORNL/llR.I-9323. Oak Ridge National I .aboiatory, Oak 

Ridge, Tenn. 

biomonitoring program: Concentrations of seven elements in freshwater fish, 

1978-1981. Arch. Environ. Contam. Toxicol. 14363-388. 

Printing Office, Washington, D.C. 

States Department of Energy, Oak Ridge facilities, calendar year 1384. ORNL-6209. 

Oak Ridge National Laboratory, Oak Ridge, Tenn. 

. Integrated Risk Information System (data base). U.S. Environrncntal 

Jones, R. A., and R. Mishu. 1986. Geotechnical and hydrologic @valuation of Y-12 Plant 

Ketelle, R. M., and D. D. Huff. 1984. Site characterizaikn of the West Chestnut Ridge 

Rs~os, I,. A., and A. J. Stewart. 1991. Effort-allocation analysis of the 7-d fathead 

Kszos, L. A., A. J. Stewart, L. IF. Wicker, and G. M. IBgsdon. 1989. Environmental 

lawe, T. P., T. W. May, W. G. Brurnbaugh, and D. A. Mane. 1985. National contaminant 

Mackenthun, K. M. 1973. Toward a Cleaner Aquatic Environment. US. Governinent 

Martin Marietta F,nergy Systems, Inc. 1985. Environmental monitoring report, United 
7-3 

Martin Marietta Energy Systems, Inc. 1986. Environmental surveillance of the Oak 

Ridge Reservation and surrounding environs during 1985. ORNL-6721.. Oak Ridge 

National Laboratory, Oak Ridge, Tenn. 

the Rogers Quarries. Y/SUB/85-00206C/4R1. Prepared by Geraughty and Miller, 

Inc. for thc Oak Ridge Y-12 Plant, April. 1986. Oak Ridge, Tenn. 

Murphy, 3. L. 1988. RCRA Facility investigation plan filled coal ash pond (D-112) Oak 

Ridge Y-12 Plant Oak Ridge, Tennew. Y/TS-411. Oak Ridge Y-12 Plant, Oak 

Ridge, Tcnn. 

Branch Oak Ridge Y-12 Plant Oak Ridge, Tennessee. Y/TS-488. Oak Ridge Y-12 

Plant, Oak Ridge, Tenn. 

McCauIey, Lo L. 1986. Proposed ground-water monitoring plans for the Ken- Hollow and 

Murphy, J. L., and J. M. Loar. 1988. Expanded RCRA facility investigation plan McCoy 

Pielou, E. C. 1977. Mathematical Ecology- John Wiiey, New York. 

Platts, W. S., Megahan, W. E, and Minshall, G. W. 1983. Methods for evaluating stream, 

riparian, and biotic conditions. U.S. Forest Service General Technical Report 

INT-138. Intermountain Forest and Range Experimental Station, Ogdon, Utah. 

Plant, the Oak Ridge Reservation, Tennessee. USGS 85- 165. Nashville, Tenn. 

Plant, thc Oak Ridge Reservation, Tennessce. USGS 85-553. Nashville, Tenn. 

estimating [ish population sizes and annual production rates. ORNLA’M-11061. 

Oak Ridge National Laboratory, Oak Ridge Tenn. 

RFI. 1987. RCRA Facility Investigation (RFI) guidance. Vol. III. Air and surface water 

releases. EPA 53O/SW-87-4#)1. Waste Management Division, Office of Solid Waste, 

US. Environmental Protection Agency, Washington, D.C. 

Rogers, J. G., K. L. Daniels, S. T. Goodpasture, C. W. Kimbrough, and E. W. Whitfield. 

1988. Environmental surveillancc of the U.S. Department of Energy Oak Ridge 

Reservation and surrounding cnvirons during 1987, Vol. 1: Narrative, summary and 

conclusions. ES/ESH4/Vl. Environmental and Safety Activities, Mart% Marietta 

Energy Systems, Inc., Oak Ridge, Tenn. 

Rogers, J, G., K. L. Daniels, S. T. Goodpasture, C. W. Kimbrough, and N. L. Prince. 

1989. Oak Ridge Rescrvation Envitonmental Report €or 1988, Vol. 1: Narrative, 

Summary and conclusions. ESESH-8Nl. Environmental and Safety Activities, 

Martin Marietta Energy Systems, Inc., Oak Ridge, Term. 

Ross, M. J. and G. R. Ultsch. 1980. Temperature and substate influence on habitat 

selection in two pleurocerid snails (Goniohasis). Am. Midl. Nat. 103:209-217. 

Rudd, J. W. M., M. A. Turner, B. E. Tmmsend, A. Swick, and A. Furutani. 1980. 

Dynamics of selcnium in mercury-contaminated experimental freshwater ecosystems. 

Can. J. Fish. Aquat. Sci. 37:848-857. 

Ryon, M. G., and J. M. Loar. 19%. A checklist of fishes on the Departmcnt of Energy 

Oak Ridge Reservation. J. Tenn. Acad. Sci. 58(4):97-102. 

SAS Institutc, Inc. 1985a. SAS User’s Guide: Basics, Version 5 edition. Sas Institutc, 

Inc., Cary, N.C. 

SAS Institute, Inc. 1985b. SAS User’s Guide: Statistics, Version 5 edition. SAS 

Institute, Inc., Cary, N.C. 

Pulliam, P. J. 198%. Water quality data for 34 sites, April and June 1984, near the Y-12 

Pulliam, P. J. 198%. Water quality data for 35 sites, September 1984, near the Y-12 

Railsback, S. F., B. D. Holcomb, and M. 6. Ryon. 1989. A computer program for 
7-4 

Smith, J. G. 1991a. Benthic mPr,hoinver‘Lebrates. In S. M. Imar, (ed.), First annual report 

on the U-12 Plant Biological Monitoring and Abatemerit Program, 

OWNLPTM- 10861. Oak Ridge National Laboratory, Oak Ridge, Term (in press)). 

effects of contaminants and remedial actions in Bear Creek, OWNL/TM-10370. Oak 

Ridge National Laboratory, Oak Ridge, Term. (in press). 

chronically exposed to selenium-laden effluent. Arch. Emiron. Contam. Toxicol. 

Smith, J, G lW?b. Benthic macrsinvertebratm- In G. R, Southworth, (ed.), Emlogical 

Sorensen, E. M. R., and T. I,. Bauer. 1983. IIcmatolsgical dyscrasia in telsosts 

12: 135-l46. 

Sorenscn, E. M. B.? 9. M. Curnbie, T. L. Batter, J. S. Bell, and C. W. Hax’lan. 1984. 

Histopathological, hematological, condition €actor, and organ weight changes 

associated with selenium accumulation in fish from Beleva Lake, North Carolina. 

Arch. Envircsn. Gontam. Toxicol. 13:153-262. 

Southwortk, G. R. 1391. Accumulation of c,ontaminanPs by biota in East E’ork Poplar 

Creek. In J. M. har, (e&), Fiist annual report on the Y-12 Plant Biological 

Monitoring and ‘4baterncnt Program. QRNIJIM-lO%l. Oak Ridge National 

Labcratory, Oak Ridgc, Tenn. (in press). 

Steel, W. G. D., and J. H. Torrie. 1980. Principles and procedures of statistics, 2nd Ed. 

McGraw-Ilill. New York. 

Stewart, A. J. 1990. Monitoring of conservative water quality factors in ORNL streams 

may be operationally advantageous. In Environmental Sciences Division Annual 

Progress Report for Period Ending Scptensber 30, 1989. ORNL-6602. Oak Ridge 

National Laboratory, Oak Ridge, Tenn. 

Stewart, A. J., L. A. Kszos, B. C. Harvey, L. F. Wicker, @. J. Maynes, and R. D. Bailey. 

1990. Ambient toxicity dynamics: Assessments using Ceri’sdapkraia dubids and fathead 

minnow (Pi~a’mephnks promebas) larvae in short-term te:,ts. Environ. Tsx- Chcm. 

S’DPII (Tennessee Department of Public Iicalth). 1978. Water quality management plan 

9367-379. 

for the Clinch River Basin. Division of Water Quality Control, Tennessee 

Departrnent of Public Ekalth, Nashville, Tenn. 

TVA (Tennessee Valley Authority). 1985. Instream cnntarninant study, Task 4: Fish 

sarnplhg and analysis. Report to U.S. Department of Energy, Oak Ridge Operations 

Office. Tennessce Valley Authority, Office of Natural Resources and Economic 

Development, MHIoxviilC, Tenn. 

Turner, M. la., and J. W. M. Rudd. 1983. The English-Wabigoon River system: 111. 

Selcniirin in lake enclosures: Its geochemistry, bioaccumulation, and ability to reduce 

mercury bioaccumulation. Can. J. Fish. Aquat. Sci. 40:2228-2240. 

Interaction between mercury and selenium accumulated from waterborne and dietary 

sources by northern pikc (Emx 1i~riz.u). Can. J. Fish. Aquat. Sci. 402241-2250. 

Y-12 Plant coal ash discharge to McCoy Branch. Y/TS-17%. Oak Ridge Y-12 Plant, 

Oak Kidge, Tenn. 

440/9-76-023, U. S. Environmental Protection Agency, Washiwgtori, D.C. 

waste. SW 846, 3d ed. Office of Solid Wastc and Emergency Rcspons&, 

Washington, D.C. 

Turner, M. A., and ‘4. 1,. Swick. 1983. The: English-Wabigoon River system: iV. 

Turner, R. R., M. A. Bogle, M. A. Kane, and 7”. M. Mercer. 1986. Characterizatkm of 

EP.4 (U. S. Emvironmental Protection Agcacy). 1976. QiraBiiy Criteria for Water. EPA 

EPA (U. S. Environmental Protcction Agency). 19%. Test niethods for evaluating solid 
7-5 

EPA (U.S. Environmental Protection Agency). 1990. Region IV toxic substances 

spreadsheet. U. S. EPA, Region IV, Atlanta, Georgia. July 1990. Unpublished 

mimeo, 8 pp. 

Ward, J. V. and J. A. Stanford (eds.). 1979. The Ecology of Regulated Streams. Plenum 

Press, New York. 

Weber, C. I. (ed.). 1973. Siological field and laboratory methods for measuring the 

quality of surface waters and effluents. EPA 670/4-73-001. National Environmental 

Research Ccn ter, U.S. Environmental Protection Agency, Cincinnati. 

Weber, C. I., W. H. Peltier, T. J. Norberg-King, W. B. Horning, F. A. Kessler, 

J. R. Mendedick, T. W. Neiheisel, P. A. Lewis, D. J. Klemm, Q. H. Pickering, 

E. L. Robinson, J. M. Lazorchak, L. J. Wymer, and R. W. Freyberg. 2989. Shortterm methods For estimating the chronic toxicity of effiuents and receiving waters to 

freshwater organisms. EPA/600/4-89/002, Environmental Monitoring Systems 

Laboratory, Cincinnati. 

Wiederholm, T. 1984. Responses of aquatic insects to environmental pollution. pp. 

508-557. In V. H. Resh and D. M. Roscnberg, (eds.), The ecology of aquatic 

insects. Praeger Pubiishers, New York. 

APPENDIX A 

WATER QUALITY DATA FOR MCCOY BRANCH WATI3RSHED 

FOR 1974-1990 

A-3 

Table A-1. Water quality data collected in 1984 for two sites in the 

McCoy Branch watershe@ 

April & June Sept. 

1984 1984 

site site site 

Parameter Upstream Downstream Downstream 

Alkalinity, lab (m@ as CaCO,) 

Alkalinity, field (mgL as CaCO,) 

Arsenic, total (& as As) 

Barium, total recoverable (& as Ba) 

Beryllium, total recoverable (@ as Be) 

Cadmium, total recoverable (pg/L as Cd) 

Calcium, dissolved (mg/L as Ca) 

Carbon, organic total (ma as C) 

Carbon, organic dissolved (mgL as C) 

Chloride, dissolved (ma as C1) 

Chromium, Total recoverable (a as Cr) 

Cobalt, total recoverable (p/L as Co) 

Cobalt, total recoverable (a) 

Copper, total recoverable (pa as Cu) 

Cyanide, total (m@ as CN) 

Gross Beta, dissolvcd (pCi/L as (3-137) 

Gross Alpha, susp. total (pg& as U-NAT) 

Gross Beta, susp. total (pCi/L as 0-137) 

Gross Beta, dissolved (pCiL as Sr/Y-90) 

Gross Alpha, dissolved (pgL as U-NAT) 

Gross Beta, susp. total (pCi/L as Srfl-90) 

lnstantaneous discharge (L/s) 

Iron, total recoverable (fig& as Fe) 

Lead, total recoverable (fi@ as Pb) 

Lithium, total recoverable (pa as Li) 

Magnesium, dissolved (mgiL as Mg) 

Manganese, total rccoverable (lLg/Id as Mn) 

Mercury, total recoverable (p@ as Hg) 

Molybdenum, total recoverable (fig/L as No) 

Nickel, total recoverablc (pgL as Ni) 

Nitrogen, NO,+NO, dissolved (rnc as N) 

Nitrogen, ammonia + organic total (m@ as N) 

Nitrogen, ammonia dissolved (mgL as N) 

Oxygen, dissolved (rng/L) 

Phosphorus, dissolved (mg/L as P) 

Phosphorus, ortho-dissolved (m& as P) 

Phosphorus, total (mgiL as P) 

Potassium, dissolved (ma as Na) 

Selenium, total (pg/L 3s Se) 

Sodium, dissolvcd (ms/I., as Na) 

Solids residue at 180 ' C, dissolved (m&) 

143 

NA 

NA 

100 

c 10 

e1 

41 

0.40 

NA 

2.7 

3 

NA 

10 

1 

40.01 

NA 

NA 

NA 

NA 

NA 

NA 

7.7 

1600 

5 

90 

13 

loo0 

<0.1 

11 

NA 

NA 

NA 

NA 

NA 

NA 

NA 

23 1 

0.100 

0.030 

4.5 

2.5 

111 

NA 

NA 

100 

c 10 

<1 

40 

0.70 

NA 

3.8 

7 

NA 

1 

4 

<0.01 

c2.6 

2.4 

1.9 

< 2.2 

~4.6 

1.7 

87.8 

290 

5 

90 

9.7 

50 

€0.1 

32 

NA 

<0.1 

NA 

NA 

12.6 

0.080 

NA 

NA 

NA 

204 

3.1 

3.3 

NA 

78 

110 

100 

< 10 

c1 

32 

NA 

2.7 

3.6 

<1 

<1 

NA 

1 

<a01 

2.6 

0.8 

0.7 

2.2 

<4.3 

0.6 

50.9 

390 

3 

70 

7 

20 

<0.1 

35 

1 

3.2 

0.50 

co.01 

9.5 

co.01 

0.02 

0.04 

3.2 

8 

3.3 

1 (jj 
A-4 

Parameter 

April & June Sept. 

1386 1984 

_l_l_.._. ." - 

Upstream Downstream Downstream 

site site ste 

Specific condrictance (pS/cm) 

Strontium, total recovcrable (& as Sr) 

Sulfate, dissolved (mg/L as SO,) 

Temperature(" C) 

Uranium, natural dissolved (& as U) 

Vanadium, dissolved (pg/L. as V) 

Zinc, total reWvCiable (pgL as Zn) 

360 324 250 

'770 230 ,250 

34 4s 50 

12.5 12.0 19.0 

1.0 2.5 2.2 

<1 30 23 

20 20 10 

The upstream site is locatcd between the ash pond and Rogers Quarry. The downstream site 

is located below Rogers Quarry. Data for some sites were not available (NA). Sources: P. 9. Pblllium 

(198% and 1985b). 
Table A-2 Water analyses for McCoy Branch, November 1974-March 1975" 

Sample montwstation - 

Parameter Nov NOV Nov Dec Dee 

1 2 2 C 2 

Jan Mar 

2 2 

Temp ("C) 

Turbidiv 

Sus solids 

Dis solids 

Dis oxygen 

Alkalinity 

Hardness" 

Al - Dis 

AI - sus 

Cd - Dis 

Cd - SUS 

Cr - Dis 

Cr - Sus 

Cu - Dis 

cu - sus 

Mn - Dis 

Mn - Sus 

Pb - Dis 

Zn - Dis 

Zn - Sus 

U 

PH 

Pb - SUS 

Hg 

NO3 

11 

17500 

253 

6.4 

7.53 

48 

151 

0.15 

171.0 

<0.002 

<0.002 

<0.01 

CO.01 

<0.004 

0.500 

0.020 

0.580 

<0.010 

0.16 

0.008 

10 

13 

182 

9.1 

7.74 

80 

126 

< 0.05 

0.24 

<0.002 

<om2 

<0.01 

<0.01 

< 0.004 

0.004 

0.010 

<0.010 

<0.010 

<OB1 

<0.005 

12 

5.0 

27 

159 

7.2 

7.39 

82 

121 

c 0.05 

0.52 

<0.002 

c0.002 

dI.01 

KO.01 

<0.004 

CO.004 

0.020 

<O.OlO 

0.020 

<0.01 

0.07 

<OB2 

~0.005 

<om 

< 1.0 

12 

15.0 

100 

101 

10.5 

6.73 

81 

81 

<0.002 

<0.002 

<0.01 

<0.01 

< 0.004 

<0.004 

<0.010 

0.055 

0.017 

<0.01 

c0.005 

c0.01 

1.4 

10 

6.0 

37 

130 

10.6 

7.43 

55 

90 

<0.002 

€0.002 

c0.01 

<0.01 

< 0.004 

<0.004 

0.019 

0.010 

0.021 

co.01 

<OB05 

4.01 

0.7 

9 

12.0 

40 

188 

9.2 

7.65 

6 

113 

~0.05 

0.49 

<0.m 

<0.002 

CO.01 

eo.01 

<O.W 

c 0.004 

0.015 

0.018 

0.010 

co.01 

0.07 

c0.02 

<0.005 

<0.01 

<0.9 

9 

9.5 

22 

118 

11.2 

8.02 

101 

<0.05 

0.20 

<0.002 

< 0.002 

<0.01 

c0.01 

< 0.004 

co.004 

rf 

Ul 

<0.010 

c0.01 

4.005 

c0.01 

2.4 
Parameter 

Sample month/starion 

NOV NOV Nav Dec DeC Jan Mar 

I 2 M 9 C 2 2 L 

1 

0.10 

0.02 

6 

I -0 

1 .o 

0.50 

< 0.04 

0.20 

0.06 

0.01 

6 

0.4 

1 .o 

0.20 

< 0.04 

3.00 

1.1 

0.06 

0.01 

6 

0.4 

1 .o 

CO.01 

<0.04 

8.40 

2. ii 

33 

0.10 

0.01 

10 

6 0.2 

2.0 

0.15 

<0.04 

1.08 

2.2 

94 

0.15 

0.01 

2 

c 0.2 

0.4 

0.08 

<8.W 

0.15 

1 .o 

fi8 

8-06 

0.01 

3 

0.6 

1.8 

< 1.80 

< 0.04 

0.416 

1.3 

32 

0.06 

0.01 

6 

0.4 

1.5 

0.30 

CO.04 

0.40 

? 

a 

'Stations 1 (200 rn above Rogers Quarry), 2 (200 rn below the quarry) and C (Control site on weslern branch of McCoy 

9urbidicq as SiO,. 

'Wardness as CaCO,. 

Branch). Dis = dissolved; Sus = suspended; all parameters in ma. Sauce: ERDA 1975. 
Table A-3. ConcenUdtions (mean values) and mass loadings of nonmetal pollutants. Zess than' prefixes have been ignored in calculating 

mean concentration values. Sourcflurner et al. 1986 

Nonmetals 

Intake water 

Concentration Mass 

(ma> ( 1 b/d) 

MBK 1.17 (Ash sluice)" Spring 

Concentration Mass Concentration Mass 

(m!YL> (Ib/cl) (m&) (Wd) 

Ammonia nitrogen 

Biological o.qgen demand (BOD) 

Bromide 

Chemical oxygen demand (COD) 

Chloride 

Chlorine, total residual 

Cyanide, total 

Fluoride 

Nitrate-nitrite nitrogen 

Oil and grease 

Phenols, total 

Phosphorus, total (as P) 

Sulfate (as SO,) 

Sulfide (as S) 

Sulfide (HACH HS-7) 

Sulfite (as SO,) 

Total alkalinity 

Total kjeldahl nitrogen 

Total suspended solids 

Total organic carbon (TOC) 

0.100 

5.OOO 

1.00 

6.333 

6.730 

1.150 

0.002 

0.500 

0.330 

2.000 

0.001 

0.240 

26.333 

0.133 

O.Oo0 

0.500 

108.333 

0.220 

18.667 

1.600 

0.690 

34.500 

6.900 

43.700 

46.437 

7.335 

0.01 1 

3.450 

2.277 

13.800 

0.007 

1.656 

181.700 

0.920 

0.OOO 

3.450 

747.500 

1.518 

128.800 

11.040 

0.15 

6.00 

1.00 

4.90 

6.33 

0.07 

0.00 

1.05 

0.15 

2.44 

0.00 

16.75 

253.90 

22.24 

0.00 

0.53 

40.00 . 

0.98 

9919.20 

0.50 

1.0 

41.4 

6.9 

33.8 

43.7 

0.5 

0.0 

7.3 

1.1 

16.9 

0.0 

115.6 

1751.9 

153.5 

0.0 

3.0 

276.0 

6.8 

68442.5 

2.7 

0.100 

5.000 

LOO0 

3.000 

4.026 

0.000 

0.m1 

0.500 

0.010 

2.250 

0.001 

0.380 

57.600 

0.100 

0.0oO 

0.400 

135.000 

0.200 

39.400 

0.500 

0.080 

3.984 

0.797 

2.390 

3.208 

0.000 

0.001 

0.398 

0.008 

1.793 

0.001 

0.303 

45.8% 

0.080 

0.000 

0.319 

107.568 

0,159 

31.394 

0.398 

Fp 

4 

~ ~ ~~ 

"Site is equivalent to MCK 2.65. 
Auminm 

hrimony 

Arsenic (US) 

Barium 

Beryllium 

Boron 

Cadmium 

Calcium 

Chromium 

Cobalt 

Copper 

Gallium 

Iron 

Lead 

Lithium 

Magnesium 

Manganese 

Mercury (AAS) 

Molybdenum 

Nickel 

Potassium 

Selenium (AAS? 

Silicon 

Silver 

Sodium 

Strontium 

Thallium (AM) 

Tin 

Titanium 

Uranium 

Vsnadium 

Zirconium 

ZiRC 

0.1oOo 

0.0200 

0.ooso 

0.0440 

c1.0002 

O.OU80 

O.uCKl5 

3S.OOQO 

0.0040 

0.0010 

0.0350 

0.0300 

0.3300 

0.0200 

0.0250 

9.1m 

0.0360 

NMb 

0.0040 

0.W 

1.7ooO 

0.0050 

1.m 

0.0050 

6.6oc#) 

0.0470 

0.0010 

@.W50 

0.w20 

0.010e3 

O.W% 

0.0020 

0.0020 

0.690 

0.138 

0.034 

0.304 

0.OOIc)i 

0.055 

0.003 

24 1.500 

0.028 

0.007 

0.24 I 

0.207 

2.277 

0.138 

0.172 

42.790 

0.248 

NM 

0.023 

0.04 L 

11.930 

0.034 

13.110 

0.034 

59.340 

0.562 

0.007 

0.034 

0.014 

0.069 

0.017 

0.014 

0.014 

31o.m 

0.260 

4.933 

0.533 

0.057 

1.5w 

0.010 

142.667 

0.253 

0.141 

0.983 

0.420 

133.333 

0.367 

2.533 

32.667 

0933 

0.009 

0.167 

0.353 

43-SOO 

0.243 

2.417 

0.087 

20.OO0 

7.m 

0.120 

0.105 

8.033 

0.010 

I .447 

0.453 

0.091 

2 139.00 

1.93 

34.04 

3.68 

0.40 

10.35 

0.07 

934.40 

1.75 

0.98 

6.78 

2.90 

920.M) 

2.53 

17.48 

225.40 

6.23 

0.06 

1.15 

2.4 

300.15 

1.68 

16.67 

0.60 

138.00 

54.5 i 

0.83 

0.72 

55.43 

0.07 

4 1.34 

3.13 

0.63 

0.0200 

3.0209 

0.03OcI 

0.0740 

0.0002 

0.3300 

0.m5 

48.m 

0.0040 

0.0032 

0.0020 

0.0300 

0.4300 

Q.0200 

0.3m 

14.oc##) 

0.53410 

Q.Oo0 1 

0.0100 

0.W60 

6.2W 

0.0050 

4.4m 

0.0050 

4.m 

0.9100 

0.m 10 

0.0050 

O.w 

0.01M3 

0.0024 

0.0020 

0.W20 

0.0153 

0.8159 

0.0239 

0.0590 

O.ooO2 

0.2629 

O.ooo4 

38.2464 

o.003:2 

0m25 

0.0016 

0.0239 

0.3426 

0.0159 

0.2390 

4 1.1552 

19.4223 03 

43.ooo1 

o.Oo80 

0.m 

4.9402 

0.m 

3.5059 

O.m 

5.4152 

0.m 1 

P9. 

0.w 

0.0035 

0.W) 

0.m19 

0.003016 

0.00 16 

? 

"Site is eqJivaleni :o MCK 2.55. 

'NM = not measured. 
Table A-5. Cowentratiws (mean values) anxf mass loadings of total remverabie metals. ‘Less ulan’ prefixes have been ignored in calculating rtxan 

amcentration values Source: Turner et al. 1986 

Total 

recoverable 

metals 

Intake water MBK 1.17 (Ash sluice). Spring 

Concentration Mass Concentration Mass Concentration Mass 

{lb/d) (ma) (Wd) (ma) ( Wd) 

Aluminum 

Antimony 

Arsenic (US) 

Barium 

Beryllium 

Boron 

Cadmium 

Calcium 

Chromium 

Cobalt 

Gallium 

Iron 

Lead 

Lithium 

Magnesium 

Manganese 

Mercury @AS) 

Molybdenum 

Nickel 

Potassium 

Selenium (M) 

Silicon 

Silver 

Sodium 

Strontium 

Thallium (AAS) 

Tin 

Titanium 

Uranium 

Vanadium 

%inc 

Zirconium 

Copper 

0.1905 

0.1100 

0.0050 

0.0300 

0.001 1 

0.0440 

0.0027 

37.oooo 

0.0220 

0.0055 

0.0133 

0.1650 

0.2250 

0.1100 

0.1100 

9,7000 

0.0755 

o.ooo1 

0.0220 

0.0330 

1 .m 

0.0050 

0.8600 

0.0275 

6.2000 

0.1025 

0.0010 

0.0275 

0.0110 

0.0100 

0.0061 

0.0170 

0.0110 

1.3 14 

0.759 

0.034 

0.207 

0.008 

0.304 

0.019 

255.300 

0.152 

0.038 

0.092 

1.138 

1.552 

0.759 

0.759 

66.930 

0.521 

0.001 

0.152 

0.228 

12.420 

0.034 

5.934 

0.190 

42.780 

0.707 

0.007 

0.190 

0.076 

0.069 

0.042 

0.117 

0.016 

228.857 

0.187 

2.97 1 

3.086 

0.038 

1.814 

0.005 

151.429 

0.224 

0.098 

0.720 

0.280 

141.571 

0.2.63 

2.650 

29.7 14 

0.616 

0.010 

0.233 

0.260 

60.400 

0.189 

19.214 

0.049 

33.143 

5.033 

0.057 

0.047 

5.767 

0.023 

1.321 

0.396 

0.061 

1579.1 1 

1.29 

20.50 

21.29 

0.26 

12.52 

0.03 

1044.86 

1.55 

0.68 

4.97 

1.93 

976.84 

1.81 

18.28 

205.03 

4.25 

0.01 

1.61 

1.79 

416.76 

1.30 

132.58 

0.33 

228.69 

34.73 

0.39 

0.32 

39.79 

0.16 

9.12 

2.73 

0.42 

0.1607 

0.1100 

0.0265 

0.0722 

0.0015 

0.2750 

0.0040 

45.5000 

0.03 17 

0.0080 

0.0155 

0.1650 

0.5275 

0,1550 

0.2050 

13.5000 

0.4825 

o.Oo01 

0.0323 

0.0465 

4.9750 

0.0050 

5.2350 

0.0387 

4.1500 

0.9700 

0.0010 

0.0275 

0.01 10 

0.0.550 

0.o080 

0.0169 

0.01 10 

0.1281 

0.0876 

0.021 I 

0.0576 

0.0012 

0.2191 

0.0032 

36.2544 

0.0252 

0.0064 

0.0124 

0.1315 

0.4203 

0.1235 

0.1633 

10.7568 

0.3845 

o.Ooo1 

0.0257 

0.0371 

3.9641 

0.0040 

4.1712 

0.0309 

3.3067 

0.7729 

O.OOO8 

0.0219 

0.0088 

0.0438 

0.0064 

0.0135 

0.0088 

9 

b 

“Site is equivalent to MCK 2.65. 
Total 

dissolved 

metals 

lnrake watzr MBK 1.:7 (Ash s1u;iz)" Spring 

Concentration Mass Concentration Mas§ Concentration Mass 

(mglL,) (!bid) (mg/Li (lb/d) jm@) (Ib,Gj 

- 

Auminum 

Antimony 

Barium 

Bcrj41um 

Boron 

Cadnxum 

Calcium 

Chroni urn 

ArSCI?iZ (AAS) 

Cobalt 

Copper 

Gallrum 

Iron 

Lithium 

Magnesium 

Manganese 

Mercury (AAS) 

Molybdenum 

Nickel 

Potassium 

Se!enium (AAS j 

Silicon 

Siiver 

S&ium 

Strontium 

Thaliium (MS) 

Tin 

Titanium 

Uranium 

Vanadium 

Zinc 

Zirconium 

0.290 

0.2063 

0.m5 

0.034 

0.002 

0.080 

0.005 

37.K?O 

0.040 

0.0 10 

0.020 

0.300 

0.200 

0.200 

1 i.Oo0 

0.005 

NMB 

0.040 

0.060 

1.700 

0.005 

1.200 

0.050 

7.300 

0.120 

0.001 

0.050 

0.020 

0.010 

0.010 

0.020 

0.020 

1.380 

1.3m 

0.034 

0.235 

0.014 

0.552 

0.034 

255.309 

0.276 

0.049 

0.138 

2.070 

1.380 

1.380 

7s.m 

NM 

0.276 

0.414 

11 .I30 

0.034 

8.280 

0.345 

50.370 

0.828 

0.007 

0.345 

0.138 

0.069 

0.069 

0.138 

0.198 

o.eu 

G.8667 

0.2m 

0.3567 

0.1767 

0.8020 

0.07113 

0.C6)SO 

89.6567 

0.04m 

0.0200 

0.02w 

0.9000 

0.2000 

1.4200 

12.3333 

0.0203 

NM 

0.3033 

0.m 

17.m 

0.0227 

1.5647 

0.0500 

15.6667 

0.8167 

a.w1o 

0.0508 

0.0200 

0.0100 

0.0873 

0.02CBcI 

0.02ftG 

S.980 

1.38:3 

2.461 

1.219 

0.014 

6.716 

0.034 

618.700 

0.276 

0.069 

0.138 

2.070 

1.3811 

9.798 

85.100 

0.140 

NM 

2.093 

0.414 

I 17.308 

0.156 

10.810 

0.345 

1%3.100 

5.635 

0.007 

0.345 

0.133 

0.069 

0.603 

0.138 

0.138 

0.200 

0.2m 

0.020 

0.082 

0.002 

0.400 

0.005 

55.000 

0.040 

0.0 lG 

0.020 

0.300 

0.200 

0.206) 

16.m 

0.480 

NM 

O*MO 

0.060 

5.400 

0.005 

7.700 

0.050 

3.m 

I .m 

0.001 

0.050 

0.020 

0.010 

0.01 1 

0. om 

0.020 

8.1594 

0.1594 

0.01S9 

d.m53 

0.0016 

0.3187 

0.0040 

43.8240 

0.03 19 

0.0080 

0.8159 

0.23% 

0.1594 

0.1554 

12.74B 

NM 

0.03 19 

0.0478 

4.3027 

0.0040 

6.1354 

0.0398 

3.1075 

0.7965 

0.00198 

0.0358 

0.0158 

0.m 

0.m 

0.019 

0.0159 

0.3825 B + 

0 

'Site is equivaienr to MGK 2.55. 

%" = n3t measured. 
A-11 

Table A-7. Sample tM)es and locations for surface water, groundwater, coal ash, and 

floodplain sediment samples of McCoy Branch, Jdy WOctober 17,1990. 

Source: CH2M Hill, personal communication 

Dry Weather Surface Water Sampling, July 30, 1990 

Sample No. Approximate stream Sample type 

location 

S3 

s4 

s5 

S6 

MCR 2.62 Environmental - Aqueous 

MCK 2.52 Environmental - Aqueous 

MCK 1.92 Environmental - Aqueous 

MCK 1.92 Duplicate of S5 

Wet Weather Water Sampling, October 8, 1W 

Sample No. Approximate stream Sample type 

location 

ww-SI MCK 1.92 Environmental - Aqueous 

ww-s3 MCK 2.62 Environmental - Aqueous 

ww-s4 MCK 2.52 Environmental - Aqueous 

WW-S6 --- Field Blank - Aqueous 

ww-s7 --- Equipment Blank - Aqueous 

~~ 

Groundwater sampling 

Sample No. Location Approximate stream Sample date 

loca t ionb 

5000 

500 1 

5002 

5003 

5004 

5005 

5006 

5007 

GW-321 

GW-672 

GW-673 

GW-674 

GW-676 

GW-676 

GW-676 

G W-672 

MCK 2.62 

MCK 2.61 

MCK 2.40 

MCK 2.38 

MCK 2.14 

MCK 2-14 

MCK 2.24 

MCK 2.61 

16 om 90 

15 OCT 90 

16 OCT 90 

16 OCT 90 

17 om 9c) 

17 om 90 

17 OCTW 

15 OCT 90 
A-12 

AsWSoil Sampling 

Sample No. Location Approximate Sample :.e' 

stream locationb 

Al-S4 

A1 -52 

A2-A 

AZSI 

A.3-A 

AM1 

Ax32 

A4 -A 

A431 

A4S2 

AS-A 

A5-Sl 

A5S2 

A6 -A 

ASS1 

Af;-S'& 

A7-A 

A7-Sl 

A732 

A1 

A1 

A2 

A2 

'$3 

A3 

A3 

A4 

A4 

A4 

'45 

AS 

A5 

A6 

A4 

A6 

A3 

A3 

A3 

MCK 2.38 

MCK 2.38 

MCK 2.62 

MCK 2.62 

MCK 2.52 

MCK 2.52 

MCM 2.52 

MCK 2-40 

MCM 2.40 

MCK 2-40 

MCK 2.10 

MCM 2.10 

MCK 2.10 

MCK 1.97 

MCK 1.97 

MCK 1.97 

MCK 2-52 

MCK 2.52 

MCK 2.52 

Environmental Soil 

Ermvirotirnentd Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environrncntal Soil 

Emkonmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

Environmental Soil 

(0-B" BE) 

(6-62" BL) 

(8-6" Bh) 

(ASH) 

(ASH) 

(0-6'' BA) 

(6- 12" B A) 

(ASH) 

(8-6" BA) 

(6- 12" BA) 

(ASH) 

(0-6" BA) 

(ASW 

(6-12" BA) 

(0-6" BA) 

(6-12" BA) 

(ASH) 

(0-6" €3'4) 

(6-12'; BA) 

"Wet weather sample taken after a 4.5-cm rain event, measured at the gage at 

bLmation in terms of stream kilometers; actual sample sites are located in floodplain 

'%A = Bclow ash; BL = Below !and. 

Rogers Quarry. 

and may be sevcral meters cast or west from stream kilometer. 
A-13 

Table A-8. Concentrations of volatile organic compounds measured in surface 

water samples of McCoy Branch, July 30,1990- 

Source: CH2M Hill, personal communication 

Compound Site 

(PE/L) 

MCK 2.62 MCK 2.52 MCK 1.92 MCK 1.92" 

1,1 -Dichloroethane 

1,l-Dichloroethene 

l,l,l-Trichloroethane 

l,l,Z-TrichIoroethane 

1,1,2,2-Tetrachloroethane 

1,ZDichloroethanc 

1,ZDichtoroe thane4.l" 

1,2-Dichloroethene (Total) 

1,2-Dichloropropane 

2-Bu tanone 

2- Herdnone 

4-Methyl-2-Pen tanone 

Acetone 

Benzene 

Bromodichloromethane 

Bromofluorobenzene" 

Bromoform 

Bromomethane 

Carbon disulfide 

Carbon tetrachloride 

Chlorobenzenc 

Chloroethane 

Chloroform 

Chloromethane 

cis-1,3-Dichloropropene 

Dibromochlorome thane 

Ethylbenzenc 

Methylene chloride 

Styrene 

Te trachloroe them 

Toluene 

Toluene-d8" 

Total xylenes 

trans-l,-?-Dichloropropene 

5 

5 

5 

5 UJb 

5 

5 

49.5 

5 

5 

10 

20 

10 

7 UJ 

5 

5 

53.9 

5 UJ 

10 

5 

5 

5 

10 

5 

10 

5 UJ 

5 UJ 

5 

5 

5 

5 

5 

54.4 

5 

5 UJ 

5 

5 

5 

5 UJ 

5 

5 

48.5 

5 

5 

10 

10 

10 

6 UJ 

5 

5 

57.4 

5 UJ 

10 

5 

5 

5 

10 

5 

10 

5 UJ 

5 UJ 

5 

5 

5 

5 

5 

54.9 

5 

5 UJ 

5 

5 

5 

5 UJ 

5 

5 

49.1 

5 

5 

10 

10 

10 

19 UJ 

5 

5 

53.6 

5 UJ 

10 

5 

5 

5 

10 

5 

10 

5 UJ 

5 UJ 

5 

5 

5 

5 

5 

53.8 

5 

5 UJ 

5 

5 

5 

5 UJ 

5 

5 

49.2 

5 

5 

10 

10 

10 

5 UJ 

5 

5 

52.5 

5 UJ 

10 

5 

5 

5 

10 

5 

10 

5 UJ 

5 UJ 

5 

5 

5 

5 

5 

53.5 

5 

5 UJ 
A-14 

Site 

MCK 2.62 MCK 2.52 MCK 1.92 MCK 1.9T 

I I_ 

Coin po u nd 

( WglL) 

-_ 

Trichloroethene 

Vinyl chloride 

Vinyl acetate 

5 

10 

2 UJ 

5 

10 

2 UJ 

5 

10 

2 UJ 

5 

10 

2 UJ 

%uplicatc samples, 

bS = estimated value; U = undeteeted-below method detection level. 

‘Tentatively identified compounds. 
A-15 

Table A-9. Concentrations of semivolatile organic compounds measured in surface 

water samples from McCoy Branch, July 30,19Po. 

Source: CH2M Hill, personal communication 

Compound MCK 2.62 MCK 2.52 MCK 1.92 MCK 1.92" 

(Pa) 

1,2-Dichlorobenzene 

1,2,4-Trichlorobenzene 

1,3-Dichlorobenzene 

1,4-Dichlroben~ene 

2-Chloronaphthalene 

2-Chlorophenol 

2-Methylnaphthalene 

2-Me t hylphenol 

2-Nitroaniline 

2-Nitrophenol 

2,4-Dichlorophenol 

2,4-Dimcthylphenol 

2,4-Dinitrophenol 

2,4-Dinitrotoluene 

2,4,5-Trichlorophenol 

2,4,6-Trichlorophcnol 

&ti-Dinitrotoluene 

3-Nitroaniline 

3,3'-Dichlorobenzidine 

4-B ro mop hen y 1 - p hen yle t her 

4-Chloro-3-me thylphenol 

4-Chloroaniline 

4-Chiorophenyl-phenyle ther 

4-Me thylphenol 

4-Nitroaniline 

4-Ni trop hen01 

4,6-Dinitro-2-methylphenol 

Acenaphthenc 

Acenaphthylene 

Anthracene 

Benzo( a)pyrenc 

Benzo( a,h)anthraccnc 

Benzo(h)fluorant bene 

Benzo (g, h, i) perylene 

Benzo( k)fluoran thcne 

10 

10 u 

10 u 

10 

10 u 

Rb 

30 u 

R 

50 

R 

R 

R 

R 

10 

R 

R 

10 u 

50 U 

20 

10 

R 

10 

10 

R 

50 

R 

R 

10 u 

10 

10 

10 

10 

10 

10 

10 

10 UJb 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

R 

10 UJ 

R 

50 UJ 

R 

R 

R 

R 

10 UJ 

R 

R 

10 UJ 

50 UJ 

20 UJ 

10 UJ 

R 

10 UJ 

10 UJ 

R 

50 UJ 

R 

R 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

50 UJ 

10 UJ 

10 UJ 

10 UJ 

50 UJ 

10 UJ 

50 UJ 

10 UJ 

10 UJ 

50 UJ 

20 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

50 UJ 

50 UJ 

50 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

SO UJ 

10 UJ 

10 UJ 

10 UJ 

50 UJ 

10 UJ 

50 UJ 

10 UJ 

10 UJ 

50 UJ 

20 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

50 UJ 

50 UJ 

50 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 IJJ 

10 UJ 

10 UJ 

10 UJ 
A-16 

Conmpollnd MCK 2.62 MCK 2.52 MCK 1.92 MCK 1.9Y 

(Pa) -__I 

Bca-rzoic Acid 

bIs(2-elPloroeBPioxy)methaase 

bis(2-Chloroetlnyl) Ether 

bis(2-ckil~rsisopropyl)ether 

BGIIlZjd AkQhOl 

bis(2-Ethylhe~cyl)pht~~~a~~ 

Butylbenzylphthalate 

Chrysewe 

Di-n-butylphthalate 

Di-n-octylphthalate 

Dibenzqa,h)an~hracene 

Dibenzsfaasaii 

Diethylphthalate 

Dime t by1 p h t hala t e 

Huoranthene 

Flu oren e 

Hexachlorethane 

Hexachlorobenzene 

Mexachlorocydobu tadienc: 

flcxachlorocyclo yen tadierie 

I Ecxanc, 3-methoxy 

Indeno(l,2,3-cd)pyrene 

Isophsrone 

N-Nitrosc-Di-n-propylamine 

N-Nitrosodiphenylamine (1) 

Napthalerae 

Nitrobenzene 

Phenanthrene 

Phenol 

E~cntachZorophenol 

ryrcne 

Unknown 

Unknown 

R 

10 

10 u 

10 u 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

R 

10 UJ 

R 

10 UJ 

4.92 UJ 

7.06 UJ 

I% 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

27 J 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 us 

10 UJ 

10 UJ 

10 UJ 

4.87 UJ 

10 UY 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

R 

10 UJ 

R 

10 UJ 

4.79 UJ 

50 UJ 

10 UJ 

10 UJ 

10 UJ 

10 u9 

10 IJJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UY 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

50 UJ 

10 UJ 

10 UJ 

10 UJ 

4.91 UJ 

50 UJ 

10 UJ 

10 UJ 

10 u9 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 us 

10 IJJ 

10 UJ 

10 UJ 

10 UJ 

10 UY 

10 UY 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

10 UJ 

50 UJ 

10 UJ 

10 UJ 

10 UJ 

4.87 UJ 

9.33 UJ 

“Dupkate sample taken at MCM 1.92. 

bJ = estimated value; R = rejected value; U = undetccted-below nmcthod detection 

levcl. 
Table A-10. Water quality data for surface water samples of McCoy Branch, July 30, 1990. 

Source: CH2M Hill, personal communication 

Parameter 

mgiL unless otherwise noted MCK 2.62 MCK 2.52 MCK 1.92 MCK 1.92" 

Alpha activity (pCi/L) 

Beta activity (pCi,rL) 

Alkalinity 

Chloride IC 

Conductivity (pmho/cm) 

Dissolved solids 

Fluoride IC 

Nitrate 

Phenols 

Sulfate 

Suspended solids 

Total organic carbon (TOC) 

Total organic halides (TOX) (p&) 

Uranium-fluorometric 

PH 

378.67 i 67.2 

936.17 + 114.7 

148 

3 

340 

180 

0.2 

<1 UP 

7.4 

0.03 J 

24 

5 

<1 

10 J 

0.001 

352.13 * 64.9 

580.17 f 99.6 

159 

2 

339 

180 

0.2 

<I UJ 

7.8 

C0.03 UJ 

26 

8 

<1 

<10 UJ 

0.001 

-143 * 160 UJ 

164 

2 

335 

168 

0.2 

1J 

7.9 

~0.03 UJ 

14 

1 

c1 

<lo U3 

<0.001 

-22.35 * 350 U 

~ ~- 

-1.27 * 160 UJ 

161 

2 

334 

174 

0.2 

1J 

8 

<0.03 UJ 

14 

2 

<1 

16 J 

<0.001 

-33.53 f 330 u 

? 

c-r 

4 

- 

"Duplicate sample taken at MCK 1.92. 

'J = estimated value; R = rejected value; U = undetected4elow method detection level. 
A-18 

Ju$ 303 1990- Sites EabW 

1_1 

Source: CII2M I-IiII, pcrsonal communication 

Element MCK MCK MCK MCK MCK MCK iMCK MCK 

(PHI>) 2.62 2.62-F 2.52 2.52-F 1.92 1.92-F 1.92 1.92-P 

Aliirnioum 

Antimony 

Arsenic 

Flanum 

B~~-J~IIu~ 

Cadmium 

Calcium 

Chromium 

Cobalt 

Copper 

Iron 

Lead 

Magnesium 

Manganese 

Mercury 

Nickel 

Niobium 

Phosphorous 

Pot assium 

Selenium 

Silvcr 

Sodiiirn 

Vanadium 

Linc 

129 Jb 

50.0 

84.8 

60.6 

0.30 

3.0 

43900 

10.0 

5.0 

4.0 

1360 

0.80 UJ 

13600 

5 13 

1 .0 

10.0 

7.0 UJ 

200 UJ 

4940 

2.0 UJ 

6.0 

2780 

5.0 

3.3 J 

32.0 

50.0 

32.0 

65.6 

0.30 

3.0 

43200 

10.0 

5.0 

7.1 

3 16 

0.80 UJ 

13200 

lo00 

1 .o 

10.0 

7.0 UJ 

200 UJ 

4430 

2.0 UJ 

6.0 

2740 

5 .o 

6.0 J 

39.4 J 

50.0 

21.0 

49.6 

0.30 

3.0 

45500 

10.0 

5.0 

4.0 

5.8 

0.80 UJ 

13500 

16.8 

1 .o 

10.0 

7.0 IJJ 

200 UJ 

4530 

2.0 UJ 

6.0 

2920 

5 .o 

2.9 J 

38.2 

50.0 

19.9 

48.9 

0.30 

3.0 

44200 

10.0 

5.0 

4.5 

14.7 J 

0.80 

12m 

29.6 

1 .o 

10.0 

85 

200 UJ 

4450 

2.0 

6.0 

3160 

5 .0 

3.1 J 

39.4 J 

50.0 

2,l 

78.5 

0.30 

3.0 

44700 

10.0 

5.0 

4.1 

4.0 

6.80 UJ 

14700 

1 .0 

1.0 

10.0 

7.? 

200 UJ 

2070 

2.0 UJ 

6.0 

1850 

5.0 

3.6 J 

38.2 

50.0 

2.1 

78.2 

0.30 

3.0 

45300 

10.0 

5.0 

4.9 

18.3 J 

0.80 

14400 

28.1 

1 .0 

10.0 

7.0 UJ 

204) UJ 

2130 

2.0 

6.0 

1730 

5 .o 

5.0 J 

48.7 J 

50.0 

2.1 

70.2 

0.30 

3.0 

32300 

10.0 

5.0 

4.0 

4.0 

0.80 

UJ 

13600 

1 .0 

1 .0 

10.0 

7.0 IJJ 

200 UJ 

2040 

2.0 UJ 

6.0 

16W 

5 .o 

2.1 J 

50.5 

50.0 

2.1 

71.9 

0.30 

3.0 

44800 

10.0 

5.0 

4.0 

15.1 J 

0.80 J 

14200 

28.8 

1 .0 

10.0 

7.0 UJ 

200 UJ 

2000 

2.0 

6.0 

1720 

5.0 

5.6 J 

“Duplicate sample taken at MCK 1.92. 

bJ = estimated value: R = rejected value; U = undetected-klow method detection level. 
Table A-12. Water quality data for surface water samples of McCoy Branch, October 8,1990, after a 45-m rain event. 

Source: CH2M Hill, personal communication - 

Parameter mg/L 

unless otherwise noted 

~~~ 

MCK2.62 MCK 2.52 MCK 1.92 Field Blank 

Alpha activity (pCi/L) -1.28 * 3.5 UJ" 2.37 * 4.0 -0.60 * 3.6 UJ 0.69 * 3.8 J 

Alkalinity 

Chloride IC 

Conductivity (pmho/cm) 

Dissolved solids 

FIouride IC 

Nitrate 

PH 7.63 8.15 7.99 6.55 

Phenols <0.03 UJ 4.03 UJ C0.03 UJ e0.03 UJ Sulfate 

Total organic carbon (TOC) 

Total organic halides (TOX) (pa) e10 UJ <10 UJ <10 UJ <10 UJ Uranium- fluorometric 

Beta 3.03 * 7.7 J -8.61 * 7.1 U activity (pCi/L) -5.35 rt 7.3 UJ -3.49 f 7.4 

155 152 171 2 

3 3 2 c1 

342 340 350 1.2 

226 214 1.94 <1 

0.1 0.1 0.2 <0.1 

<1 UJ c1 UJ <1 UJ <1 UJ 

? 

Suspended solids C1 c1 <1 <1 5; 

24 26 18 <1 

c1 1 1 2 

0.00 1 0.001 <O.Ool €0.001 

"J = estimated value; R = rejected value; U = undetected-below method detection level. 
A-20 

Table A-113. we in 

M 8; 45 

Source: CI 12M Hill, personal communication 

Element MCK MCK MCK MCK MCK MCK Field Equip 

2.62 2.62-F 2.52 2.52-F 1.92 1.92-F blank blank (rBIJ,) ~ 

Alumiiium 

Antimony 

Barium 

Arscnic 

Beryllium 

Cadmium 

Calcium 

Chromium 

Cobalt 

collpcr 

Iron 

Lead 

Magnesium 

Manganese 

Mercury 

Nickel 

Niobium 

Phosphorous 

Potassium 

Selenium 

Silver 

Sodium 

Vanadium 

Zinc 

'79.8 J" 

50.0 

35.4 

71.1 

0.30 

3.0 

46'700 

10.0 

5.0 

4.0 

550 

0.80 [JJ 

14400 

1090 

0.10 

10.0 

9.5 J 

200 UJ 

4700 

2.0 UJ 

6.0 

2960 

5.0 

7.0 J 

48.7 J 

50.0 

20.9 

67.2 

0.30 

3.0 

45900 

10.0 

5.0 

4.0 

97.3 

0.80 UJ 

14100 

940 

0.10 

10.0 

8.7 J 

20 UJ 

4510 

2.0 UJ 

6.0 

2800 

5.0 

5.4 J 

76.7 J 

50.0 

20.8 

53.4 

0.30 

3.0 

46100 

10.0 

5 .o 

4.0 

170 

0.80 UJ 

13W 

204 

0.10 

10.0 

7.0 UJ 

200 UJ 

4720 

2.0 UJ 

6.0 

2'780 

5 .o 

15.3 

26.9 J 

50.0 

23.9 

48.9 

0.30 

3.0 

45600 

10.0 

5.0 

4.0 

4.0 

0.80 UJ 

13700 

1 .0 

0.10 

10.0 

7.0 UJ 

200 UJ 

4920 

2.0 UJ 

6.0 

2890 

5.0 

4.7 J 

76.7 J 

50.0 

2.4 

84.1 

0.30 

3.0 

5 1200 

10.0 

5.0 

8.9 

122 

0.80 UJ 

14500 

53.3 

0.10 

iO.0 

7.0 UJ 

200 UJ 

2410 

2.0 UJ 

6.0 

2020 

5.0 

9.1 J 

61.1 J 

50.0 

2.4 

82.8 

0.30 

3.0 

50400 

10.0 

5.0 

4.0 

60.8 

0.80 UJ 

14200 

41.4 

0.10 

10.0 

8.1 J 

200 UJ 

2490 

2.0 UJ 

6.0 

1890 

5 .o 

5.1 J 

33.2 J 

50.0 

2.1 

1.3 

0.30 

3.0 

93.6 J 

10.0 

5.0 

4.0 

4.0 

0.80 UJ 

12.2 J 

1 .o 

0.10 

10.0 

7.0 US 

200 UJ 

600 

2.0 UJ 

6.0 

248 

5.0 

' 2.4 J 

20.0 

50.0 

2.1 

1.3 

0.30 

3.0 

133 

10.0 

5.0 

4.0 

4.0 

0.80 UJ 

11.6 J 

2.2 

0.10 

10.0 

7.0 UJ 

200 UJ 

600 

2.0 UJ 

6.0 

274 

5.0 

6.3 J 

"J = estimated value; R = rejected value; U = undetected-kloav method detection level. 
Tabk A-14. Monthly means (stamlard deviation) and range (number of measurements) of water tempmature (‘C) in McCoy Branch (MCK), in upper White Oak creelr 

(WCK 6.8) and in upper Fdh (3reek (FFK l.Q), two re€ermcc sites Data were obtain4 with a Ryan TempMentor digital temperature 

recolcteT wilh values recotded every hour. NA=tempture data not avaiIable 

Sampling Pen& MCK 1.60 MCK 1.92 WCK 6.8 - FFlc 1.0 

Year Month Mean Range Mean Range Mean Range Mean Range 

1989 December 

1990 January 

February 

March 

April 

May 

June 

July 

August 

September 

October 

November 

December 

9.53 

(1.15) 

8.36 

(0.58) 

(0.92) 

10.38 

12.17 

(1.62) 

13.64 

(2.06) 

17.90 

(1.57) 

23.26 

(1.97) 

26.40 

(0.76) 

26.32 

(0.82) 

24.67 

(1.85) 

20.55 

(2.15) 

15.04 

(1.2) 

12.42 

(0.63) 

7.5-11.5 

(5041 

(744) 

(672) 

(744) 

(733) 

(6%) 

(720) 

(744) 

(744) 

(576) 

(744) 

(720) 

10.0-13.8 

(453) 

6.3-10.0 

8.1-12.6 

9.2-16.5 

10.3-19.6 

15.2-21.6 

19.6-27.4 

24.0-28.9 

17.6-29.0 

20.2-28.1 

15.2-23.8 

12.8-17.8 

9.71 

(1.25) 

NA 

NA 

NA 

NA 

14.41 

(1.01) 

15.08 

(0.73) 

15.89 

(0.72) 

16.29 

(0.90) 

(1.23) 

15.87 

14.35 

(1 69) 

12.27 

(1.33) 

11.19 

6.7-12.3 

(500) 

NA 

NA 

NA 

NA 

12.0-18.4 

(6%) 

(739 

(744) 

(744) 

(576) 

(744) 

(7%) 

8.9-13.8 

(453) 

13.4-17.0 

14.7-19.8 

11.1-199 

12.6-18.7 

10.5-18.4 

9.4-15.9 

8.76 

(1.95) 

9.96 

(0.94) 

10.25 

(2.10) 

(1.22) 

11.65 

12.76 

(1.95) 

13.83 

(0.89 

15.23 

(1.07) 

16.24 

(0.99) 

16.19 

(0.78) 

15.76 

(1.51) 

13.84 

(2.07) 

11.37 

(1.52) 

10.59 

3.9-12.7 

(672) 

(744) 

(672) 

(744) 

(720) 

(7%) 

(720) 

(744) 

(744) 

(576) 

(744) 

(720) 

7.2-1 2.6 

2.2-15.2 

9.2-15.3 

8.6-18.1 

11 6-16.3 

12.6-183 

14.4-19.3 

14.7-19.4 

11.6-18.8 

8.6-18.2 

8.0-15.9 

6.8-133 

NA 

12.53 

(0.39) 

12.71 

(0.53) 

13.15 

(0.63) 

13.57 

(0.75) 

15.66 

(2W 

14.76 

(0.63) 

15.22 

(0.68) 

(0.66) 

(0.85) 

(1.11) 

(OW 

1539 

15.02 

14.24 

13.14 

1219 

(1.20’1 (4541 

NA 

11.1-13.4 

(192) 

(672) 

11.5-14.0 

11.6-15.0 

(744) 

(718) 

11.8-15.4 

8.1 -24.1 9 

(7201 k 

13.5-19.0 

(720) 

(744) 

14.4-20.0 

11.8-19.7 

(744) 

(576) 

(744) 

12.6-18.4 

11.3-16.8 

10.2-16.1 

(733) 

9.8-14.2 

(455) 
A-22 

le A-15. Sediment an 

= emission 

: ERDA 1975 

-_c_. 

Sample month/station 

- 

Parameter OCt Nov 1 Nov DeC Dec Jan 

2 1 2 c 2 1 

Al (US Cd (AA) 

Cr (AA) 

cu 

Mn (AN 

(AN 

m (AN 

u (AA) 

(ES) 

(ES) 

Zn (AA) 

PCR (AA) 

Ba (ES) 

Ca (ES) 

Cs (ES) 

E'e (ES) 

K (ES) 

Mg (ES) 

Li (ES) 

Mn (ES) 

Mo (ES) 

Na (ES) 

Ni (ES) 

Si (ES) 

Ti (ES) 

Zr (ES) 

Y (ES) 

1 1000 

1.4 

12 

12 

520 

21 

6% 

4.00 

0.4 

<0.1 

0.025 

0.04 

20.0 

< 0.6 

11.0 

1.2 

0.10 

2.50 

0.30 

<0.01 

20 

0.8 

0.015 

7300 

<2.0 

6 

23 

62 

8 

0.14 

2.2 

0.3 

<0.01 

0.08 

0.5 

<0.6 

5.0 

0.3 

0.30 

0.02 

0.01 

15 

0.3 

0.005 

4550 

4.0 

10 

8 

579 

18 

34 

<0.20 

< 1.0 

<0.1 

<0.01 

0.04 

2.5 

<Oh 

1.2 

0.6 

0.03 

0.15 

0.0% 

0.01 

20 

0.3 

0.00s 

<2.0 

20 

13 

34 

<0.20 

c 1.0 

<0.1 

4.0 

<0.01 

0.04 

0.6 

< 0.6 

2,5 

0.3 

402 

0.30 

0.15 

0.04 

tO.O1 

20 

0.3 

0.010 

<2.0 

16 

16 

22 

<0.20 

< 1.0 

<0.1 

5.0 

C0.01 

0.04 

10.0 

<0.6 

1.2 

0.3 

0.06 

0.80 

0.15 

0.04 

<0.01 

15 

0.3 

0.010 

<2*0 

14 

34 

46 

0.40 

< 1.0 

<0.1 

2.5 

c0.01 

0.04 

1.2 

<0.6 

2.5 

0.6 

<0.02 

0.30 

0.15 

<0.02 

0.04 

<0.01 

20 

0.3 

0.010 

0.02 
Table A-16. Concentrations of elements measured in coal ash samples of the McCoy Branch floodplain, October 17,1990. 

Source: CH2M Hill, personal communication 

Element - Site" hm AlSl A1S2 A2A A2S 1 fdA A3s1 A3s2 

Aluminum 

Antimony 

Arsenic 

Barium 

Beryilium 

Cadmium 

Calcium 

Chromium 

Cobalt 

Copper 

Iron 

Lead 

Magnesium 

Manganese 

Mercury 

Nickel 

Niobium 

Phosphorus 

Potassium 

Selenium 

Silver 

Sodium 

Vanadium 

Zinc 

9030 

Rb 

2.2 J 

89.0 

0.60 

2.1 

2230 

25.0 

18.0 

6.1 

19200 

33.4 

597 

2240 

0.10 

6.7 

1.7 UJ 

326 J 

544 

0.24 UJ 

1.4 

49.6 J 

39.4 

34.4 

9550 

R 

2.2 J 

118 

0.71 

0.88 

684 

17.4 

25.0 

5.5 

16900 

36.2 

525 

2600 

0.12 

8.3 

1.7 UJ 

211 J 

65 1 

0.24 UJ 

1.5 

88.8 J 

34.3 . 

33.9 

18600 

R 

54.5 J 

684 

3.2 

1.0 

3460 

15.5 

12.0 

74.9 

18300 

13.0 

1140 

81.3 

0.73 

29.1 

2.4 UJ 

2180 J 

3570 

9.1 J 

2.1 

326 

83.7 

39.3 

15300 

R 

24.3 J 

109 

1.2 

1.5 

1880 

12.0 

27.5 

24.1 

19800 

26.0 

970 

1830 

0.11 

34.2. 

2.0 UJ 

272 J 

1960 

2.2 J 

1.7 

141 J 

50.0 

102 

20800 

R 

46.2 J 

548 

2.9 

4.2 

5 130 

18.2 

21.9 

53.5 

64300 

15.4 

1 690 

672 

0.66 

40.7 

2.7 UJ 

1060 J 

3670 

5.3 J 

2.3 

384 

74.2 

75.7 

5830 

10.6 J 

28.3 J 

71.4 

0.49 

1.2 

858 

5.6 

13.0 

11.8 

20100 

125 

473 

%5 

0.05 

22.3 

1.5 UJ 

129 J 

91 1 

0.47 J 

1.3 

141 J 

22.1 

56.1 

7480 

R 

22.0 J 

77.1 

0.56 

1.7 

906 

10.1 

11.1 

11.5 

19600 

6.5 

614 

702 

0.06 

15.5 

1.6 UJ 

145 J 

1310 

0.23 UJ 

1.4 

135 J 

33.4 

43.5 

'Approximate stream kilometers for sites are given in Table A-7. 

bJ = estimated value; R = rejected value; U = undetected-below method detection level. 
Table A-17. Conmtrations of elements rneaswed in coal ash samples 04 the McCoy Branch floodplain, Ocbber 17,1y90. 

Source: CH2M Hill, persona1 communication 

Element - Site* 

(Pgk) A4A A4S1 A4S2 MA ASS1 Ass2 A6A A6S 1 A6S2 A7A A7S1 A7S2 

Aluminum 

Antimony 

menic 

Barium 

Beryllium 

Cadmium 

Calcium 

Chromium 

Cobalt 

Copper 

Iron 

Lead 

Magnesium 

Manganese 

Mercury 

Nickel 

Niobium 

Phosphorus 

Potassium 

Selenium 

Silver 

Sodium 

Vanadium 

Zinc 

20200 

54.2 3 

355 

2.3 

1.6 

3210 

16.4 

15.7 

37.7 

29900 

14.3 

1620 

575 

0.19 

32.3 

2.2 UJ 

757 J 

3900 

1.7 3 

1.9 

355 

52.7 

66.5 

Rb 

11200 

R 

15.3 J 

18.1 

0.72 

1.2 

620 

8.6 

18.5 

11.2 

14500 

8.6 

977 

2 030 

0.07 

22. I 

1.6 UJ 

97.3 J 

1780 

0.23 UY 

1.3 

95.9 J 

27.7 

90.2 

9500 

R 

10.6 J 

39.3 

0.59 

1.2 

518 

8,6 

21.4 

10.7 

13600 

15.1 

732 

1050 

0.07 

18.0 

1.6 US 

47.0 UY 

I320 

0.24 US 

1.4 

45.4 J 

25.2 

79.6 

12300 

R 

53.2 J 

250 

1.: 

4.2 

3300 

9.1 

12.5 

27.6 

51500 

10.4 

Im 

577 

0.13 

26.4 

2.1 UJ 

262 J 

2100 

2.7 J 

1.8 

257 

37.7 

46.2 

6060 

R 

10.3 J 

71.0 

0.86 

22.8 

12400 

50.6 

29.5 

70.2 

372000 

14.5 

3740 

2360 

0.09 

40.4 

20.1 UJ 

575 UJ 

I720 

0.30 9 

17.2 

626 

94.0 

81.7 

16600 

R 

11.5 J 

196 

1.4 

2.3 

17800 

21.5 

10.2 

4.9 

21300 

13.8 

3320 

248 

0.09 

15.3 

2.0 u3 

269 3 

2190 

0.30 u3 

1.7 

125 3 

29.4 

46.6 

15000 

K 

15.6 J 

252 

1.2 

1.4 

6950 

14.3 

20.0 

26.0 

25200 

15.1 

1610 

3200 

0.19 

21.0 

2.4 UJ 

375 J 

2800 

1.5 9 

2.1 

290 

40.2 

72.3 

9210 

n 

3.2 J 

79.5 

0.69 

7.0 

25oooo 

22.9 

11.4 

9.1 

13700 

21.7 

112w 

425 

0.05 

22.9 

16.0 U3 

457 UJ 

2140 

1.2 US 

13.7 

177 

12.7 

84.5 

9460 

K 

3.0 J 

71.6 

0.69 

1.5 

22oooo 

8.9 

8.6 

23.1 

1m 

27.1 

7880 

320 

0.05 

9.9 

1.6 UJ 

227 5 

1990 

0.24 us 

1.4 

189 

16.2 

79.3 

14905 

R 

59.2 J 

425 

2.4 

2.6 

3830 

11.5 

11.9 

40.8 

36600 

16.6 

1210 

194 

0.30 

21.8 

2.2 u3 

IO00 3 

2930 

1.4 J 

1.9 

332 

55.8 

34.2 

6670 

R 

43.6 J 

96.0 

0.56 

1.6 

IO30 

6.8 

17.0 

15.1 

24900 

11.4 

653 

820 

0.07 

21.9 

1.6 UJ 

143 

1070 

0.89 J 

1.3 

86.0 -I 

26.0 

59.1 

8540 

n 

41.9 J 

74.6 

0.62 

1.2 

963 

7.4 

18.9 

11.9 

16700 

11.9 

694 

1020 t3 

0.07 

? 

A 

18.4 

1.6 UJ 

17h 

1370 

0.50 9 

1.3 

106 3 

26.0 

55.3 

“Approximate siream kilsmelers for sites are given in Table A-7. 

bJ = astimeted value; R = rejected value; U = undetected-below method detection level. 
Table A-1B Radioactivity and percent oil and grease in coal ash samples from the McCoy Branch floodplain, October 17,1990. 

Source: CH2M Hill, personal communication 

Alpha Beta Uranium Oil and 

Site' activity activity Cesium-137 fluorometric grease Uranium-235 

(pCi/g) (PCW (PW> (Wg) (%I (Weight %) 

Misc! 

(PCW 

AIS1 

A1S2 

A2A 

A2s 1 

A3A 

A3s1 

A3s2 

A4A 

A4S 1 

A4S2 

A5A 

A5s 1 

A5s2 

A6A 

A6S1 

A6S2 

A7A 

A7S1 

A7S2 

0.04 * 2.3 J' 

0.46 * 2.4 U 

-0.38 f 2.3 UJ 

0.62 * 2.4 J 

1.35 * 2.5 J 

2.82 f 1.7 

3.44 f 1.7 

-0.20 f 2.3 UJ 

2.78 f 1.7 

5.99 * 2.0 

2.39 f 1.6 

1.21 r 1.4 J 

3.38 f 1.7 

5.75 * 2.0 

0.60 L 1.3 J 

1.6 f 1.5 

1.21 * 2.4 J 

-1.44 f 2.2 

6.30 f 2.1 

-1.79 f 4.2 UJ 

-3.13 * 4.2 UJ 

-0.67 f 4.3 UJ 

-3.13 * 4.2 UJ 

-1.12 f 4.3 UJ 

2.46 f 3.3 J 

2.91 f 3.4 J 

-2.35 i 4.2 UJ 

0.78 f 3.2 J 

3.24 * 3.4 J 

2.01 Q 3.3 J 

-0.78 * 3.2 UJ 

3.13 Q 3.4 J 

7.27 f 3.6 

0.11 f 3.2 J 

4.14 f 3.4 

-4.14 * 4.1 UJ 

5.59 f 3.4 R 

1.68 * 3.3 3 

7.30"' f 2.ZE' 

3.30E1 * 1.7&' 

1.52&' f 2.0E1J 

2.07&' f 1.9"' 

1.39&l f 2.0"' J 

6.45E2 f lSE1 J 

8.SE2 f 2.3"' J 

2.65&' i 1.5%' 

l.WF" lSE1 J

8.25"' k 1.5&'J 

9.3P2 f 19' 3 

2.68%' f 19' 

5.WE2 * 1.651 J 

6.95"2 1.5E1 J 

-5.6SL2 Q 1.5"' UJ 

-6.80E2 f 2.0E' UJ 

5.05"2 2 1.5"' J 

4.47"2 f 1.5"' J 

1.03"' f 12iE' J 

4 

3 

7 

5 

8 

4 

3 

7 

3 

3 

6 

3 

7 

8 

2 

2 

13 

3 

3 

<O.l 

eo.1 

co.1 

<0.1 

<O.l 

co.1 

<o. 1 

<0.1 

<0.1 

<0.1 

co.1 

C0.1 

<0.1 

co.1 

<0.1 

0.1 

c0.1 

€0.1 

<0.1 

LOWU*xxx 

Lowufxxx 

INSUFF U * 0.0 

LOWU*xXx 

0.76 * 0.01 

LOWU*xXx 

LOWUkxXx 

INSUFF U * 0.0 

LOWU*xxx 

LOWU*xxx 

INSUFF U r 0.0 

LOWU*xxx 

INSUFF U f 0.0 

LOWU*xxx 

LOWU*xxx 

LOWU*xxx 

LOWU*xxx 

3.32&' f 2.4Eb 

5.15 * 1.3 

6.30 * 1.4 

5.10 1.3 

9.2 f 5.5'' 

~ ~- 

'Approximate stream kilometers for sites are given in Table A-7. 

bUranium-235 at site A4& Th-234 at sites A452, A64 and A651. 

7 = estimated value; R = rejected value; U = undetected-below method detection level. 

%-223. 
Table A-19. GrouwtsPatm &ta fOr McQ €3- Lktd~X 15-17,1998. 

Source: CH2M IHi& personal communication 

Parameter - Siteu 

m& unless otherwise noted 50002 5000-F 5001 5001-F 5002 5002-E 

GW-321 GW-321 GW-672 GVi-672 GW-673 GW-673 

Alpha acliviry (pCirL) -14.51 2 29.8 UJb 27.10 f 35.4 21.08 2 14.9 J 11.45 i 33.3 J 91.34 i 43.0 1.61 _+ 32.2 3 

Beta activity (pCi/L) -60.53 t 75.4 UJ -72.17 2 74.8 -11.64 s 77.9 UJ -83.80 2 74.2 U 25.61 i 75.8 U -35.57 2 76.5 UJ 

Alkalinity 119 115 262 279 121 143 

Chloride 1C 1 1 3 3 2 2 

Conductivity (urn hokm) 228 225 622 632 375 376 

Dissolved solids 148 138 332 374 222 226 

Flouride IC C0.1 co.1 0.1 0.1 1 I 

Nitrate 

PfI 

Phenols 

1J 1J 35 4J 1J c1 UJ 

8.2 8.2 7.7 7.6 9.9 10.0 ? 

s 

4.03 UJ <0.03 UJ ~0.03 UJ c0.03 UJ <a03 u3 <0.03 hlJ 

Sulfate 2 2 37 37 27 27 

Suspended solids 38 <I 1170 2 <1 C1 

Total organic carbon (TOC) 4 2 2J 2J 10 9 

Total organic halides (TOX) (p&) <I0 UJ <10 UJ 54 J 120 J 351 J <I0 UJ 

Uranium-fluorometric <0.001 <0.001 0.002 0.002 0.001 5.002 
T&k A-19 (conlinued) 

Parameter 

Site 

mgL unless otherwise 5003 FCAP 5003 FCAP-F 5004 FCAP 5004 FCAP-F 500s FCAP 5005 FCAP-F 5006 FCAP 5007 FCAP 

noted GW-674 GW-674 GW-676 GW-676 GW-676 GW-676 G W-676 GW676 

Alpha activity (pCi/L) 

Beta activity (pCi/L,j 

Alkalinity 

Chloride IC 

Conductivity 

(gmho/cm) 

Dissolved solids 

Flouride IC 

Nitrate 

PH 

Phenols 

Sulfate 

Suspended solids 

Total organic carbon 

floc> 

(TOXI @g/L) 

Total organic halides 

46.07 t 37.8 

-90.79 -+ 73.9 u 

224 

2 

450 

260 

0.2 

<1 UJ 

7.8 

c0.03 UJ 

27 

<l 

7 

<lo UJ 

-27.23 127.6 UJ 

-93.12 f 73.8 U 

226 

2 

462 

268 

0.2 

c1 UJ 

7.6 

<0.03 UJ 

27 

2 

8 

<10 UJ 

Uranium-fluorometric 0.002 0.002 

-0.19 +- 36.0 UJ 

15.65 74.3 J 

185 

5 

504 

336 

0.2 

73 

7 

c0.03 UJ 

10 

526 

1 

<IO UJ 

0.001 

R 

-37.25 t 76.6 

216 

4 

535 

314 

0.2 

5J 

7.9 

4.03 UJ 

8 

<1 

2 

13 J 

0.002 

70.56 f 40.9 

128.04 t 54.6 

208 

5 

525 

298 

0.2 

7J 

7.7 

<0.03 UJ 

10 

408 

1 

<lo UJ 

0.2 

11-04 t 33.6 J 

-65.18 t 75.2 UJ 

230 

.4 

540 

318 

0.2 

5J 

7.8 

<0.03 UJ 

8 

3 

2 

40 UJ 

0.002 

58.83 2 39.7 J 

76.82 f 82.2 J 

3 

<I 

2.6 

28 

e0.1 

<1 UJ 

7.2 

<OM UJ 

<1 

<1 

18 

<IO UJ 

<0.001 

24.14 f 27.6 UJ 

-97.77 * 73.5 u 

3 

<1 

2.1 

14 

<0.1 

5. 

<I UJ tL 4 

7.3 

<0.03 UJ 

<l 

<1 

<1 UJ 

<lo UJ 

<0.001 

.Approximate stream kilometers for sites are given in Table A-7. 

bJ = estimated value; R = rejected value; U = undetected-below method detection level. 
Table A-20. Ceacentratbns of elements measured in groundmler frorn McCoy Branch, October 15-17,199[). 

Source: CH2M Hill, personal communication 

Element - Site. 

So00 5000-F 5001 5001-F 5002 5002- 5003 5003-F 

GW-321 GW-321 GW-672 ~~472 GW473 GW673F GW-674 GW-674 PgR. 

Aluminum 

Antimony 

Arsenic 

Barium 

Beryllium 

Cadmium 

Calcium 

Chromium 

Cobalt 

Copper 

iron 

Lead 

Magnesium 

Manganese 

Mercury 

Nickel 

Niobium 

Phosphorus 

Potassium 

Selenium 

42.9 

50.0 

43.3 

0.30 

3.0 

24300 

10.0 

5.0 

4.0 

22.8 

13900 

5.2 

10.0 

5.4 

200 UJ 

775 

12000 

50.0 

2.0 2.7 

255 

1.3 

3.0 

114000 

24.9 

21.1 

30.1 

16100 

3.9 3 6.5 J 

33900 

2150 

0.20 0.26 

25.4 

7.0 UJ 

200 UJ 

4960 

2.0 8.0 

910 

50.0 

2.0 

133 

0.30 

3.0 

95200 

10.0 

5.6 

11.1 

1110 

2.4 J 

25500 

1380 

0.20 

10.0 

7.0 UJ 

200 UJ 

3960 

2.2 

1060 

50.0 

2.0 

46.9 

0.30 

3.0 

8310 

74.7 

5.0 

52.5 

2110 

15.4 J 

12100 

44.6 

0.20 

32.9 

7.0 UJ 

200 u3 

67900 

2.0 

48.7 Jb 

50.0 

2.0 

29.6 

0.30 

3.0 

5290 

10.0 

5.0 

6.3 

37.1 

R 

11200 

3.8 

0.20 

10.0 

7.0 UJ 

200 UJ 

65500 

2.0 

21800 

50.0 

3.2 

674 

4.0 

8.0 

93200 

31.4 

27.6 

73.5 

33500 

52.9 J 

37400 

2460 

0.33 

41.1 

7.0 UJ 

200 UJ 

7710 

4.0 

70.4 J 

50.0 

2.0 

236 

0.30 

3.0 

62200 

10.0 

5.0 

6.6 

20.6 

R 

21105 

224 

0.20 

10.0 

8.8 

200 UJ 

4230 

2.0 

Silver 6.0 6.0 6.0 6.0 6.0 6.0 6.0 

Sodium 660 3870 4200 16800 17000 3510 3540 

Vanadium 5.0 34.3 5 .O 5.0 5.0 62.7 5.0 

Zinc 50.0 244 56.2 134 46.3 2010 73.5 
Tabie A-20 (cwtinued) 

Element - Site 

5005-F 5006 5006-F 5007 rgn 5004 5004-F 5005 

GW-676 GW-676 GW-676 GW-676 GW-676 GW-676 GW472 

Aluminum 

Antimony 

Arsenic 

Barium 

Beryllium 

Cadmium 

Calcium 

Chromium 

Cobalt 

Copper 

Iron 

Lead 

Magnesium 

Manganese 

Mercury 

Nickel 

Niobium 

Phosphorus 

Potassium 

Selenium 

Silver 

Sodium 

Vanadium 

11700 

50.0 

2.0 

179 

0.50 

3.0 

159000 

22.0 

13.1 

15.0 

17700 

8.1 

21200 

1610 

0.20 

13.4 

7.0 u 

530 

4100 

4.0 

6.0 

8250 

18.5 

52.1 

50.0 

2.0 

62.8 

0.30 

3.0 

7m 

10.0 

5 .O 

4.0 

26.3 

3.1 

16400 

680 

0.20 

10.0 

7.0 U 

200 u 

1470 

2.0 

6.0 

7720 

5.0 

1620 

50.0 

2.0 

66.3 

0.30 

3.0 

77800 

10.0 

5.0 

4.0 

1030 

3.7 

19OOO 

361 

0.20 

10.0 

7.0 U 

200 u 

1950 

2.0 

6.0 

10500 

5.0 

73.5 

50.0 

2.0 

61.8 

0.30 

3 .O 

77100 

10.0 

5.0 

4.0 

23.9 

2.2 

16500 

682 

0.20 

10.0 

7.0 U 

200 u 

1410 

2.0 

6.0 

7- 

5.0 

30.6 

50.0 

5.0 

0.30 

3.0 

250 

10.0 

5.0 

4.0 

13.1 

15.0 

1.5 

10.0 

10.2 

200 u 

600 

20 

0.20 

20.7 

50.0 

2.0 2.0 

3.1 

0.30 

3.0 

152 

10.0 

5.0 

4.0 

14.6 

2.0 

23.4 

2.2 

0.2 

10.0 

7.0 U 

200 u 

600 

20 

6.0 

378 

5.0 

2.0 

6.0 

448 

5.0 

18.2 4.8 14.6 Zinc 87.1 32.3 17.2 

8Approximate stream kilometers for sites are given in Table A-7. 

*J = estimated value; R = rejected value; U = undetected-belaw method detection level. 

APPENDM: B 

CHECKILIST OF BENTHIC MACROINVEXTEBRATE TAXA FROM 

MCCOY BRANCH AND WMTE OAK CREEK, APRIL 1989-JANUARY 1990 

B-3 

Table B-1. Checklist of benthic marroirlveffebrafe taxa mkcted &om McCoy Branch 

(MCK) and White Oak Creek (WCK), a reference stream, April 1989-January 1990. 

The ‘X indicates that the taxnu w8cf mllected at least once in 

quantitative samples during the sampling period 

TIE ‘Q indicates that the taxon was mWtd 

ia qualitative samples only 

Taxon 

Site 

MCK MCK WCK 

1.40 2.03 6.8 

Coelenterata (hydras) 

Hydridae 

Hydra 

Turbellaria 

Tricladida 

Planariidae (flat worms) 

Copepoda (copepods) 

Nematoda (roundworms) 

Annelida 

Oligochaeta (aquatic earthworms) 

Ostracoda (seed shrimp) 

Crustacea 

Amphipoda (sideswimmers) 

Gammaridae 

Crangonyx 

Decapoda (crayfish) 

Cambaridae 

Cambanis 

Hydracarina (water mites) 

Insecta 

Collembola (springtails) 

Anthropleona 

Entomobryomorpha 

Smin t huridae 

X 

X 

X 

x 

X 

Q 

X 

X 

X 

X 

X 

Q 

Q 

X 

X 

X 

X 

X 

X 

X 

X 

X 

Q 

X 

X 
B-4 

Table B-1 (Continued) 

Site 

MCK WCK 

6.8 

MCK 

‘Taxon 1.40 2.03 

Ephemcroptera (mayflies) 

Baetidae? 

Baetidae 

Baetis 

Baetis Pluto 

Baetis tricaudatus 

Pseudocloeon 

Ephernerellidae 

Ephemerella 

Ephemerella ? 

Ephemerella invaria 

Eurylophella 

Euiylophella doiisltemporalis 

Ephemeridae 

Ephemera 

Heptageniidac 

Stenacron 

Stenacron inteipunctatum 

Stenonema 

Stenonema? 

Lepto phlebiidae 

Ha hrophlehiodes 

Pa ra leptophle bia 

Oligoneuriidae 

Zsonychia 

Odon ata 

Anisoptera (dragonflies) 

Aeshnidae 

Boyeria 

Cordulegastridae 

Cordulegnster 

Gornphidae 

Srylogornphus 

Stylogomphus albistylus 

Stylogomph us? 

Zygoptera (damselflies) 

Libellulidae 

X 

x v 

n Q L! 

X 

X 

X 

X 

X 

X 

X 

X 

X 

Q 

Q 

X 

Q 

X 

X 

X 

Q 

X 

X 

X X 

X X 

X 

Q 

X 

X 

X 

X 

X 

Q 

X 
B-5 

Table B-1 (continued) 

Taxon 

Site 

MCR MCK WCK 

1.40 2.03 6.8 

Calopterygidae 

Calopteryx 

Calopteryx? 

Ckenagrionidae 

Ischnura 

Plecop tera (s toneflies) 

Chloroperlidae 

Haploperla 

SweEtsa 

Sweltsa ? 

Leuctridae 

Leuclra 

Leuctra? 

Nemouridae 

Amphinemura 

Amphinemura delosa 

Peltoperlidae 

Tallaperla 

Viehoperla? 

Eccoptura 

Perlesta 

Perlodidae 

Isoperla 

lsoperla holochlora ? 

Isoperla ? 

Perlidae 

xanthenes 

Hemiptera (true bugs) 

Veliidae 

Microvelia 

Microvelirr nmericnno ? 

Hydrometridae 

Hydrometra 

Mesovel iidae? 

Corixidae 

Sigam 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

Q 

X 

X 

X 

X 

X 

Q 

X 

Q 

Q 
B-6 

Table B-1 (Conhucd) 

Site 

MCK MCK WCK 

Taxon 1.40 2.03 6.8 

Megaloptera 

Nigronia 

Nigronia 

Nigronia 

Corydalidae (dobsonflies, fishflies) 

fasciatus 

serriconzis 

Sialidae (alderflies) 

Sialis 

Trichoptera (caddisflies) 

Glossosornatidae 

Agapetus 

Glossosomn 

Hydropsychidae 

Cheumatopsyche 

Diplectrona 

rnodesta 

Hydropsyche 

IYydropsyche ? 

Hydroptilidae 

Hydroptiln 

Limnephilidae 

Neophylax 

Pycnopsyche 

Pycnopsyche gentilis 

Pycnopyche luculenta 

Pycnopsyche scabiipennis 

Odontoceridae 

Psilotretn 

Philopotamidae 

Chiman-n 

Dolophilodes 

distinctus 

Wonnaldin 

Molannidae 

Molanna 

X 

X 

X 

X 

X 

X 

X 

X 

X X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

x 

X 

X 

X 

X 

Q 

Q 

Q 

X 

X 

X 

X 
€3-7 

Table El (continued) 

Site 

MCK MCK WCK 

Taxon 1.40 2.03 6.8 

Polycentropodidae 

Polycentropus 

Polycentropus? 

Psychomyiidae 

Lype diversa 

R hyacophilidae 

Rhyacophila 

Goeridae 

Goera 

Lepidostoma 

X 

X 

X 

X 

Lepidostomatidae X 

X X 

Coleoptera (beetles) 

Dryopidae 

Elmidae 

Q 

Q 

X X 

X X 

Helichus fastigiatus 

Dubiraphia 

Optiosewus 

Stenelmis 

Stenelmis? 

Microcyllloepus 

pusilIus 

X 

X 

Eubriidae 

Ectopna 

Hydrophilidae 

Hydrobius 

Psephenidac 

Psephenus 

henicki 

Ptilodactylidae 

Anchytarsus 

bicolor 

X 

Q 

X 

X 

Diptera (true flies) 

Muscomorpha 

Cera topogonidae 

A trichopogon 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 
B-8 

Table B-1 (Co~tin~ed) 

Site 

MCK MCK WCK 

Taxon 1.40 2.03 6.8 

Chironomidae 

Tanypodinae 

Labrundinia 

Natarsia 

Nilotanypus 

Nilotanypus? 

Paramerina 

Pa M merin n '? 

Thienemannirnyia gp 

Thienemannimyia ? 

Trissopelopia ogema wi 

Trissopelopia ? 

Za vrelimy in 

Zavrelirnyin? 

Diamesinae 

Diarnesa 

Orthocladiinae 

Brillin 

Chaetoclndius 

Chaetocladius? 

Corynoneu rn 

Corynoneurn ? 

Cricotopus bicinclus 

Cricotopus tremulus 

Cricotopusl 

Cricotopusl 

Orthockrdius 

Orthocla diu s ? 

Diploclndius 

EukieSferiella 

Eukieffenella claripennis 

Eukieffeeliella devonicn 

Eukieffenelln? 

Helenielln 

Heleniella ? 

Heterottissoclad ius 

HeterorriSsocladius marcidus 

Heterotnssoclndius? 

Limnophyes 

Q Q Q 

X X X 

X 

X 

X X 

X 

Q 

Q 

X X X 

X X 

X 

X 

X 

X 

X 

X 

Q 

X 

X 

X 

Q 

X 

X 

X 

Q 

Q 

X 

X 

X 

Q 

Q 

Q 

X 

X 

Q 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

Q 

X 

X 

X 

Q 

X 

X 
€3-9 

Table B-1 (Chutind) 

Taxon 

Site 

MCK MCK WCK 

1.40 2.03 6.8 

Lopescladius 

Nanocladius 

Pa rukiefferiella 

Parametriocnemus 

Psectrocladius 

Rheocricotopus 

Smittia 

Symposiocladius 

Thienemannielln 

Tvetenia 

Tvetenia bavmica 

Chironominae 

Chironomini 

ChironamuslEinfeldia 

Cyptochironomus 

Dicrotendipes 

Microtendipes 

Microtendipes ? 

Paralauterborniella 

Para tendipes 

Para tendkes ? 

Polypedilu rn 

Stictochironomus 

Micropsectla 

Micropsectra ? 

Paratanytarsus 

Para tanyta rsus ? 

Rheotanytaisus 

Rhea f onyta rsus ? 

Stempe flinn 

Stempellineiln 

Sternpellinella ? 

Culicidae 

Anopheks 

Dixidae 

Dixa 

Dolichopodidae 

Sciom yzidae 

Tanytarsini 

X 

X 

X 

X 

X 

X 

X 

Q 

X 

X 

Q 

Q 

X 

X 

Q 

Q 

X 

X 

Q 

X 

X 

X 

Q 

X 

X 

X 

Q 

X 

X 

X 

Q 

x 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

Q 

X 

X 

X 

X 

X 

X 

Q 

X 

X 

X 

X 

Q 

X 

X 

X 

X 

X 

x 

X 

X 

X 

Q 

~~ .. .... .. ....... ..... ..... ~ I..l.........._____....... * ~ ......... 
B-10 

Table El (Continued) 

Site 

MCK WCK 

5.8 

MCK 

1.40 2.03 Taxon 

Simuliidae 

Simulium 

Simulium? 

Muscidae 

Empididae 

Chelifera 

Clinocera 

Hemerodromia 

Hemerodromia ? 

Psychodidae 

Pen'coma 

Stratiomyidae 

Ca lopa ryphus 

Myxosargus 

Nemotelus 

Odontomyia 

Tabanidae 

Chrysops 

Tu banus 

Antocha 

Hexa toma 

Limnophila 

Limnophila? 

Polymera 

Pseudolimn np hila 

Pseiidolimnophila ? 

Tipula 

Tipula abdominalis 

Tipulidae 

Mollusca 

Gastropoda (snails) 

Lymnaeidae 

Lymnaeidae? 

Physidae 

Physella 

Planorbidae 

Gyrtrulus 

Pseudosmcinea colu.mella 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

X 

Q 

X 

X 

X 

X 

X 

Q 

Q 

X 

X 

X 

Q 

Q 

X 

X 

X 

X 

Q 

X 

X 

X 

Q 

X 

X 

X 

X 

X 

X 

X 

Q 

X 

X 

X 

X 

X 

X 

X 
B-11 

Table €3-1 (coatinued) 

Site 

Taxon 

MCK MCK WCM 

1.40 2.03 6.8 

Pleuroceridae 

Elimia 

Bivalvia (clams) 

Sphaeriidae 

Pisidium 

Pisidium? 

Sphaerium 

Corbicula ffuminen 

X 

X 

X 

X 

X X 

X X 

ORNLm-11926 

1. 

2. 

3. 

4. 

5. 

6. 

7. 

8. 

9. 

10. 

11. 

12. 

13. 

14. 

15. 

16. 

17. 

18. 

19. 

20. 

21. 

22-29. 

30. 

31. 

73. 

74. 

75. 

76. 

77. 

78. 

79. 

80. 

81. 

L. J. Allison 

T. L. Ashwood 

B. G. Blaylock 

W. R. Brown 

G. F. Cada 

S. W. Christensen 

R. B. Clapp 

R. B. Cook 

M. E P. DeLozier 

M. L. Frank 

C. W. Gehrs 

S. G. Hildebrand 

C. C. Hill 

R. L. Hinzman 

M. A. Huston 

P. Kanciruk 

B. L. Kimmel 

J. M. Loar 

R. B. McLean 

L. W. McMahon 

M. J. Peterson 

M. 6. Ryon 

J. A. Shaakir-Ali 

F. E. Sharples 

lNTERNAL DISTRIBUTION 

32. E. M. Schilling 

33. L. R. Shugart 

34. J. G. Smith 

35. G. R. Southworth 

36. C. L. Stair 

37. A. J. Stewart 

38. J. E. Stone 

39. G. W. Suter 

40. D. W. Swindle 

41. V. R. Tolbert 

42. J. R. Trabalka 

43. R. R. Turner 

44. W. Van Winkle 

45. L. D. Voorhees 

46. S. Walker 

47. R. K. White 

48. Central Research Library 

49-63. ESD Library 

64-67. ER Document Management Ctr 

68-69. Laboratory Records Department 

70. Laboratory Records-RC 

71. ORNL Patent Office 

72. ORNL Y-12 Technical Library 

EXTERNAL DISTRIBUTION 

S. Ahlstedt, Division of Water Resources, Tennessee Valley Authority,' Norris, TN 

37828 

D. S. Day, Environmental Division, US. Department of Energy, Savannah River 

Operations Office, Box A, Aiken, SC 29802 

P. H. Edmonds, Radian Corporation, 120 South Jefferson Circle, Oak Ridge, 

TN 37830 

W. Fisher, Department of Zoology, Oklahoma State University, Stillwater, OK 

74078 

J. F. Franklin, Bloedel Professor of Ecosystem Analysis, College of Forest 

Resources, University of Washington, Anderson Hall (AR-lo), Seattle, WA 98195 

C. S. Gist, Environmental Protection Division, SE-31, DOE Oak Ridge Field 

Office, Oak Ridge, P.O. Box 2001, Oak Ridge, TN 37831 

H. W. Hibbitts, Deputy Assistant Manager, Department of Environment, Safety 

and Quality, SE-30, DOE Oak Ridge Field Office, P.O. Box 2001, Oak Ridge, 

TN 37830 

D. R. Hopkins, U.S. Environmental Protection Agency, 345 Courtland Street, 

NE., Atlanta, GA 30365 

G. M. Hornberger, Professor, Department of Environmental Sciences, University 

of Virginia, Charlottesville, VA 22903 
82. G. Y. Jordy, Director, Office of Program Analysis, Office of Energy Research, 

ER-30, G-226, US. Departmcnt of Energy, Washington, DC 20545 

83. T. Joseph, Environmental Remediation Branch, Environmental Protection 

Division, SE-312, DOE Oak Ridge Field Office, P.O. 2001, Oak Ridge, TN 37830 

84. R. A. Jump, Environmental Restoration Division, EW-91, DOD Oak Ridge Field 

Office, P.O. Box 2001, Oak Ridge, "4 37830 

85. W. h Mocker, 1219 Riverbend Drive, Kingston, TN 37763 

86. E. C. Leming, Director, DOE Oversight Division, 761 Emory Valley Road, 

Oak idgc, TN 37830-7072 

87. G. J. Marciante, Environmental Protection Division, SE-31, DOE Oak Ridge Field 

Office, P.O. Box 2001, Oak Ridge, Oak Ridge, TN 37830 

88. A. D. McKinney, Chief, Environmental Serviccs, TWRA, P.O. Box 40747, 

Ellington Agricultural Center, Nashville, TN 37204 

89. W. G. McMillan, Environment and Protection, DOE Oak Ridge Ficld Office, 

P.O. Box 2001, Oak Ridge, TN 37830 

90. C. R. Olsen, Environmental Sciences Division, Office of Health and 

Environmental Research, ER-74, U.S. Department of Energy, Washington, DC 

20585 

91. R. H. Olsen, Vicc President for Research, University of Michigan, Medical Science 

Building 11, #5605, 1301 East Catherine Street, Ann Arbor, MI 48109-0620 

92. A. Patrinos, Acting Director, Environmental Sciences Division, Office of Health 

and Environmental Research, ER-74, U.S. Department of Energy, Washington, 

DC 20585 

93. S. S. Perkins, c/o Labat-Anderson, Inc., Information Resource Center, 

Administrative Record File, 105 Broadway, Oak Ridge, TN 37830 

94. 'I'. D. Richardson, Department of Biology, Box 504-A, University of North 

Alabama, Florence, AL 35682-0001 

95. S. P. Riddle, Environmental Restoration Division, EW-91, DOE Oak Ridge Field 

Office, P.O. Box 2001, Oak Ridge, TN 37830 

96. W. Schacher, Aquatic Habitat Protection Biologist, Tennessee Wildlife Resources 

Agency, 6032 W. Andrew Johnson Highway, Talbot, TN 37877 

97. R. C. Sleeman, Environmental Rcstoration Division, EW-91, DOE Oak Ridge 

Field Office, P.O. Box 2001, Oak Ridge, TN 37830 

98. D. Turner, 1201 Tuskegee Drive, Oak Ridge, TN 37830 

99. F. J. Wobber, Environmental Sciences Division, Office of Health and 

Environmental Research, ER-74, U.S. Department of Energy, Washington, DC 

20585 

100. Office of Assistant Manager for Energy Research and Development, DOE Oak 

Ridge Field Office, P.O. Box 2001, Oak Ridge, TN 37831-8600 

101-110. Office of Scientific and Technical Information, P.O. Box 62, Oak Ridge, TN 37831