(4) Crecelius, E. A., Bothner, M. H., Carpenter, R., Enuiron. Sci. Technol., 9,325-33 (1975). (5) Koide, M., Soutar, A., Goldberg, E. D., Earth Planet. Sei. Lett., 14,442-6 (1972). (6) Bruland, K. W., Bertine, K., Koide, M., Goldberg, E. D., Environ. Sci. Technol., 8,425-32 (1974). (7) Frey, H. W., Hein, R. F., Spruill, J . L., Report of the Natural Resources of Upper Newport Bay and Recommendations Concerning the Bay’s Development, Dept. of Fish and Game, State of California, 1970. (8) Koide, M., Bruland, K. W., Anal. Chim. Acta, 75,l-19 (1975). (9) Van Loon, J. C., Lichwa, J., Ruttan, D., Kinrade, J., Water, Air, Soil Pollut.. 2,473-82 (1973). (10) Perkin-Elmer Corp., Norwalk, Conn., Instruction Manual for Atomic Absorption Spectrophotometer, Model 403, 1973. (11) Gietzen, J. B., Orange County Flood Control District, private communication, 1977. (12) Leopold, L. B., Wolman, M. G., Miller, J. P., “Fluvial Processes in Geomorphology”, Freeman, San Francisco, Calif., 1964. (13) Gietzen, J. B., Franklin, E .J., Nestlinger, A. J., Mastrocola, N., Recht, W. J., Hydrological Data Report 1973-74 Season, Orange County Flood Control District, Santa Ana, Calif., 1974. (14) US.Geological Survey, Water R.esources Data for California, Water Year 1975, Vol 1, National Tech. Information Service, Springfield, Va., 1976. (15) Stevenson, R. E., Emery, K. O., “Marshlands a t Newport Bay, California”, Univ. of Southern California Press, Los Angeles, Calif., 1958. (16) Davidson, C. I., PhD thesis, California Institute of Technology, Los Angeles, Calif., 1977.
(depth: 0-1.5 m). However, at longer time exposure, which occurs for tidal flats, the data obtained were not sufficient for the determination of sedimentation rates. Rates determined by the Pb-210 technique were: 0.8 f 0.1 cm/yr for the channel between the southern large island in Upper Newport Bay and the west bank, and 1.8 f 0.4 cm/yr for a tidal creek 800 m north of the Narrows. Vertical profiles of heavy metals in dated sediment cores indicate that zinc and lead are the only metals of those investigated that show clearly increased levels in the upper strata, deposited since about 1955. The highest lead level (132 ppm) was found close to the mouth of the channel draining an urban area. Vertical profiles of heavy metals in sediment cores from the tidal flat south of the main dike show a clearly oscillating pattern, also shown by the average grain size. Thus, maximum concentration of a metal such as lead is associated by maximum grain size, indicating material carried by large storms. A plot of 4-year-averaged rainfall vs. time shows a similar oscillating pattern, so that maximum grain size can be matched with maximum rainfall. This strongly suggests a cause-effect relationship between patterns of rainfall and patterns of grain size and heavy metals. The sedimentation rate obtained for the tidal flat by this matching is 1.8 cm/yr in good agreement with the value of 1.8 f 0.4 cm/yr obtained by thePb-210 method for a tidal creek that runs through the flat.
Received for review November 7, 1977. Accepted May 4, 1978. Work supported i n part by grants from Statens Naturvidenskabelige Forskningsrad, Otto Mtjnsteds Fond, Thomas B. Thriges Fond, Knud HQjgards Fond, and Handelsbankens Studierejselegat.
Acknowledgment
Supplementary Material Available. Additional graphs for Cr, M n , Fe, Co, and Cu (Figure 3 ) will appear following these pages i n the microfilm edition of this volume of the journal (10 pages). Photocopies of the supplementary material from this paper only or microfiche (105 X 148 m m , 2 4 X reduction, negatives) containing all of the supplementary material for the papers in this issue may be obtained f r o m the Business Operations Office,Books and Journals Division, American Chemical Society, 1155 16th St., N . W., Washington, D.C. 20036. Remit check or money order for $6.50 for photocopy or $3.00 for microfiche, referring to code number ES&T-781168.
We thank V. P. Guinn and E. D. Goldberg for valuable comments on this work.
Literature Cited (1) Sartor, J. D., Boyd, G. B., Agardy, F. J., J. Water Pollut. Control Fed., 46,458-67 (1974). (2) Whiuule. W.. Jr.. Hunter. J . V.. ibid.. 49. 15-23 (1977). (3) Galloway, J., PhD thesis; University of’california, San Diego, Calif., 1972.
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Assessment of Intermittently Chlorinated Heated Effluents on Survival of Adult Rainbow Trout ( S a h o gairdneri) at Power Generating Facilities lbrahim H. Zeitoun Department of Environmental Services, Consumers Power Co., Jackson, Mich. 49201 ~
Monthly 96-h bioassays were carried out from November 1975 to June 1976 at the J. H. Campbell Plant of the Consumers Power Co., Michigan, to determine the effects of intermittent chlorination on the survival of caged rainbow trout (Salrno gairdneri). The results indicated that eight covariates, which included total and free chlorine-exposure time integrations, dissolved oxygen supersaturation and temperature, contributed significantly to the mortalities exhibited among caged fish. Squared multiple correlation coefficients were used to determine the relative effects of these significant covariates on fish mortality since the individual function of these variables appeared to be additive. A maximum value of 0.3 mg/L TRCl per 54 min of exposure time was extrapolated as a safe concentration that would result in the same mortality rate as in controls which were not exposed to chlorine. Blood analysis indicated that chlorine was not the primary cause of the observed stress.
0013-936X/78/0912-1173$01.00/0
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A matrix of algae, bacteria, fungi, and other organisms develops on the cooling surfaces of condensers of steam power plants that use natural waters for cooling. This biofouling reduces the flow of cooling waters and insulates the heat exchange’ surface, which reduces the efficiency of electrical generation and causes a considerable power loss. T o counteract the biofouling buildup, condensers are periodically chlorinated. Although chlorination is normally the most economical and practical means for controlling the fouling organisms ( I ) , the chlorinated effluents could produce localized effects on aquatic life in natural habitats ( 2 , 3 ) . The U S . Environmental Protection Agency ( 4 )limited the discharge of free available chlorine from power plants to a maximum concentration of 0.5 mg/L and an average concentration of 0.2 mg/L for not more than 2 h daily. Mattice and Zittel ( 5 ) used the available chlorine literature and extrapolated acute chlorine levels that would be considered safe for aquatic organisms. The acute toxicity threshold for freshwater organisms was approximated by a straight line connecting
1978 American Chemical Society
Volume 12, Number 10, October 1978
1173
ONSOMERS POWER COMPANV
LAKE
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0
250
500
METERS
Flgure 1. Control and experimental stations Numbers 1, 2. 3. 4. 5 . and 6 denote control unheated tank. control heated tank, inlet control cage, upstream test cage, middle test cage, downstream test cage, respectively
0.015 mg/L for 7200 min (5 days) to 1.0 mg/L for 1.1min. Basch and Truchan (6) postulated that 0.04 mg/L total residual chlorine (TRCl) when water temperature is less than 21.1 "C (70 O F ) and 0.2 mg/L TRCl when water temperature is above 21.1 OC are safe for all fish species for chlorination periods not exceeding 30 min. They also suggested that the daily number of these allowable chlorinations should be determined for each plant on a case-by-case basis. In the case of power plants, chlorine as gas or hypochlorite salt solution is normally added immediately upstream from the condenser for a short period as a shock defouling treatment. As a result, the discharged chlorine concentration, when plotted against time, will portray a more or less bell-shaped curve (7,8). Therefore, safe chlorine concentrations for fish are difficult to extrapolate from continuous chlorine exposure bioassays. Also, exposure of fish to power plant effluents does not preclude the influence of other environmental factors that could distort the output of a test when all mortalities are attributed to only one variable. This study was undertaken to determine the effect of intermittent chlorinations on the survival of caged trout; the role of other environmental factors that coexist with the chlorinated effluents in the discharge channel on fish; and the hematological changes a t the end of the bioassays and compare them to previously identified blood changes as a result of chronic (9) and acute (10,l I ) chlorine toxicity to identify the source of stress.
Experimental The J. H. Campbell Plant, which was chosen for this field study, is a coal-fired, 2-unit electric generating facility located on the southeastern shore of Lake Michigan, Ottawa County, Michigan. The electrical output of the 2 units is 267 and 372 MWe. Condenser cooling water is drawn from Lake Michigan through Pigeon Lake (Figure.1) a t a rate of 1140 m3/min via 1174
Environmental Science & Technology
an inlet channel. The cooling water, after passing through the condensers, is emptied into a discharge channel that opens into Lake Michigan. In this study, one experiment was carried out monthly from November 1975 through June 1976. Each monthly test included an in-channel bioassay and a hematological study. In-Channel Bioassay. Mature 2-3-year-old, cultured rainbow trout ( S a l m o gairdneri) were used. Prior to the bioassays, duplicate groups of 10-15 thermally acclimated fish each were randomly allocated in three double-unit cages positioned in the middle of upstream (Station 4), middle (Station 5), and downstream (Station 6) points of the discharge channel (Figure 1).Another similar cage was placed at approximately the middle of the intake channel and used as the control (Station 3). Since the water temperature in the discharge channel was warmer during plant operation than that in the intake channel, one control was not sufficient. A wet laboratory was established in a trailer on the shore of the intake channel opposite to the control cage (Figure 1)to house a double-unit control tank. This wet laboratory received its water from the intake channel using a submerged pump. The pumped water was heated to approximately the discharge channel temperatures and circulated through the tank that was termed the control heated tank (Station 2). A second unheated control tank (Station 1)was installed outside the trailer and received the intake water directly. Each unit of Stations 1 and 2 contained approximately 340 L of water, and water circulation was over 11L/min. The approach using multiple controls was intended to compare the effect of cages (Station 3) and tanks (Station 1) as holding devices for fish during the test. Fish were placed in tanks and cages a t least 18 h before the first chlorination. Condenser chlorination at this plant occurs once daily for 30 min. All these monthly bioassays were carried out for four days, and fish were exposed to one chlorination daily.
Table 1. Summary of Monthly Means ( f S E ) of Mortality Percentages, Weight, and Length of Rainbow Trout (Salmo gairdneri) Used in Control and Test Groups of In-Channel Bioassays Nov.
control groups Stations
1 2
3 significance days
(PJ 1 2 3 4
significance ( P ) test groups Stations
4 5 6
significance ( P ) days
significance weight, g length, mm
(PJ
1 2 3 4
0 0 0
. . .a 0 0 0 0
. . .a 0 3.3 (0.39) 3.3 (0.39) NS
0 0 0 2.2 (0.59) NS 268 (5.4) 282 (1.7)
Dec.
1.1 (1.1) 5.6(1.1) 0 NS 0 0 6.7 (1.9)
Jan.
100 0
0
. . .a 33.3 33.3 33.3
Feb.
... 0 0
. . .a 0 0 0
... . . .a
... . . .a
33.3 (5.0) 45.2 (5.0) 34.5 (5.0) NS 6.3 (6.2) 33.9 (6.2) 100.0 (6.2)
100 100 100
0
