ML20151M109
| ML20151M109 | |
| Person / Time | |
|---|---|
| Site: | Seabrook  |
| Issue date: | 04/24/1987 |
| From: | Dow K YANKEE ATOMIC ELECTRIC CO. |
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| Shared Package | |
| ML20151L940 | List: |
| References | |
| YAEC-1576, NUDOCS 8804220239 | |
| Download: ML20151M109 (39) | |
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HALOGENATED HYDROCARBON PRODUCTION AND THE POTENTIAL OF BI0 ACCUMULATION AT SEABROOK STATION By K. W. Dow February 1987
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Prepared By:
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Yankee Atomic Electric Company Nuclear Services Division 1671 Worcester Road Framingham, Massachusetts 01701 4962R 8804220239 880408 PDR ADOCK 05000443 D
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- .i DISCLAIMER OF RESPONSIBILITY This document was prepared by Yankee Atomic Electric Company
("Yankee"). The use of information contained in this document by anyone other j
than Yankee, or the Organization for which this document was prepared under contract, is not authorized and, with respect to any unauthorized use, neither Yankee nor its officers, directors, agents, or amployees assume any obligation, responsibility, or liability or make any warranty or representation as to the accuracy or completeness of the material contained in this document.
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e ABSTRACT To control the growth of biofouling organisms within the Circulating Water and Service Water Systems at Seabrook Station, continuous low-level chlorination is employed. This involves the gt.neration of a sodium hypochlorite solution from seawater and injecting this solution into the intake stream at a maximum dosage of approximately 2.0 mg/1. The injection is such that a concentration of 0.2 mg/l total residual oxidant, measured as equivalent C1, is not exceeded within the discharge transition structure.
2 The presence of halogenated hydrocarbons formed through the use of continuous chlorination, and the potential for bioaccumulation of these within
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the tissues of marine organisms, was reviewed as part of the Seabrook Station chlorine minimization study.
To evaluate the formation of halogenated i
hydrocarbons, samples of intake water were chlorinated under controlled-conditions, simulating the time-temperature path through the Seabrook Station Cooling Water System and returned to the lab for analysis. Bioaccumulation of those compounds formed was assessed through review of the open literature for those organisms potentially affected by the cooling water discharge.
Halogenated hydrocarbon formation under the normal operating conditions l
at Seabrook Station was determined to be limited to that of bromoform and I
dibromochloromethane. Bromoform was found to develop to a maximum concentration of 160 ppb (parts per billion) following a ISO-minute travel time through the test system (approximate time from intake to discharge to the Atlantic Ocean). Dibromochloromethane formed to a maximum concentration of 3 i
ppb over the same period. These concentrations are well below levels associated with acute toxicity. Rapid dilution (approximately 10:1) of discharged cooling water with the receiving water along with additional chemical reactions and volatilization, will dramatically reduce the concentration of released halogenated hydrocarbon compounds to below those associated with chronic exposure mortalities of marine organisms.
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Review of the potential for bioaccumulation of these compounds determined that while they may develop within tissue to levels which approximate those within the surrounding environment, they are rapidly 1
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ABSTRACT (Continued) i i
depurated once an organism leaves to an area of reduced concentration.
In addition, acute mortality due to exposure has not been found to occur until concentrations reach at least two orders of magnitude above those formed I
during this test and at other power plant sites identified within the literature reviewed. Thus, the formation of halogenated hydrocarbons in the discharge of Seabrook Station cooling water will not cause bioaccumulation within the environment, and the~ environmental impact of these compounds is considered negligible.
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TABLE OF CONTENTS l
P*K2 DISCLAIMER OF RESPONSIBILITY.....................................
11 ABSTRACT.........................................................
iii LIST OF IABLES...................................................
vi AC KNOWLEDG EMENT..................................................
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1.0 INTRODUCTION
1 2.0 CHLORINE UTILIZATION.............................................
2 1
2.1 System Design..............................................
2 2.2 Chlorine Chemistry.........................................
2 3.0 HALOGENATED HYDROCARBON FORMATION................................
6 3.1 Experimental Design........................................
6 3.2 Experimental Results.......................................
7 3.3 Discussion.................................................
8 4.0 BI0 ACCUMULATION P0TENTIAL........................................
10 4.1 Literature Review..........................................
10 4.2 Discussion.................................................
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5.0 CONCLUSION
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6.0 REFERENCES
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LIST OF TABLES Number Title Page 1
Annual Means and Coefficients of Variation of Irradiance and Water Quality Parameters at Nearfield Station P2, 1978-1984 17 2
Volatile Organic Analysis by EPA Method 624 -
Test 7/9/85; 2.5 ppm TRO 18 L
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3 Chlorine Demand Evaluation - 7/9/85 20 4
Volatile Organic Analysis by EPA Method 601 -
Test 9/12/85; 3.44 ppm TRO 21 5
Volatile Organic Analysis by EPA Method 601 -
Test 9/18/85; 1.92 ppm TRO 27 6
Volatile Organic Analysis by EPA Method 624 -
Test 9/18/85; 1.92 ppm TRO 28
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7 Organic Priority Pollutant Analysis by EPA Method 625 -
Test 9/18/85; 1.92 ppm TKO 30 8
Chlorine Demand Evaluation - 9/18/85 32
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ACKNOWLEDGEMENTS 1
i This report was prepared by the Yankee Atomic Electric Company's Environmental Sciences Group, John P. Jacobson, Manager. Field work was performed by Marine Blocontrol Corporation (MBC) located in Sandwich Massachusetts, and involved the acquisition of the offshore samples and the performance of the chlorine innoculation phase. Energy Resources Company of f
Cambridge Massachusetts analyzed the test water samples, as subcontractor to MBC, determining the occurrence and relative concentration of the halogenated hydrocarbon compounds formed.
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HALOGENATED HYDROCARBON PRODUCTION AND THE POTENTIAL OF BI0 ACCUMULATION AT SEABROOK STATION
1.0 INTRODUCTION
In compliance with the provisions of the Federal Clean Water Act, as amended (33 U.S.C., Paragraph 125% et seq.; the "CWA"), the owners of Seabrook Station are authorized to discharge to the Atlantic Ocean in accordance with effluent limitations as set forth by the Environmental Protection Agency and the State of New Hampshire. These limitations along with applicable monitoring requirements are presented within Seabrook Station's National Pollutant Discharge Elimination System (NPDES) permit. Through this NPDES pe rmit, the permittee is required to conduct a chlorine minimization program.
Among other aspects, this program is designed to determine the minimum level of chlorine discharged to the receiving waters while maintaining suitable biofouling control of the Intake Cooling Water System and condenser efficiency.
l As part of this chlorine minimization program for Seabrook Station, a study was conducted to measure the presence of halogenated hydrocarbons which f
might potentially be discharged from the Cirenlating Water System.
In addition, a literature review was conducted to determine the potential for bioaccumulation of these halogenated hydrocarbons once discharged into the marine environment.
The results of these activities have shown that there is limited formation of halogenated hydrocarbon compounds in seawater, and that the accumulation of these compounds within the tissues of marine organisms is approximately equal to concentrations found within the surrounding water body. Furthermore, these compounds were found to be rapidly and completely depurated from tissue, thus biomagnification through '.he food chain appears unlikely.
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2.0 CHLORINE UTILIZATION 2.1 System Design Sodium hypochlorite solution, the biocide utilized to control marine
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growth within the Circulating and Service Water Systems, is produced on-site by two hypochlorite generators using 600 gpm of seawater taken from the j
Circulating Water System. These generators are capable of producing about 424 pounds of equivalent chlorine per hour in a hypochlorite solution. Chlorine is injected at a rate such that a concentration of 0.2 mg/l total residual j
oxidant, measured as equivalent chlorine, is not exceeded within the discharge transition structure on-site. During the 85-minute transit time from the discharge transition structure to the offshore discharge diffusers (one-unit operation), the total residual oxidant will continue to decrease through 1
increased decay at elevated water temperatures (Wong, 1980). The total i
residual oxidant concentration release will then be diluted by the diffuser flow, approximately 10 to 1, and further reduced through additional chemical reactions with ambient water and through volatilization.
2.2 Chlorine Chemistry The chlorination of seawater results in an immediate conversion of hypochlorous acid (H001) to both hypobromous acid (HOBr) and hypolodous acid j
(HOI), yielding chloride ions (C1"). This results in no loss of oxidizing i
capacity. EPRI (1980) reviewed literature describing the reactions of chlorine in seawater.
In this review, Johnson (1977) reported the initial 1
reaction described above to proceed to 50% completion within 0.01 minutes while Sugam and Helz (1977) indicated it was essentially 99% complete within l
ten seconds. References by EPRI to Sugawara and Terada (1958) and Carpenter and Macaldy (1976) revealed that iodine in seawater is in an oxidized state as i
lodate, and unavailable to react with hypochlorous acid. Bromide on the other hand, is described as being in ample supply, estimated at 68 mg/1, and able to I
consume more than 27 mg/l of chlorine.
(Lewis (1966); within EPRI (1980).)
1 Hypobromous acid, under the conditions found at Seabrook, partially j
dissociates into hypobromite ions (obr').
Both items are considered to be 1 4962R 9
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the free available or residual oxidant.
Free residual bromine is more i
reactive than free residual chlorine, yet enters into the same type reactions.
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The decay of chlorine in natural seawater is extremely variable.
f Coldman, et al. (1978) indicated that losses due to chlorine demand occurred 1
in two stages; a first very rapid and significant demand, followed by a continuous loss at a reduced rate. They indicated that in natural seawater.
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the two minute chlorine demand ranged from 0.42 - 0.50 mg/l following an i
t initial chlorine dose of 1.02 mg/l and 2.88 mg/1, respectively.
j, Hostgaard-Jensen (1977) indicated that in Denmark, seawater reduced an initial l
chlorine dose of 2.0 mg/1, to 0.5 mg/l within 10 minutes, and to 0.2 mg/l i
after 60 minutes.
Fava and Thomas (1977), described studies on chlorine j
demand, giving a value for the demand in clean seawater of 1.5 mg/l following 1
'a 10-minute contact period.
For coastal waters, demand values from 0.035 to 0.41 mg/l following a five-minute contact period, and values of C.50 to 5.0 mg/l following a three-hour contact period were given.
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Frederick (1979) examined the decay rate of equivalent chlorine in seawater samples at Seabrook. He found that the decayed amount at any time 1
appeared to vary from month to month over a narrow range, and that the amount of equivalent chlorine decayed, rose with either time or an increased inoculation, indicating that there may not be a fixed chlorine demand level.
l Based on a 2.0 mg/l injection dose, his data indicates that the chlorine decay
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in seawater following a 12J-minute period averages 1.0 mg/l over a twelve-month period. Va'ues ranged from 0.8 mg/l to 1.24 mg/1, a decay of 40 to 621, respectively.
further decay at Seabrook Station is expected to occur q
due to the elevated temperatures within the cooling water system, i
The products from chlorination depend upon pH, salinity, the i
concentrations of annonia-nitrogen and organic carbon, temperature, pressure.
i and the concentration of the applied chlorine. Normally, the conversion of hypochlorite to hypobromite prevents the production of chloramines, yielding j
brosamine analogs.
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With the exception of temperature, the physical and chemical parametera l
of the Atlantic Ocean at the iatake and discharge structures do not vary 3
significantly (Table 1).
In the marine environment, pH generally remains l
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constant due to natural buffering capacities; however, even within the range of pH values at Seabrook (roughly 7.8-8.4), the proportions of hypobromous acid and hypobromite ions may be affected.
The presence of ammonia in chlorinated seawater has a significant effect on the concentration of residual oxidants. Sugam and Helz (1977) as referenced in EPRI (1980), determined that at pH 8.0 and with a 35 ppt salinity, seawater containing 0.15 mg/l ammonia dosed at 0.5 mg/l chlorine, would result in an equal formation of chloramines and hypobromous acid -
hypobromite. A decrease in either pH or ammonia-nitrogen reduces the rate of chloramine production.
Sugam and Helz also found that in seawater with ammonia concentrations of 0.01 mg/1, tribromamine is the only combined bromine residual formed. At ammonia concentrations of 1.0 mg/l and a pH of 8.0, the residual was determined to be entirely that of combined bromine (70%
dibromamine, 25% conobromamine and 5% tribromamine). The major residual oxidants formed from the chlorination of seawater would then be either free bromine and tribromamine, or dibromamine and monochloramine, depending upon the ammonia concentration and halogen-to-nitrogen ratios.
At Seabrook Station, free bromine and tribromamine will dominate as ammonia-nitrogen levels are relatively low. 0.01 mg/l to 0.09 mg/l (Frederick, 1979).
Both dibromamine and tribromamine are unstable, decomposing to nitrogen gas and bromide ions, and to nitrogen gas, bromide ions and hypobromous acid, respectively. Depending upon environmental conditions, the decomposition from tribomamine results in roughly 90% decay in approximately 30 minutes. Based on the chemical reactivity of residual bromine, the oxidation of organic carbon (aminn acids) with free bromine to form organic bromamines is another available reaction.
Envirosphere (1981) indicated that salinity and the toxicity to chlorinated seawater were positively correlated, described as a lower 24-hour and 48-hour LC50 (the concentration at which there is 50% mortality of a j
species over a 24-or 48-hour exposure period). The causes of these lower values are unknown but suspected to be related to chemical interactions at higher salinities and to the physiology of the species.
EPRI (1980) also reviewed data pertinent to salinity and toxicity. Here, it was indicated that an evaluation between the two was complicated by the fact that the chemical 4962R
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form, concentration, and duration of residual oxidant species are also affected by salinity. At Seabrook Station, the salinity is relatively high and stable, however, the dilution and chemical reactions of biocides with ambient waters upon discharge and the subsequent limited period of exposure reduces these effects.
Wong (1980) indicated that for a given dosage and contact time, residual chlorine concentrations were seen to decreasu systematically with increased temperatures.
Higher temperatures were found to yield higher chlorine demands. He suggested that this increase in demand represents reactions with organic compounds that normally do not react at lower temperatures.
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Various effects of temperature on the toxicity of chlorinated cooling water have also been reported.
Investigations have found that the effects of increased temperature range from producing no change in toxicity, to causing increased toxicity.
EPRI (1980) suggests that the synergistic interaction between temperature and chlorinated cooling water would not be great for species residing in the area of the thermal plume.
Biocides entering the receiving waters via the Seabrook Station discharge are diluted by a factor of 10 to 1.
As previously mentioned, a total residual oxidant concentration of 0.2 mg/1, measured at the discharge transition structure, will further decay during the transit time through the j
discharge tunnel. Additional reduction through the decay of oxident is expected to occur upon release from the cooling system into the receiving waters. Here, reductions in total residual la expected through volatilization, through renewed ambient chlorine demand of the entrained water, and through reactions between the oxidant and ultraviolet light which results in a light-induced oxidation of hypobromite to bromate thereby reducing the concentration of free bromine.
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3.0 HALOGENATED HYDROCARBON FORMATION 3.1 Experimental Design To determine the halogenated hydrocarbons (bromine and/or chlorine containing trihalomethanes) that are formed from the chlorination of seawater at Seabrook Station, Marine Biocontrol Corporation was consigned to obtain samples of water from the region of the Seabrook intake structures and return these to the laboratory for testing.
During three separate tests, volumes of water samples taken, as described above, were chlorinated under controlled conditions, simulating the time-temperature path through the Seabrook Station Circulating Water System.
A total of 2.38 mg/1, 3.44 mg/1, and 1.92 mg/l of chlorine, measured as Total Residual 0xidant (TRO), was added to separate samples of water from the intake region. Ninety-seven minutes following chlorine addition (an approximation of the transit time from the offshore intakes to the condensers), the water was heated to 39 F over ambient with quartz immersion heaters. This temperature rise corresponds to the design AT following passage through the station condensers.
The water was then allowed to cool naturally to an end time of 182 minutes (the total transit time through the Seabrook Circulating Water System).
The formation of volatile organics was measured during this simulated transit time through the Circulating Water System.
Samples for volatile organic analysis were taken directly after sodium hypochlorite addition (0 minutes), af ter 45 minutes, 97 minutes (af ter heating), and at 182 minutes.
Chlorine reactions were stopped at the time of sampling through the addition of s7dium thiosulfatt. Control samples of nonchlorinated intake water, with and without the addition of sodium thiosulfate were also taken.
Samples were sealed in sample vials, placed on ice, and delivered for analysis. Laboratory analysis for volatile halogenated organics was performed using EPA Methods 624 and 601 (Volatile Organics) and EPA Method 625 (Semivolatile Organics).
On July 9, 1985, water samples from the intake region were taken to the lab and inoculated with 2.38 mg/l of a sodium hypochlorite solution. 4962R
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Following this, samples for volatile halogenated organic analysis were drawn at 0 minutes, 45 minutes, 97 minutes, and 182 minutes.
Samples of nonchlorinated water with and without the addition of sodium thiosulfate were also taken. Sealed within sample vials and placed on ice, these were transported to an analytical lab (Energy Resources Company) for analysis for the presence of halogenated organics via EPA Method 624 (Table 2).
This method covers the determination of a number of purgeable organics utilizing a gas chromatograph / mass spectrometer.
At the same time that volatile organics were being obtained, measurements of chlorine demand were also taken (Table 3).
These were calculated by measuring intake water chlorine residual concentrations (measured as TRO with a Wallace & Tiernan amperometric titrator) at specific times, and subtracted f rom an identical volume of chlorine-f ree water which had been chlorinated with an identical dose at the same time.
On September 12, 1985, a second set of data were obtained under the same sampling procedure.
The desired initial dosage of 2.0 mg/1, however, was exceeded (3.44 mg/1) due to a faulty titrator.
EPA Method 601, which determines the presence of the same compounds as Method 624, but with lower detection limits, was utilized for the 0 minute, 45 minute, 97 minute, and 182 minute control-thiosulfate, control no-chlorine and treated samples (Table 4).
i As a result of the overdosage on September 12, 1985, a third treatment run was performed on September 18, 1985.
Treatment and sampling for halogenated organics was performed as previously described, with the initial dose being 1.92 mg/l TRO.
EPA Methods 601 and 624 were utilized for the analysis of the 182-minute samples only (Tables 5 and 6, respectively).
In addition, EPA Method 625, which identifies semivolatile organics (organic priority pollutant analysis), was performed (Table 7).
As during July, the chlorine demand was calculated throughout the test (Table 8).
3.2 Experimental Results Consistent with the findings of Bean et al. (1981) and Carpenter and Smith (1978), bromoform was identified as the major trihalomethane (THM) 4962R
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compound formed through the chlorination of seawater.
Following a 180-minute contact time (the design period of flow through the Circulating Water System),
the concentration of bromoform was found to be 150 ppb (parts per billion) and 160 ppb following an initial sodium hypochlorite dose of 1.92 mg/l TRO and 2.58 mg/l TRO respectively. Standard Method No. 624 was utilized in this evaluation. A concentration of 130 ppb of bromoform and 2.5 ppb and 3.0 ppb of dibromochloromethane was determined through Standard Method No. 601 following an applied chlorine dose of 1.92 mg/l TRO and 3.44 mg/l TRO, respectively. These were the only volatile organics determined through both sets of analysis. Standard Method No. 625, utilized for a review of semivola' tile organics, revealed that no additional compounds or organic priority pollutants were generated.
3.3 Discussion The fate of trihalomethane compounds is largely controlled by the physical properties of the individual compounds and those of the receiving water. Perwalk et al. (1980), indicated that the volatility of trihalomethanes is an important environmental factor which substantially reduces concentrations in aqueous solutions.
An increase in temperature and water turbulence would increase the rate of loss.
In their study, it was found that the half life of these compounds in stirred aqueous solutions was approximately 20 minutes. Other potential fates are adsorption, hydrolysis, bloaccumulation, and biodegradation; however, these appeared low when compared to volatilization. Carpenter and Smith (1978) indicated that in addition, light reduced the production of bromoform by 25-30%.
Perwalk et al. (1980),
i noted that the concentration of bromoform within the natural waters of New England and the mid-Atlantic were between 1-10 ppb and that the concentration of dibromochloromethane was between 0.1-10 ppb.
Studies conducted by Mattice et al. (1981) further documented the volatility of trihalomethanes. Their decay studies indicated that the half-lives were 5.6 hours6.944444e-5 days <br />0.00167 hours <br />9.920635e-6 weeks <br />2.283e-6 months <br /> and 6.9 hours1.041667e-4 days <br />0.0025 hours <br />1.488095e-5 weeks <br />3.4245e-6 months <br /> for dibromochloromethane and bromoform, respectively; this due primarily to volatilization. Mattice noted that the persistence of trihalomethanes may be influenced by processes such as photolysis, adsorption, and microbial degradation. He concluded, however, that their persistence in the environment was unlikely. 4962R
Important considerations when evaluating potential environmental effects are the influence of effluent concentration and the duration of exposure. The decay of residual chlorine depends upon time, temperature, and mixing characteristics of the discharge stream within the receiving waters.
At Seabrook Station, multiport diffusers provide a 10:1 dilution with rapid mixing, thus affording chemical reactions with ambient water, thus reducing concentrations within the region of the discharge. With increased distance from the discharge, chlorine and chlorine nroduced oxidants will continue to drop as additional mixing, dilution, and reactions occur.
Exposure, while related to the decline of chlorine and chlorine produced oxidant, is also a function of an organism's ability to maintain itself within an area of elevated concentration, Mattice (1983).
Planktonic organisms which passively drift into the discharge plume will not be able to maintain their positions in the region of elevated concentrations. With a diffuser system designed to avoid bottom impact, benthic organisms will r.ot be exposed to continuous levels of chlorine or chlorine produced oxidants.
Fish species will be subjected to limited exposure times and minimal concentration which will mitigate possible effects of exposure to discharged biocides.
Hall et al. (1981), conducted studies on the avoidance response of juvenile Atlantic menhaden subjected to simultaneous chlorine and AT conditions. Through these, it was found that a temperature preference did not override avoidance behavior to TRC (Total Residual Chlorine) levels. They determined (on the contrary), that there was greater avoidance to elevated TRC when there was an associated temperature component.
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4.0 BI0 ACCUMULATION POTENTIAL t9 4.1 Literature Review m
A review of available liter'ature on the bioaccumulation of halogenated hydrocarbons (trihalomethanes) was performed.
In particular, the two halogenated compounds identified through laboratory studies at Seabrook Station, bromoform and dibromochloromethane, were keyed upon.
The literature indicates that while there is a concentration of these compounds within the tissues of organisms, it is only to levels experienced within the surrounding environment and these are depurated rapidly once the organism is removed from the region.
Gibson et al. (1979), tested the relative toxicity of bromoform and the probability of bioaccumulation through a series of bioassays on five marine species. Their results show that bromoform does not cause acute effects at concentrations below 1 mg/l (1,000 ppb). The 96-hour LC50 (the concentration which caused mortality to 50% of the organisms after a 96-hour exposure) through a 28-day uptake and 28-day depuration study ranged from approximately 7 mg/l for menhaden (Brevoortia tyrannus) to greater than 40 mg/l for the littleneck clam (Protothaca staminea).
In a review of the ambient life water quality criteria for chlorine edited by Brungs (1983), adult blue crabs were found to be insensitive to
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700-800 ppb CP0 (chlorine produced oxidants). Other invertebrates (amphipods, hermit crabs, and shrimp) were found to have only intermediate sensitivity to CP0; LC f 90-687 ppb.
Brief exposure to CP0 did not cause substantial 50 damage to phytoplankton.
In this review, Goldman and Quinby (1979) were found to conclude that phytoplankton subjected to a combined CP0 and temperature stress, recovered with no prolonged effect on growth rates of natural populations.
Uptake and depuration studies were also reported by Gibson et al.
(1981). For those molluscan species tested, tissue concentrations were found
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to be approximately equal to the concentrations found within the surrounding water. While the body burdens appeared higher during the first week of the 28-day uptake period, there was a corresponding drop during the remaining l 4962R J
I period with tissue concentrations remaining close to that of the environment.
The eastern oyster (Crassostrea virginica), a species not prevalent in coastal waters adjacent to Seabrook Station, appeared as an exception with only a few individuals of those tested, concentrating up to fif teen times the concentration found within the environment during their test study.
Scott et al. (1981), also reviewed bioconcentration within the American oyster and found conversely that substantial quantities of bromoform did not bioconcentrate.
In addition, bromoform was found to be completely depurated from tissues within 2-4 days following exposure.
When reviewing the uptake and depuration of bromoform within the tissues of the brown shrimp (Penaeus acztecus) and Atlantic menhaden (Brevoortia tyrannus), Gibson et al. (1981) found that both developed body burdens in excess of a 1.0 mg/l and 0.1 mg/l test setup over the first week of a 28-day period similar to that of the molluscan species.
These were depurated to approximate water concentrations over the remaining weeks of each study.
Both depurated all bromoform from their tissues within 48 hours5.555556e-4 days <br />0.0133 hours <br />7.936508e-5 weeks <br />1.8264e-5 months <br /> following exposure.
Brungs (1983) also described results presented from studies conducted by Seegert and Bogardus (1980) which found that chlorine was not persistent within the environment and that it did not bioaccumulate.
4.2 Discussion The literature reviewed on the potential for the bioaccumulation of bromoform, dibromochloromethane, and for those halogenated compounds not found in the Seabrook chlorinated seawater samples, indicated that while there is an accumulation within the tissues of exposed organisms, it is generally to levels that approximate that found in the environment.
In some instances there appeared to be either limited magnifica' tion within a few individuals, or increased concentrations over an initial period which fell to levels consistent with the environment.
All organisms tested were found to completely depurate these compounds rapidly when removed from the region of elevated -
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concentrations. Bean et al. (1981), Gibson et al. (1979) and Mattice et al.
(1981), indicate that acute mortality (96-hr LC
's) due to exposure to 50 trihalomethanes occurs at concentrations at least_two orders of magnitude above that released from chlorination activities at power plants. These power plant concentrations are consistent with concentrations obtained during our testing and therefore can be expected to be typical for Seabrook Station.
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5.0 CONCLUSION
1 The formation of trihalomethanes through the chlorination of water from the Atlantic Ocean was reviewed during three separate occasions. During each test, samples of water from the region of Seabrook's offshore intake structures was chlorinated and then analyzed for the presence of the halogenated hydrocarbon products. Utilizing EPA Methods 624 and 601 for the analysis of volatile organics, only bromoform and dibromochloromethane were detected, having concentrations well below toxicity levels.
EPA Method 625, which was utilized for the analysis for semivolatile organics, revealed that these compounds were not produced.
Exposure to trihalomethanes is dependent on both time and concentration. Released bromoform and dibromochloromethane, as well as other reaction products, will experience a 10:1 dilution and renewed reaction with the chemical demand of the ambient environment.
In addition, due to the configuration of the offshore diffusers, organisms will be unable to maintain themselves within the discharge stream, which with the associated temperature component will be buoyant, avoiding bottom contact.
Exposure to released concentrations of bromoform and dibromochloromethane is expected to be minimal, thus the potential for accumulation within the tissues of those organisms exposed minimal. The studies reviewed within the literature have documented that in general, an organism will develop released trihalomethane compounds within body tissues, only to those levels experienced within the environment.
The possibility of biomagnification through the food l
chain was not found to occur as accumulated compounds were completely and rapidly depurated once exposure was terminated.
The concentration and makeup of halogenated hydrocarbon compounds j
determined within this study, follow closely the results of studies identified within the literature and at other coastal power plants under similar conditions. These determined that the discharge was at least two orders of magnitude below those identified as causing acute mortality within test organisms. 4962R
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The operation of the chlorination system at Seabrook Station is therefore expected to produce only limited concentrations of two halogenated hydrocarbon compounds, bromoform, and dibromochloromethane.
Exposure to these will result in only minimal levels within tissues of marine organisms if at all, as a brief duration within the discharge plume will limit exposure and rapid depuration once the organism is outside the discharge region will occur. Continued loss through dilution and volatilization of these compounds will likewise reduce those available for exposure. Given the data obtained in this study which follows closely that seen within the referenced documents, marine organisms will not be exposed to, and will not accumulate high levels of halogenated hydrocarbons within body tissues.
Thus, the formation of halogenated hydrocarbons in the Seabrook Station discharge will have negligible environmental impact.
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6.0 REFERENCES
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1.
Bean, R. M. et al. (1981). Biocide By-Products in Aquatic Environments; j
Final Report September 10, 1976-September 30, 1979, NUREG/CR-1300.
Prepared by Battelle, Pacific Northwest Laboratories for the U.S. Nuclear Regulatory Comission.
2.
Carpenter, J. H. and C. A. Smith, Reactions in Chlorinated Seawater in Water Chlorination: Environmental Impact and Health Effects. Volume 2, R. L. Jolley, H. Gorchev, and D. H. Hamiton, Jr., EDS (Ann Arbor, Michigan, Ann Arbor Science Publishers, Inc., 1978), pp. 195-207.
3.
Electric Power Research Institute, 1980. Review of Open Literature on Effects of Chlorination on Aquatic Organisms.
EPRI EA-1491 Project 877.
4.
Envirosphere Company, 1981. Chlorine Toxicity as a Function of Environmental Variables and Species Tolerance for Edison Electric Institute.
i 5.
Fava, J. A. and D. L. Thomas, 1977.
Use of Chlorine for Antifouling on Ocean Thermal Energy Conversion (OTEC) Power Plants. Proceedings of the OTEC Biofouling and Corrosion Symposium, August 1978.
6.
Frederick, L.
C., 1979. Chlorine Decay in Seawater. Public Service of New Hampshire.
7.
Gibson, C. I. et al., 1979. Toxicity and Effects of Bromoform on Five Marine Species, NUREG/CR-0835.
Prepared by Battelle, Pacific Northwest Laboratories for the U.S. Nucicar Regulatory Commission.
8.
Gibson, C. I. et al., 1981. Toxicity, Bioaccumulation, and Depuration of l
Bromoform in Five Marine Species, NUREG/CR-1297.
Prepared by Battelle, Pacific Northwest Laboratories for the U.S. Nuclear Regulatory Commission.
9.
Goldman, J.
C., et al., 1978. Chlorine Disappearance in Seawater. Woods Hole Oceanographic Institution; Water Research, Volume 13, pp. 315-323.
- 10. Hall, L. W. et al., Avoidance Responses of Juvenile Atlantic Menhaden (Brevoortia tyrannus), Subjected to Simultaneous Chlorine and AT Conditions, in Water Chlorination: Environmental Impact and Health i
Effects, Volume 4, Book 2. R. L. Jolley, W. A. Brungs, J. A. Cotruvo, R. B. Cumming, J. S. Mattice, and V. A. Jacobs, EDS (Ann Arbor, Michigan, Ann Arbor Science Publishers Inc., 1983), pp. 983-991.
- 11. Hostgaard-Jensen, P., et a l.,1977.
Chlorine Decay in Cooling Water and Discharge into Seawater, Journal WPCF, August 1977, pp. 1832-1841.
12.
Jolley, R. L. and Carpec.cer, J. H.
A Review of the Cnemistry and Environmental Fate of Reactive Oxidant Species in Chlorinated Water, in
{
Water Chlorination: Environmental Impact and Health Effects Volume 4, Book 1, R. L. Jolley, W. A. Brungs, J. A. Contruro, R. B. Cumings, J. S. Mattice, V. A. Jacobs, EDS.
(Ann Arbor, Michigan, Ann Arbor Science Publishers Inc., 1983), pp. 3-4 7.
j
. 4962R
i t i
l 13.
Mattice, J. S. et al., Toxicity of Trihalomethanes to Common Carp Embryos in Transactions of the American Fisheries Society 110:261-269, 1981.
14.
Mattice, J.
S., Chlorination of Power Plant Cooling Waters, in Water Chlorination: Chemistry, Environmental Impact and Health Effects, Volume 5 R. L. Jolley, R. J. Bull, W. P. Davis, S. Katz, M. H. Roberts, Jr., and V. A. Jacobs, EDS (Ann Arbor, Michigan, Ann Arbor Science Publishers, Inc., 1983), pp. 39-62.
15.
Perwalk, J. et al. (1980), An Exposure and Risk Assessment for Trihalomethanes: Chloroform, Bromoform, Bromodichloromethane, Dibromochloromethane, EPA-440/4-81-018. Prepared by Arthur D. Little, Inc., Cambridge, Massachusetts for U.S. EPA, Monitoring and Data Support Division.
16.
Scott, G.
I., Physiological Effects of Chlorine-Produced Oxidants, Dechlorinated Effluents, and Trihalomethanes on Marine Invertebrates in Water Chlorination: Environmental Impact and Health Effects, Volume 4, Bcok 2, R. L. Jolley, W. A. Brungs, J. A. Cotruvo, R. B. Cumming, J. S.
Mattice, and V. A. Jacobs, EDS (Ann Arbor, Michigan, Ann Arbor Science Publishers Inc., 1983), pp. 827-841.
17.
Scott, G. I. et al., Bioconcentration of Bromoform by American Oysters (Crassostrea virginica) (G._), Exposed to Chlorinated and Dechlorinated Seawater with Notes on Survival and Feeding in Water Chlorination, Environmental Impact and Health Effects, Volume 4, Book 2, R. L. Jolley, W. A. Brungs, J. A. Cotruvo, R. B. Cumming, J. S. Mattice, and V. A.
Jacobs, EDS (Ann Arbor, Michigan, Ann Arbor Science Publishers Inc.,
1983), pp. 827-841, pp. 1029-1037.
18.
U.S. Environmental Protection Agency, Ambient Aquatic Life Water Quality Criteria for Chlorine, W. A. Brungs, Editor.
Draft September 28, 1983.
- 19. Wong, G. T. F. (1979-1981).
The Fate of Chlorine in Seawater; Progress Report for the Period November 1,1979 - January 31, 1981. Department of Oceanography Old Dominion University, Virginia.
Prepared for the U.S.
Department of Energy, Contract No. DE-AS05-77EV05572.
4 4962R
y_
.A.
TABLE 1 ANNUAL MEANS AND COEFFICIENTS OF VARIATION IRRADIANCE AND WATER QUALITY PARAMETERS AT SEABROOK STATION INTAKE VICINITY 1978 1979 1980 1981 1982 1983 1984 X
X X
X X
X X
PARAMETER (CV)
(CV)
(CV)
(CV)
(CV)
(CV)
(CV)
- ~ ~ ----......------...--...------..............--.....-------......--............-........
Surf ace irradiance 305.71 330.68 326.04 325.43 312.35 308.83 Langleys/ Day (49.99)
(41.22)
(45.04)
(45.24)
(43.93)
(38.71)
Temperature (OC)
Surface 8.37 8.76 8.76 8.72 8.88 9.58 8.94 (66.93)
(57.85)
(57.86)
(63.34)
(53.02)
(53.74)
(55.72)
Bottom 6.61 6.36 7.05-7.37 7.36 7.32 6.93 (55.62)
(47.96)
(52.76)
(59.11)
(46.03)
(44.43)
(45.04)
Salinity (ppt)
Surface 31.68 31.82 32.17 31.89 31.84 31.04 30.63
( 3.33)
( 3.84)
( 2.64)
( 2.16)
( 3.47)
( 4.39)
( 4.93) i Bottom 32.24 32.47 32.42 32.32 32.41 31.92 31.77
( 1.65)
( 2.77)
( 1.52)
( 1.41)
( 2.01)
( 2.12)
( 1.83)
Dissolved Oxygen (ag/1)
Surface 10.28 10.02 10.27 9.90 9.60 9.48 10.01 (10.00)
(13.39)
(11.17)
(12.70)
(11.15)
( 7.73)
(12.06)
Bottom 10.07 9.69 Y.65 9.43 9.25 8.98 9.32
( 8.86)
(14.67)
(14.28)
(17.90)
(16.17)
(11.99)
(13.56) i Nitrite (ug/1) 2.12 1,71 3.17 2.92 2.30 2.05 1.02 (46.11)
(66.58)
(59.59)
(53.13)
(68.34)
(54.34)
(98.08)
Nitrate (pg/1) 52.02 38.33 48.33 45.42 37.17 51.83 36.75 (116.61) (101.24) (111.88)
(94.41) (137.89) (106.62) (117.47) b Amsmonia (ug/1) 51.46 47.42 104.17 36,25
< 30. 00 27.32 16.57 (115.96)
(70.02)
(120.96)
(42.93)
(40.73)
(64.73) a Irradiance data at Seabrook Station site unavailable f or 1978 b Below detection limit (30pg/1) of method used in 1982 v.
i TABLE 2 VOLA 11LE ORGANIC ANALYSIS BY EPA METHOD 624 l
i 9
DATE: 7/9/85 Page j
INITIAL DOSAGE: 2.5 ppm TRD 1 of 2 i
Minimum
)
Compounds reporting limit 30 Sec.
45 Min.
97 Min. 180 Min.
Control Thios-Cont, l Chloromethane 5
ND ND ND ND ND ND Bromonethane 5
ND ND ND ND ND ND Vinyl chloride 5
ND ND ND ND ND ND Chloroethane 5
ND ND ND ND ND ND Methylene chloride 5
ND ND ND ND ND ND Acetone 50 ND ND ND ND ND ND Carbon disulfide 2
ND ND ND ND ND ND 1,1-dichloroethene 2
ND ND ND ND ND ND-1,1 -di c hl or o e t h an e 2
ND ND ND ND ND ND f
Trans-1,2-dichloroethene 2
ND ND ND ND ND ND j
Chloroform 2
ND HD ND ND ND ND 1,2-dichloroethane 2
ND ND ND ND ND ND 2-Butanone 10 ND ND ND ND ND ND 1,1,1-trichloroethane 2
ND ND ND ND ND ND Carbon tetrachloride 2
ND ND ND ND ND ND Vinyl acetate 2
ND ND ND ND ND ND Bromodichloromethane 2
ND ND ND ND ND-Nb 1,2-dichloroprepane 2
ND ND ND ND ND ND Trans-1,3-dichloropc'opene 2
ND ND ND ND ND ND Trichloroethene 2
ND ND ND ND ND ND Dibromer.hloromethane 2
ND ND ND ND ND ND 1,1,2-trichloroehtane 2
ND ND ND ND ND ND Benzene 2
ND ND ND ND ND ND Cis-1,3-dichloropropene 2
ND ND ND ND ND HD 2-Chloroethylvinylether 2
ND ND ND ND ND ND Brosoform 2
ND 120 160 160 ND ND
]
2-Hexanone 10 ND ND ND ND ND ND 4-Methyl-2-pentanone 10 ND ND ND ND ND ND Tetrachloroethene 2
ND ND ND ND ND ND 1,1,2,2-Tetrachloroethane 2
ND ND ND ND ND ND Toluene 2
ND ND ND ND ND ND Chlorobenzene 2
ND ND ND ND ND ND Ethylbenzene 2
ND ND ND ND ND ND Styrene 2
ND ND ND ND ND ND Total xylenes 2
ND ND ND ND ND ND Results in pg/l (ppb)
NDs Not detected i s
y
- 9 t
?
TABLE 2 (cont.)
VOLATILE ORGAN:C ANALYSIS BY EPA METHOD 624
~
DATE: 7/9/85 Pa9e 2 cf 2-INITIAL DOSE 2.5 ppm TRO Mintaus Compounds Reporting Limit 30 Sec.
45 Min.
97 Min. 100 Min.
Contre! Thios-Cont.
Additional compounds NONE DETECTED Dilution factor 10 10 10 10 10 10 Multiply minimum reporting limit by dilution factor to obtain true 1
einimum limit.
s i
l l
i
0-r.
i r*
~3
~]
TABLE 3 1
s.
7/9/95 CHLORINE DEMAND EVALUATION TIME AFTER DEMAND FREE INTAKE CHLORINE WATER WATER DEMAND ADDITION (ppm TRO)
(ppm TRO)
(ppm TRO)
_____________________________=
INSTANTANEOUS 2.38 2.25 O.13 45 f11N.
2.39 1.10 1.28 97 MIN.
2.38 0.98 1.40 182 MIN.
2.38 0.56 1.82 Ambient Seawater Temperature 62 0 F o
l
=- }
G l
TABLE 4 VOLATILE ORGANICS ANk.(LIS BY EPA METHOD 601 DATE :
9/12/05 INITIAL DOSAGE: 3.44 ppm TRO O Nin.
Minimum COMPOUND RESULT Reporting Limit
-~
45V Chloromethane ND 5
46V Bronomethane ND 5
88V Vinyl chloride ND 2
16V Chloroethane ND 5
44V Methylene chloride ND 1
29V 1,1-dichloroethylene ND 1
13V 1,1-dichlercethane ND 1
30V 1,2-trans-dichloroethylene ND 1
23V Chloroform ND 1
10V 1,2-dichloroethane ND 1
11V 1,1,1-trichloroethane ND 1
6V Carbon tetrachloride ND 1
f.GV Bromedichloromethane ND 1
32V 1,2-dichloropropane ND 2
33V Trans-1,3-dichloropropylene ND 2
87V Trichloroethylene ND 1
51V Dibromochloromethane 1.0 1
33V Cis-1,3-dichloropropylene ND 2
14V 1,1,2-trichloroethane ND 2
47V Brosoform 42 5
15V 1,1,2,2-tetrachloroethane ND 2
85V Tetrachloroethylene ND 1
7V Chlorobenzene ND 5
19V 2-chloroethyl vinyl ether ND 10 Multiply minimum reporting limit by dilution factor to catain true minimum limit.
Dilution factor 1.
Results in pg/l (ppb).
ND= Not detected above minimum reporting limit.
- Trace concentrations detected below the minimum reporting limit.
_21
V TABLE 4 (cont.)
~
VOLATILE ORGANICS ANALYLIS BY EPA METHOD 601 DATE :
9/12/85 INITIAL DOSAGE: 3.44 ppm TRO 45 Min.
Minimum COMPOUND RESULT Reporting Limit 45V Chloromethane ND 5
46V Bronomethane ND 5
BBV Vinyl chloride ND 2
16V Chloroethane ND 5
44V Methylene chloride ND 1
29V 1,1-dichloroethylene ND 1
13V 1,1-dichloroethane ND 1
30V 1,2-trans-dichloroethylene ND 1
23V Chloroform ND 1
10V 1,2-dichloroethane ND 1
11V 1,1,1-trichloroethane ND 1
6V Carbon tetrachloride ND 1
46V Brosodichloromethane ND 1
32V 1,2-dichloropropane ND 2
33V Trans-1,3-dichloropropylene ND 2
87V Trichloroethylene ND 1
51V Dibromochloromethane 1.5 1
33V Cis-1,3-dichloropropylene ND 2
14V 1,1,2-trichloroethane ND 2
47V Brosofore 78 5
15V 1,1,2,2-tttrachloroethane ND 2
85V Tetrachloroethylene ND 1
7V Chlorobenzene HD 5
19V 2-chloroethyl vinyl ether ND 10 Multiply minimum reporting limit by dilution factor to obtain true minimum limit.
Dilution factor 1.
Results in pg/l (ppb).
ND= Not detected above minimum reporting limit.
- Trace concentrations detected below the minimum reporting limit.
-22
y TABLE 4 (cont.)
9 VOLATILE ORGANICS ANALYLIS BY EPA METHOD 601 DATE :
9/12/85 INITIAL DOSAGE: 3.44 ppm TRO 97 Min.
Minimum COMPOUND RESULT Reporting Limit 45V Chloromethane ND 5
46V Bronomethane ND 5
88V Vinyl chloride ND 2
16V Chloroethane ND 5
44V Methylene chloride ND 1
29V 1,1-dichloroethylene ND 1
13V 1,1-dichloroethane ND 1
30V 1,2-trans-dichloroethylene ND 1
23V Chloroform ND 1
10V 1,2-dichloroethane ND 1
11V l t l-trichloroethane ND 1
i i 6V Carbon tetrachloride ND 1
48V Brosodichloromethane ND 1
32V 1,2-dichloropropane ND 2
33V Trans-1,3-dichloropropylene ND 2
87V Trichloroethylene ND 1
51V Dibromochloromethane 1.8 1
33V Cis-1,3-dichleropropylene ND 2
14V 1,1,2-trichloroethans ND 2
i 47V Brosoform 100 5
15V 1,1,2,2-tetrachloroethane ND 2
85V Tetrachloroethylene ND 1
7V Chlorobenzene ND 5
19V 2-chloroethyl vinyl ether ND 10 Multiply minimum reporting limit by dilution factor to obtain true air.imum limit.
Dilution factor 1.
Results in pg/l (ppb).
ND= Not detected above minimum reporting limit.
- Trace concentrations detected below the minimum j
reporting limit.
-23
v f.'
TABLE 4 (cont.)
VOLATILE ORGANICS ANALYLIS BY EPA METHOD 601 DATE :
9/12/85
~
INITIAL DOSAGE: 3.44ppe TRO 182 Min.
Minimum COMPOUND RESULT Reporting Limit 43V Chloromethane ND 5
46V Bromomethane ND 5
88V Vinyl chloride ND 2
16V Chloroethane ND 5
44V Methylene chloride ND 1
29V 1,1-dichloroethylene ND 1
13V 1,1-dichloroethane ND 1
30V 1,2-trans-dichloroethylene ND 1
23V Chloroform ND 1
10V 1,2-dichloroethane ND 1
11V 1,1,1-trichloroethane ND 1
6V Carbon tetrachloride ND 1
48V Bromodichloromethane ND 1
32V 1,2-dichloropropane ND 2
33V Trans-1,3-dichloropropylene ND 2
87V Trichloroethylene ND 1
51V Dibromochloromethane 2.5 1
33V Cis-1,3-dichloropropylene ND 2
14V 1,1,2-trichloroethane ND 2
47V Brosoform 130 5
15V 1,1,2,2-tetrachloroethane ND 2
85V Tetrachloroethylene ND 1
7V Chlorobenzene ND 5
l 19V 2-chloroethyl vinyl ether ND 10 Multiply minisum reporting limit by dilution factor to obtain true minimum limit.
Dilution factor 1.
Results in pg/l (ppb).
ND= Not detected above minimum reporting limit.
- Trace concentrations detected below the minimus reporting limit.
i v
.),
TABLE 4 (cont.)
VOLATILE ORGANICS ANALYLIS
~~
i BY EPA METHOD 601
)
l DATE :
9/12/05 INITIAL DOSAGE: 3.44 ppm TRO l
Control-Thiosulfate Minimus j
COMPOUND RESULT Reporting Limit 45V Chloromethane ND 5
46V Bronomethane ND 5
OBV Vinyl chloride ND 2
16V Chloroethane ND 5
44V Methylene chloride ND 1
29V 1,1-dichloroethylene ND 1
13V 1,1-dichloroethane ND 1
30V 1,2-trans-dichloroethylene ND 1
23V Chloroform ND 1
10V 1,2-dichloroethane ND 1
11V 1,1,1-trichloroethane ND 1
)
6V Carbon tetrachloride ND 1
48V Brosodichloromethane ND 1
32V 1,2-dichloropropane ND 2
l 33V Trans 1,3-dichloropropylene ND 2
67V Trichloroethylene ND 1
51V Dibromochloromethane ND 1
33V Cis-1,3-dichloropropylene ND 2
14V 1,1,2-trichloroethane ND 2
47V Bromnform ND 5
15V 1,1,2,2-tetr achl oroethane ND 2
85V Tetracnloroethylene ND 1
7V Chlorobenzene ND 5
19V 2-chloroethyl vinyl ether ND 10 Multiply minimum reporting limit by dilution factor to obtain true minimum limit.
Dilution factor 1.
Results in pg/l (ppb).
NDa Not detected above minimum reporting limit.
- Trace concentrations detected below the minisua reporting limit.
25
TABLE 4 (cont.)
VOLATILE ORGANICS ANALYLIS BY EPA METHOD 601 DATE :
9/12/05 INITIAL DOSAGE: 3.44 ppm TRO Control-no clit orine Minimum COMPOUND RESULT Reporting Limit 45V Chloromethane ND 5
46V Bronomethane ND 5
88V Vinyl chloride ND 2
16V Chloroethane ND 5
44V Methylene chloride ND 1
29V 1,1-dichloroethylene ND 1
13V 1,1-dichloroethane ND 1
30V 1,2-trans-dichloroethylene ND 1
23V Chloroform ND 1
10V 1,2-dichloroethane HD 1
11V l t l-trichloroethane ND 1
i i 6V Carbon tetrachloride ND 1
48V Brosodichloromethane ND 1
32V 1,2-dichloropropane ND 2
33V Trans-1,3-dichloropropylene ND 2
87V Trichloroethylene ND 1
51V Dibromochloromethane ND 1
33V Cis-1,3-dichloropropylene ND 2
14V 1,1,2-trichloroethane ND 2
47V Brosoform ND 5
15V 1,1,2,2-tetrachloroethane ND 2
i 85V Tetrachloroethylene ND 1
7V Chlorobenzene ND 19V 2-chloroethyl vinyl ether ND 10 i
Multiply minimum reporting limit by dilution factor to obtain true minimum limit.
Dilution factor 1.
Results in ug/l (ppb).
ND= Not detected above minimum reporting limit.
- Trace concentrations detected below the minimum reporting limit.
26
+
p 9
I Il TABLE 5 0
VOLATILE ORGANICS ANALYLIS l
BY EPA METHOD 601 f-DATE :
9/18/85 INITIAL DOSABE 1.92 ppa TRO
^
182 Min.
Minimus COMPOUND RESULT Reporting Lin,it 45V Chlaromethane ND 5
46V Bronomethane ND 5
88V Vinyl chloride ND 2
16V Chloroethane ND 5
44V Methylene chloride ND 1
29V 1,1-dichloroethylene ND 1
13V 1,1-dichloroethane ND 1
30V 1,2-trans-dichloroethylene ND 1
j 23V Chloroform ND 1
10V 1,2-dichloroethane ND 1
11V 1,1,1-trichloroethane ND 1
6V Carbon tetrachloride ND 1
46V Bromodichloromethane ND 1
32V 1,2-dichloropropane ND 2
33V Trans-1,3-dichloropropylene ND 2
87V Trichloroethylene ND 1
51V Dibromorbloromethane 3.0 1
33V Cis-1,3-dichloropropylene ND 2
14V 1,1,2-trichloroethans ND 2
47V Brosoform 130 5
15V 1,1,2,2-tetrachloroethane ND 2
95V Tetrachloroethylene ND 1
7V Chlorobenzene ND 5
19V 2-chloroethyl vinyl ether ND 10 Multiply minimum reporting limit by dilution f actor to obtain true minimus limit.
Dilution factori 1.
Results in ug/l (ppb).
ND= Not detected above minimum reporting limit.
- Trace concentrations detected below the minimum reporting limit.
27 l
1
,--g-
--r v
y
- f.-
e' 4
TABLE 6 VOLATILE ORGANIC ANALYSIS BY EPA METHOD 624 DATE: 9/18/85 Page
- INITIAL DOSAGE: 1.92 ppm TRO 1 of 2 Minimum Compounds reporting limit 102 Min.
Chloromethane 5
ND Bromonethane 5
ND Vinyl chlorfde 5
ND Chloroethane 5
ND Methylene chloride 5
ND Acetone 50 ND Carbon disulfide 2
ND l l-dichloroethene 2
ND i
1,1-dichloroethane 2
ND Trans-1,2-dichloroethene 2
ND Chlorofore 2
ND d
1,2-dichloroethane 2
ND 2-Butanone 10 ND 1,1,1-trichloroethane 2
ND Carbon tetrachloride 2
ND Vinyl acetate 2
ND Bromedichloromethane 2
ND 1,2-dichloropropane 2
ND Trans-l 3-dichloropropene 2
ND i
Trichloroethene 2
ND Dibromochloromethane 2
ND 1,1,2-trichloroehtane 2
ND Benrene 2
ND Cis-1,3-dichloropropene 2
ND 2-Chloroethylvinylether 2
ND Brosoform 2
150 2-Heuanone 10 ND 4-Methyl-2 pentanone 10 ND Tetrachloroethene 2
ND 1,1,2,2-Tetrachloroethane 2
ND Toluene 2
ND Chlorobenzene 2
ND Ethylbenzene 2
ND Styrene 2
ND Total xylenes 2
ND Results in ug/l (ppb)
ND= Not detected.
.)
- y 7
- e f
78+
2 a
n TABLE 6'(cont.')
VOLATILE ORGANIC ANALYSIS i
BY EPA METHOD 624 u.
DATE: 9/19/85 Page INIT!AL DOSE: 1.92 ppa TRO 2 of 2 l
Minimus Compounds Reporting Limit 182 Min.
)
1 Additional J
1 compounds l
NONE DETECTED Dilution factor 1
i Multiply minimum reporting limit by dilution factor to obtain true minimum limit.
O h.
29
1
'd
"?
TABLE 7 ORGANIC PRIORITY POLLUTANT ANALYSIS EPA METHOD 625 DATE: 9/10/85 INITIAL DOSAGE: 1.92 ppm TRO TIME: 182 Minutes
~-
ACID COMPOUNDS BASE / NEUTRAL COMPOUNDS 21A 2,4,6-trichlorophenol ND 41B 4-brosophenyl phenyl ether ND 22A p-chlore-a-cresol ND 42B bis (2-chloroisopropyllether ND 24A 2-chlorophenol ND 43B bis (2-chloroethoxy) methane ND 31A 2,4-dichlorophenol ND 52B hexachlorobutadiene ND 34A 2,4-dimethylphenol ND 53B hexachlorocyclopentadiene ND
$7A 2-nitrophenol ND 54B isophorona ND 5BA 4-nitrophano!
ND 55B naphthalene ND
$9A 2,4-dinitrophenol ND 56B nitrobenzene ND 60A 4,6-dinitro-o-cresol ND 61B N-nitrosodimethylamine ND 64A pentachlorophenol ND 62B N-nitrosodiphenylamine ND 65A phenol ND 63B N-nitrosodi-n-propylamine HD 66B bis (2-ethylhexyl)phthalate ND BASE / NEUTRAL COMPOUNDS 67B butyl benzyl phthalate ND 68B di-n-butylphthalate ND 18 acenaphthene ND 69B di-n-octy1phthalate ND SB benridine ND 70B diethyl phthalate ND EB 1,2,4-trichlorobenzene ND 71B dimethyl phthalate ND 9B hexachlorobenzene ND 72B benzo (a) anthracene ND 12B hexachloroethane ND 73B benzo (alpyrene ND 189 bis (2-chloroethyllether ND 74B benzo (b)flueranthene ND 20B 2-chloronaphthalene ND 75B benzo (k)flueranthene ND 259 1,2-dichlorobenzene ND 769 chrysene ND 26B 1,3-dichlorobenzene ND 77b acenaphthylene ND 27B 1,4-dichlorobenzene ND 78B anthracene ND 29B 3,3-dichlorobenzidine ND 799 bento(ghilperylene ND 35B 2,4-dinitrotoluene ND 80B fluorene ND 36B 2,6-dinitrotoluene ND 81B phenanthrone ND 37B 1,2-diphenythydrazine ND 82B dibenzo(ai ) anthracene ND h
399 flouranthene ND 83B ideno(1,2,3-cd) pyrene ND 40B 4-chlorophenyl phenyl ether ND 84B pyrene ND ND = None detected above the average reporting limit of 20 ppb for acids and 20 ppb for 9/N.
30-
,u TABLE 7 (cont.)
ORGANIC PRIORITY POLLUTANT ANALYSIS EPA METHOD 625 DATE: 9/18/85 INITIAL DDSAGE: 1.92 ppa TRO Control & Thiosulfate Control ACID COMPOUNDS BASE / NEUTRAL COMPOUNDS 21A 2,4,6-trichlorophenol ND 41B 4-broacchenyl phenyl ether ND 22A p-chloro-a-cresol ND 42B bis (2-chloroisopropyllether ND 24A 2-chlorophenol ND 43B bis (2-chloroethoxy)eethane HD 11A 2,4-dichlorophenol ND 52B hexachlorobutadiene ND 34A 2,4-dimethylphenol ND 53B hexachlorocyclopentadiene ND 57A 2-nitrophenol ND 549 isophorone ND 59A 4-nitropheno!
ND 55B naphthalene ND
$9A 2,4-dinitropheno!
ND 56B nitrobenzene ND 60A 4,6-dinitro-o-cresol ND 61B N-nitrosodimethylamine ND 64A pentachlorophenol ND 62B N-nitrosodiphenylamine HD 65A phenol ND 63B N-nitrosodi-n-propylamine ND 66B bis (2-ethylhexyl)phthalate ND BASE / NEUTRAL COMPOUNDS 679 butyl benzyl phthalate ND 689 di-n-butylphthalate ND 18 acenaphthene ND 69B di-n-octylphthalate ND 59 benzidine ND 70B diethyl phthalate ND EB 1,2,4-trichlorobenzene ND 71B dimethyl phthalate ND 98 hexachlorobenzene ND 728 benzo (a) anthracene ND 12B hexachloroethane ND 73B banz'o(alpyrene ND 199 bis (2-chloroethyllether ND 74B benzo (b)flueranthene ND 20B 2-chloronaphthalene ND 758 benzo (k)flueranthene ND 25B 1,2-dichlorobenzene ND 76B chrysene ND 268 1,3-dichlorobenzene ND 77b acenaphthylene HD 27B 1,4-dichlorobenzene ND 789 anthracene ND 20B 3 3-dichlorobenzidine ND 798 benzo (ghi) perylene ND
'5B 2,4-dinitrotoluene ND B0B fluorene No 36B 2,6-dinitrotoluene ND 81B phenanthrone ND 37S 1,2-dipheny1hydrazine ND 82B dibenzo(a,5) anthracene ND 39B flouranthene ND 83B ideno(1,2,3-cd) pyrene ND 40B 4-chlorophenyl phenyl ether ND 84B pyrene ND ND = None detected above the average reportit.g limit of 20 ppb for acids and 20 ppb for B/N.
-31 t
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TABLE 8 i
9/18/05 CHLORINE DEMAND EVALUATION e-1 TIME AFTER DEMAND FREE INTAKE CHLORINE WATER WATER DEMAND ADDITION (ppm TRO)
(ppm TRO)
(ppm TRO)
INSTANTANEOUS 1.92 1.08 0.84 45 MIN.
1.EO 0.80 1.08 97 MIN.
1.05 0.63 1.22 182 MIN.
1.82 0.08 1.44 Ambient Seewate. Temper ature 62.6 F
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