Text

Suppl Section IV to Environ Radiation Monitoring Program, Semiannual Rept 9,Jul-Dec 1976
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Site:	Pilgrim
Issue date:	12/31/1976
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[OREWORD

)

Boston Edison's Pilgrim Station's ninth Semi-Annual Environmental Radiation Monitoring Report indicates measured concentrations of radioactivity found in Pilgrim's environment during the second half of 1976.

Environmental radiation measurements included samples from both liquid and gaseous exposure I

pathways to man.

These environmentally observed levels of radioactivity i

are made up of contributions from naturally occurring radioactive sources, i

nuclear fallout from past and current weapons tests, and the addition to i

l the environment from Pilgrim's effluents. The following document addresses the comparison between calculated concentrations arising from station discharges, and measured concentrations at locations subject to Boston i

j Edison's Environmental Radiation Monitoring Report.

l l

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k 1

I V.

Calculated Radionuclides Concentrations In order to assess the relative impact of the addition rif radioactivity to the environment f rom Pilgrim's operation, estimates of environmental i

concentrations of radioactivity due to Pilgrim's effluents have been made s

and compared to the total observed levels found in several important environmental media. The overall comparison of the plant's contribution to environmental radioactivity to that present from natural sources and fallout indicates that in most cases, ottly a nmall or negligible f raction of the total activity in the environment can be associated with Pilgrim's operation. Two exceptions to this were identified. Observed concentrations near the plant of airborne strontium-89 correlated closely with predicted air concentrations due to Pilgrim's ef fluents indicating that the plant i

was the prime source of strontium-89 in the local environment. Also, cobalt 60 detected in algae in the vicinity of Rocky Point was probably related j

to the plant's operation.

In many cases, the levels of concentrations of I

radioactivity predicted to be present due to the plant's ef fluents were j

below the minimum detectable levels of the detection system, and thus, no definitive correlation between observed and expected concentrations can be made.

The models used to calculate the magnitude of plant related radioactivity in environmental media are the same as used in Pilgrim's Appendix 1 evaluation (l)

These calculational methods were taken from the Nuclear Regulatory Commission's Regulatory Guide 1.109(2) with minor exceptions (9)

This guide describes acceptable calculational models for the estimation l

1 of doses to man, and concentrations of radioactivity in environmental media which represent the principle exposure pathways to man.

These models have 2

been supplemented where possible with site specific parameters, such as crop yields and animal grazing habits, in order to make relevant estimates of environmental levels of plant related activity.

S'ite specific meteorology for this six month period, along with reported gaseous and liquid effluents from the plant, were used in the calculations. Meteorological dispersion parameters were calculated for quarterly periods based on the models given in Regulatory Guide 1.111(3), and which were described in detail in Pilgrim's demonstration of compliance with.10CFR50, Appendix I.

However, because of the large number of uncontrollable factors which can affect how plant ef fluents will be transported through the environment, such as feeding regimes of dairy cows, type and density of soil where crops are grown, 1

l migration patterns of fish, and the chemical form of effluents, the predicted concentrations of plant related nuclides in the environment indicate the I

average magnitude of the plant's influence.

l i

i Radionuclides concentrations were estimated for milk, food crops, air and j

l marine organisms such as fish. These media represent the principal pathways of potential exposure to man from plant effluents. Direct radiation, j

sediments, and domestic water were not included in these comparisons of observed concentrations versus predicted plant contributions since they either do not relate directly to plant effluent concentrations, do not represent principal exposure pathways to man, or have not been addressed in the calculational models of Regulatory Guide 1.109.

The following paragraphs describe the comparisons between observed concentrations of radioactivity in environmental media.and the predicted contribution from Pilgrim's operation during the last six months of 1976.

3 l

i l

A.

Air Surveillance Weekly air samples were taken at eleven air monitoring stations and analyzed for gross beta activity and radiciodine. Tabic 6 (of Report #9) indicates the results of the weekly gross beta analyses, and Tables 8 and 8A gives the results of airborne iodine-131 measurements.

For comparison, weekly gross beta measurements at each air monitoring location were averaged over three month periods for both the 3rd and 4th quarters of 1976.

Table IV-1 shows the average of the weekly observed gross beta activity at each location l

l compared with the quarterly average predicted contribution from airborne l

1 particulate released f rom the plant. Table IV-2 compares quarterly average l

iodine-131 predicted f rom plant ef fluents with the observed weekly data

]

for the second half of 1976.

Because most iodine-131 measurements had statistical counting errors greater than the observed concentrations, the l

weekly iodine-131 measurements were not averaged over quarterly time periods J

i since average values would not reflect environmental concentrations.

For use in comparison with observed airborne gross beta particulate activity, Pilgrim's particulate airborne gross beta effluent was estimated from plant l

records by summing all relatively long lived particulate radionuclides emitted during each quarter. Since air particulate filters were allowed l

to decay for several days before counting, only nuclides emitted from the plant which had half lives greater than two days were considered. This allowed for the decay of short lived nuclides which would not be expected to contribute significantly to the gross beta activity detected on the air particulate filters. Moreover, this estimate is possible only because the environmental air particulate filters have identical retention ef ficiencies for all particulate, regardless of radionuclides composition.

1 4

1 l

0

i i

In the case of iodine-131 which has only an 8 day half life, all iodine-131 reported in gaseous releases was assumed to have decayed by a factor of two by the time gross beta activity measurements were made on each air filter. Also, since most of the iodine released in plant effluents is expected to be in gas.eous forms, the air particulate filter sampler used l

for gross beta determinations would not be expected to retain a significant fraction of the iodine passed through them.

Based on limited measurements l

of iodine species in BWR ef fluents, relative f ractions of I-131 which may be in particulate form in plant releases have been used to estimate the l

I contribution of iodine-131 to the total gross beta activity.

Iodine-131 released from main stack which was in particulate form was assumed to be 4% of the total 1-131 released.

For the plant vent, 12% of the total iodine-131 released was assumed to be in particulate form.

Table IV-1 shows that the plant contribution to gross beta activity measured I

in air near the plant represents only a few percent of the total activity.

l The maximum contribution represents about 17% at the Clef t Rock air monitor (0.9 miles south) for the 3rd quarter, and 11% of the total for the Rocky Hill Road East monitoring location (0.8 miles southeast) during the 4th quarter. As expected, most (approximately 83% to 99 + %) of the gross beta activity detected is due to natural occurring sources of radioactivity, or from nuclear weapons fallout.

This fallout contribution was pronounced during the 4th quarter of 1976 when the Chinese were conducting air tests of nuclear weapons. The 4th quarter gross beta activity increased by about p)

)w[, b [ ('O a factor of 5 at all stations over the levels measured during the 3rd r

y quarter. This increase in total beta activity shows no cor_r_e__la_ti.o..n.with

[/ '

6 predicted contributions f rom plant ef fluents, thus supporting the conclusion 5

i

that the increase in activity during the fourth quarter was due to the Chinese testing.

In addition, the expected levels of airborne gross beta activity due to plant operation during the 3rd quarter were essentially at, or below, the detection limit (approximately 4 x 10~3 pCi/m ) of the sampling system.

3 For the fourth quarter, several onsite air monitoring stations have l

calculated plant contributions slightly above the minimum detectable level, l

but still only a small fraction of the total activity observed. The i

relatively low icvels of activity contributed by the plant are essentially indistinguishable from the background activity during this six month period.

Background levels experienced fluctuations far greater than the predicted l

contribution f rom the plant.

The data collected for total f odine-131 in air indicates that, with the exception of a month and a half period following the September Chinese j

nuclear test, the levels of airborne iodine were not statistically significant compared to the total stochastic error associated with each iodine analysis. The only positive analyses of iodine which can be identified occurred during October and early November. All monitoring locations, including the control station, showed elevated levels of iodine far above the predicted contribution from Pilgrim.

These results indicate that the observed iodine levels were directly related to the Chinese test.

The predicted quarterly average plant related air concentrations of iodine-131 were between factors of 3 and 2000 below the detection limit of the counting system, and therefore would not be expected to be observed. The method of sampling for iodine has recently been changed in the radiation 6

l

~

a monitoring program.

TEDA impregnated activated charcoal canisters are now in use for collecting airborne iodine. These samplers will give increased sensitivity for methyl iodine-131 by factors of between 5 and 10.

This will allow for enhanced detection of plant related iodine.

o In addition to the weekly gross beta and lodine measurements, weekly air particulate samples were composited during the months of July and October for gamma isotopic analysis, and composited quarterly for strontium i

o determinations.

Table 7A (Report #9) indicates the results of the monthly composited gamma ray anafysis.

For the July analysis, no plant related fission products were detected above the minimum detectable activity of the counting system.

The October composite did indicate the presence of fission isotopes such as Zirconium / Niobium-95, Barium / Lanthanum-140, and Ruthenium 103 and 106.

However, most of these detected nuclides were below or only slightly above a three sigma error determination and thus not definitely confirmed as being present.

Table IV-3 indicates the average air concentration of plant related gamma ray emitting nuclides expected to be present during the third and fourth quarter.

Comparing these predicted concentrations from plant operation with those environmentally observed levels in Table 7A indicates that the observed fission nuclide concentrations are many times greater than the calculated values. This supports the conclusion that all detected fission nuclides in the October composite were directly related to the Chinese weapons test the month before. No correlation between observed and predicted concentrations of gamma emitting isotopes can be made for the July sample 7

.y since no fission nuclides were observed and all predicted values were far below the detection limits of the counting system.

Table IV-4 compares the observed and predicted air concentrations of strontium 89 and 90.

As can be seen from the Table, predicted concentrations of strontium 89 were either just below the detection limit of the counting system, or represented all, or a significant fraction of, the observed activity.

Since strontium 89 has only a 51 day half life, no significant long term buildup of this isotope would be expected in the environment from past weapons testing, thus making the plant's effluents the principal source of this nuclide found in the local environment.

However, immediately following open air testing of atomic weapons, it could be expected that increased airborne levels of strontium 89 would be observed.

In fact this phenomenon was also observed at one other New England location (10)

For the fourth quarter's air particulate samples, increased levels were observed over the third quarter's concentrations. However, calculated concentrations at several air monitoring stations were also predicted to be higher during

'}

the fourth quarter. These higher predicted levels corresponded with observed levels. Only in the air samples taken at the Property Line monitor and j

Plymouth Center monitor were there significant differences between observed I

and predicted concentrations. This suggests that plant effluents do l

correlate closely with observed strontium 89 levels, but that fallout from 1

recent weapons tests also contributed to the total activity levels identified.

Quarterly composite air samples also indicate detectable levels of strontium-90 at several monitoring locations. Predicted plant related contributions to the total concentrations observed run between 0.1% and 9% for those 1

8 E_---___----_-

i monitoring locations near the plant site.

Because of large counting errors, a high degree of confidence in the measured strontirm-90 levels is not possible. Therefore, the actual correlation between observed and predicted I

concentration may be different from what is apparent. However, since strontium 90 has a relatively long half life (28.9 years), concentrations of strontium 90 deposited in the environment from the weapons testing of the nineteen-fif ties and sixties would be expected to contribute significantly to the total measured levels. This effect can be seen in Figure 6 (Report #9) which illustrates how strontium-90 levels in milk samples taken before and after Pilgrim's startup have remained fairly constant.

B.

Milk Monthly milk samples were collected from several locations and analyzed for radionuclides content (Table 10 of Report #9).

For comparison purposes, i

monthly measured values were averaged for the 3rd and 4th quarters and compared with the quarterly contribution predicted for plant ef fluents.

l Table IV-5 indicates the results of the comparison of observed and predicted radionuclides concentration in milk.

Farm practicas in the vicinity of the site indicate that during the growing i

season (3rd quarter), dairy cows receive about 40% of their daily food intake from pasture grass.

Supplemental grain feeding from supplies grown outside a 50 mile radius of the site make up the remaining 60% of the cows diets.

For the 4th quarter, milk cows receive about 60% of their daily diet from l

locally grown stored feed and silage, with about 40% of the daily intake from grain supplements. These feeding practices were used, along with 9

4 1

i

l

)

quarterly average meteorology for both three month periods, in calculating the concentration of plant related radionuclides.in milk.

Regulatory Guide 1.109 assumptions for the transfer f ractions of dif ferent nuclide species through the grass-cow-milk pathway were utilized.

For both the 3rd and 4th quarters of 1976, the estimated concentration in milk of plant related isotopes represents less than 0.04% of the total measured concentration of the principal nuclides identified.

Therefore, the plant's contribution to radionuclides found in milk samples is an insignificant f raction of the totals observed. This suggests that levels of Cesium-137, Strontium-90, Iodine-131 and Barium-140 found in milk were due to nuclear weapons tests. This conclusion is supported by the fact that the isotopic concentrations observed in milk were essentially the same at the control station and at the indicator location.

(

It should also be noted that the maximum predicted radionuclides concentrations in milk due to plant effluents were factors of about 10, e

1000, 7000, and 300,000 below the detection sensitivity of the counting system for iodine-131, cesium-137, strontium-90 and barium-140, respectively.

These low predicted levels of plant related nuclides cannot be observed because of the detection sensitivity of the counting system and the relatively large concentrations of these nuclides present from fallout.

C.

Food Crops Food crop samples of corn, cranberries, lettuce, potatoes and hay were collected during the 3rd and 4th quarters and analyzed for concentrations of radioactivity.

Table IV-6 lists the measured levels of radionuclides detected in crops.

For each crop sample taken, Table IV-6 also indicates 10 e

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e the predicted plant contribution to the total radionuclides concentrations.

As indicated, no crop sample showed a detectable level of manganese-54, cobalt 58 and 60, or zinc 65.

The predicted contribution of these nuclides i

from Pilgrim's effluents are all at least four orders of magnitude below l

I the minimum detectable activity levels of the detection system, and thus would not be expected to be observed.

Iodine-131 was deweted in one crop sample during the reporting period at about 900 pC1/kg. The corresponding predicted plant contribution was estimated to be about 0.07% of the total observed level. All other estimated iodine-131' concentrations in food crops were between one and four orders of magnitude below the detection limit for iodine. The detected iodine in this one crop sample is ther:o. fore also related directly to the September I

Chit.ese weapons test.

Cesium-137 was positively detected in all cranberry samples. The observed concentrations exceeded the predicted plant related levels by four orders of magnitude. The relatively high levels of cesium-137 seen in cranberries are greater than what would be expected from air deposition and normal uptake through the soil. Cranberries seem to concentrate cesium to a greater extent than what would be expected f rom the crop uptake models of Regulatory Guide 1.109.

One possible explanation for this could be that because cranberries are grown in jowland areas which are periodically flooded, cesium deposited s

by air deposition over large land! areas could be washed down into these lowland bogs, sedimentated out into the soil, and therefore made available for uptake through the root system of the cranberry.

A second mechanism which could account for elevated cesium levela might 11

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1 1

be that the sandy soil in which cranberries are grown is deficient in l

potassium, or some other chemical normally assimilated by terrestrial plants, and that in its place, cranberries extract a higher than expected fraction of cesium from the soil.

Cesium is a congener of potassium.

The uptake i

of cesium from soil has been shown to be inversely proportional to the potassium content of soil.- in which there is a potassium deficiency.(4)(5) l Broseus(6)has also observed that cesium 137 introduced by fallout is more readily available through root uptake from soil when conditions of high moisture and deficient soil potassium exist.

f In total, both these possibilities may be contributing to the relatively high uptake of cesium in cranberries. The actual mechanism which accounts for the observed levels of cesium cannot be determined with the available

data, Analyses of soil samples from both cranberry bogs and other farm crop locations would be required in order to determine the importance of 1

efiber of these two reconcentration mechanisms. The results of such analyses could then be used to adjust the concentration fraction for uptake of cesium from soil by cranberries, and/or adjust the predicted soil concentration of plant related or weapons fallout cesium.

Present environmental monitoring tec'suical specifications require the periodic analysis of soil by in site gamma sp9etroscopy. This analysis method can be used to evaluate the amounts of cesium potassium, and other gamma ray emitting radionuclides present in cranberry bogs and thus provido the data nceded to determine soil uptake fractiona, ln' addition, a review of the observed levels of cesium-137 f cranberries suggest that Pilgrim's effluents may be contributing to tb e

ected concentrations by a larger fraction than predicted by t.he,

at model.

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The lowest measured concentration of cesium was observed at the control location (Pine Street Bog).

As the calculated plant effluent air deposition rates increase for those bogs closer to the plant, the observed cesium concentration in cranberries also increases. The difference in concentration of cesium between the control location and the three closest cranberry bogs is a factor of about 8.

However, this observation may also be due to differences in irrigation practices, soil conditions, or weapons fallout history between the different cranberry bogs.

in order to determine whether the plant ef fluents contributed to the cesium levels observed in cranberries, we plan a program of environmental measurements. This program will include field spectroscopic measurements of K-40 and Cs-137 in bogs at various locations both near to and far from the station. Measurements will also be made at seve::a1 wetland locations where drainage and meteorological dispersion characteristics will be taken into account to determine any significant accumulations of cesium in soil.

The determination of tne relative concentration of potassium and casium at these locations, together with appropriate geographic and dispersion data,will permit an evaluation of the plant's contribution to the observed cer' un levels.

Strontium 90 was also detected in most crop samples. Again, the plants predicted contribution to the observed strontium-90 concentrations were only small fraction (0.04% or less) of the total. Unlike cesium-137, strontium-90 was identified in all types of food crops with the highest i

levels being detected in hay samples. The fact that strontium was detected in all crop samples, and cesium was not except for cranberries, is in good 1

agreement with reported root uptake concentration factor.(7) Under average 13

1 l

conditions, strontium uptake is 10 times greater than cesium uptake per unit of soil activity concentration. The degree to which radionuclides will be taken up through the root systems of plants depends on the chemical form of the nuclide, the metabolic requirements of the plant, and the i

physicochemical characteristics of the soil. The detected levels of strontium-i 90 are most likely due to nuclear weapon's fallout and subsequent buildup of fallout activity in soil. Quarterly composite air samples at the control station indicate detectable levels of strontium-90.

These airborne concentrations of strontium-90 are principally the result of activity deposited by weapons tests being washed out from the atmosphere and/or the resuspension of strontium into the air from soil deposits.

I i

l Several other fission related nuclides were detected in one cranberry sample 1

taken on October 12.

Table IV-6 indicates both the observed concentrations and corresponding predicted plant contribution. The fission nuclides j

detected in this sample are the direct result of the Chinese weapon test I

of September 26, two weeks prior to sampling.

D.

Marine Biological Samples Marine environmental media were grab sampled according to the schedule in Table 1A (Report #9). Locations are shown in Figure 3A.

As indicated in Tabic 5, analyses of gross beta, gross gamma, gamma spectroscopic and Sr-90 activity concentrations were performed on each sample.

Gross beta and gross gamma results have not been compared to predicted values for biologieci media.

Since overall radionuclides toxicity is not directly related to gross activity but rather to the sum of concentrations for individual radionuclides, the purpose of such comparisons is moot.

14

l Accordingly, gross beta and gross gamma analyses have been removed from the marine biological radiological surveillance requirements of Pilgrim Nuclear Power Station. Hence, comparisons of calculated and observed activities are restricted to individual radionuclides measured by gamma spectroscopy or Sr-90 radiochemical analysis.

i Detection of Pilgrim related Sr-90 is hampered by the overwhelming presence of Sr-90 originating from weapons testing programs.I7) In the third and fourth quarters of 1976, the maximum detected Sr-90 activities were 45 pC1/Kg in fish, 130 pCi/Kg in invertebrates, and 24 pC1/Kg in alage (Table 15).

1 The sensitivity of these analyses is 5 pC1/Kg and measurements abcve 5 pCi/Kg were common. During this same period, the maximum predicted activities j

near the discharge canal in marine biological media were 0.0027 pC1/Kg in fish, 0.027 pCi/Kg in invertebrates and 0.013 pC1/Kg in plants. Hence, Pilgrim's contribution to ambient radiostrontium concentrations is not sufficient to account for the frequent detection of Sr-90 levels greater than 5 pC1/Kg, especially at locations distant from the plant.

Information derived from environmental surveys at another New England seacoast site supports this conclusion.0)

The comparison of observed and expected concentrations of gamma-emitting radionucl' des is presented in Tables IV-7 through IV-ll.

Table IV-12 lists the parameters employed in converting the quarterly ef fluent releases into quarterly averaged water concentrations. Water concentrations were converted into calculated biological sample concentrations using transfer ratios from NRC Regulatory Guide 1.109, with minor exceptions.59)

At Rocky Point, these comparisons (Table IV-7) indicate that Mn-54, co-60 15

and Cs-137 may appear in greater concentrations than are expected. The reason for this discrepancy may be that the particular algae sampled here

_(Citondrus c rispus) have a greater bio-accumulation factor than the values employed in this analysis (Hn-54/5500, Co-60/1000, Cs-137/50).

Although other reports have recommended higher values (Mn-54/10,000, CS-137/500),

these differences do not account for the difference between observed and calculated concentrations. Of course, it is possible that no published values are appropriate for the particular marine algae at Rocky Point.

However, it is not possible to conclude that the present bio-accumulation factors are too low because (1) these samples may have been taken when ambient water concentrations were higher than the quarterly average concentrations and (2) the dilution ratio assumed for Rocky Point (0.2) may not be appropriate for the exact location of algae sampling.

Since high sensitivity gamma spectroscopy will be performed in mussel samples j

in 1977, more data will be available shortly to discriminate further among the several potential causes of this inconsistency. Note that predicted concentrations of Co-60 and Zn-65 in mussels are approximately equal to

{

the sensitivities used in 1976 analyses.

At Manomet Point (Table IV-8), all radionuclides are predicted to be below analytical sensitivities and there are no positive indications of plant related radioactivity in these sample results.

Note that the radionuclides composition of 4th quarter algae samples is characteristic of the heavy

]

weapons testing fallout prevalent at that time.

16

'l i

Samples from Plymouth and Duxbury are combined for comparison purposes (Table IV-9) since the calculated radionuclides concentration..s are identical. No plant related radionuclides were observed in statistically significant I

quantities.

I i

At Green Harbor and Ellisv111e (Tables IV-10 and IV-ll), gamma spectrum analyses produced negative results except for fallout related radionuclides in alage.

The disagreement between predicted and observed values lends credence to this conclusion.

i in general, the calculated values of environmental radionuclides concentrations do not conflict with results reported by the marine biological radiological surveillance program. Of course, the force of these comparisons is somewhat weakened because the calculated concentrations are usually beyond l

the detection sensitivity of the measurements. A program of high sensitivity mussel sample analyses has been undertaken and may help to explain the disparity between some calculated and observed values at Rocky Point.

l Although Fe-55 was calculated to be present in detectable quantities, no 1

analyses are conducted for this radionuclides in environmental media.

Since Fe-55 decays by electron capture, only the de-excitation X-rays of Mn-55 are emitted. These X-rays are not observable in Ge(L1) spectra and therefore l

a separate radiochemical procedure would be required to isolate Fe-55 for 1

l observation with a low background X-ray detector. These additional steps are not warranted in the case of Fe-55 because the present monitoring program is sufficient to detect very small dosimetric impacts on human beings in

~

the local environs.

1 i

17

.J

For example, if adults were to obtain 1% of their total dietary intake from mussels harvested along the plant shoreline, the present surveillance program would detect an increase of 5 pC1/Kg of Cs-137 in these molluscs and this corresponds to a yearly whole body commitment of 0.0055 mrem / year. Although Fe-55 concentrations are expected to be up to 3000 times greater than Cs-I 137 concentrations in these organisms, the dose commitment from Fe-55 is 160 times less than Cs-137 per unit activity ingested. Hence, the increased dose from Fe-55 is only 0.1 mrem / year to the whole body in this case. Thus, normal monitoring for Cs-137 in environmental media is suf ficiently sensitive to detect a radiological impact at dose levels far below doses of public health interest. Finally, therefore Fe-55 analyses are not mandated unless l

Cs-137 concentrations should increase to the point where an enhanced surveillance ef fort would be recommended.

For example, concentrations which exceeded the guidelines of 10CFR50 Appendix I would require expanding the i

surveillance program.

I E.

Other Marine Samples Radioactivity in sediments has not been calculated from effluent data because sed 1ments are not per sji a dose pathway to humans. Moreover, parametric data do not exist which would allow calculation of radionuclides concentrations in sediments corresponding to the 6 to 9 inch deep sediment cores which were sampled in 1976.

Among seawater analyses, only H-3 and 1-131 were specifically analyzed.

The maximum average H-3 concentration calculated for the discharge canal i

is 0.0016 pC1/ml, while the sensitivity is approximately 50 pCi/ml. Note that concentrations of H-3 in the discharge canal do not exceed those at 18

l l

Powder Point, the control station.

1-131 concentrations are expected to be at least four orders of magnitude smaller and therefore generally beyond detection.

The maximum average calculated Cs-137 concentration in the discharge canal is 0.00017 pCi/ml, which is considerably lower than the 0.27 and 0.25 pC1/ml measured in the intake and discharge, respectively, during the same period.

No other radionuclides were identified in seawater samples.

l 19

1 i

TABLE IV-1 I

Cross Beta Activity in Air Particulate Observed Concentrations vs.. Pgant Predicted Contributions (a)

(pci/m )

3rd Quarter (b) 4g

,7(c)

Air Particulate 1(

11 (e)

I 11(8)

W SamplinR Station Observed Predicted 11:1 Observed Predicted II:1 l

East Weymouth 3.1x10-2 2.4x10~5 7.7x10~4 1.6x10-1 2.0x10~5 1.2x10~4

~

(Background) l Plymouth Center 3.1x10~2 2.2x10~4 7.1x10-3 1.6x10"I 1.4x10~4 8.8x104 (Offaite)

Cleft Rock Area 2.7x10-2 4.5x10-3 0.17 1.4x10~1 3.5x10-3 0.02 (Offsite)

Hanomet Substation 3.0x10-2 5.9x10 '

~

O 02 1.4x10~1 9.7x10~3 0.07 (Offsite)

Rocky liill Rd.(West) 2.9x10~2 1.2x10~3 0.04 1.6x10~1 8.0x10~4 5.0x10-3 (Onsite) i Property Line 3.0x10-2 3,7,1g 4 0.02

-1.4x10"1 9.1x10 6.5x10~3-4 (Onsite)

Overlook Area 2.8x10-2 4.0x10~4 0.01 1.6x10"I 3.2x10~3

.0.02 (Onsite)

Pedestrian Bridge 3 3x10-2 1.7x10-3 0.05 1.5x10~1 1.5x10-2 0.10 (Onsite)

East Ereakwater 3.1x10-2 1.5x10-3 0.05 3.5x10"I(f) 1.3x10-2 0.04' (Onsite)

Rocky lil11 Rd.(East) 3.2x10-2 4.3x10 0.01 1.4x10~1 1.5x10-2 0.11 4

(Onsite)

Warehouse 3.3x10~2 8.2x10-4 0.02 1.7x10"I 6.3x10~3 0.04' l

(Onsite)

(a) observed gross beta concentrations in air are average quarterly values for each air particulate monitoring station (see Table 6).

The gross beta concentration in air predicted from plant ef fluent data and site specific meteorology are included for compa rison.

(b) 3rd quarter extends from July 1 to September 30. 1976.

(c) 4th quarter extends from September 30 to December 30, 1976.

(d) column 1 indicates everage quarterly gross beta concentrations observed at each air 3

sampling station (pC1/m )

(e) column 11 indicates predicted gross beta concentration of air particulate due to plant effluents 20 i

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TABLE IV-7 J

l MARINE RADIONUCLIDES CONCENTRATIONS (pCi/kg) j l

Rocky Point j

(1)

Mn-54 Co-60 Zn-65 Zr/Nb-95 Cs-137 Algae exp.

8.8 48 1.5 0.7 1.7 obs.

130+50 640+70 20+40

<40 100+40 l

Mussels exp.

0.6 48 74 0.1 0.8 obs.

<30

<70

<60

<30 Lobster exp.

0.6 48 74 0.1 0.8 obs.

<40

<100

<60 60+30 Fish exp.

0.1 0.7 0.4

5. 5 0.2 l

obs.

0+20 0+20

<60

<40 30+20 Fourth Quarter (

Algae exp.

24 16 0.4 0.2 0.7 obs.

130+80 380+100

<80

<40 130+80 Mussels exp.

1.7 16 21 0.04 0.3 obs.

None None None None None Lobster exp.

1.7 16 21 0.04 0.3 obs.

<30

<100

<60

<30 Fish exp.

0.4 0.2 0.1 1.7 0.08 obs.

0+20 0+20

<50 40+40 10+20 Footnotes:

(1)

Fe-55 expected at 86 pCi/kg (Algae), 2400 pCi/kg' (Mussels and lobsters) and 53 pCi/kg (Fish).

(2)

Fe-55 expected at 72 pCi/kg (Algae), 200 pCi/kg (Mussels and lobsters), 30 pCi/kg (Fish) and Fe-59 expected at 4.6 pCi/kg (Mussels and Lobsters).

(3) One pollock observed with 10+40 pCi/kg of Ru-103; expected value is <0.00001.

28

l 1

TABLE IV-8 MARINE RADIONUCLIDES CONCENTRATIONS (pCi/kg)

Manomet Point Mn-54 Co-60 Zn-65 Zr/Nb-95 Cs-137 Third Quarter Algae (1) exp.

0.9 4.8 0.1 0.07 0.2 l

obs,

<90

<100

<300

<200

<90 Mussels exp.

0.06 4.8 7.3 0.01 0.09 obs.

<30

<60

<30 l

Lobster exp.

0.06 4.8 7.3 0.01 0.09 I

obs.

None None None None None Fish exp.

0.09 0.5 0.3 4.0 0.1 i

obs.

None None None None None l

Fourth Quarter Algae (2) exp.

2.3 1.6 0.04 0.02 0.07 obs.

<80 170+90

<200 2300+300

<80 Mussels exp.

0.2 1.6 2.1 0.004 0.03.

obs.

None None None None None Lobster exp.

0.2 1.6 2.1 0.004 0.03 obs.

None None None None Mone Fish exp.

0.2 0.2 0.09 1.2 0.05 obs.

None None None None None i

Footnotes:

(1)

Fe-55 expected at 8.7 pCi/Kg (Algae), 230 pCi/Kg (Mussels 6 Lobster) and 35 pCi/Kg (Fish).

(2)

Also observed:

Ru-103, 1050+200 pCi/kg; Cc-141, 4900+500 pCi/kg; Ce-144,<1000+600 pCi/kg; and La-140, 170+90 pCi/kg. _ Respective predictions are:

Ru-103, <0.00001; Cc-141, 0.02; Ce-144, 0.08; and La-140, 0.8 29

TABLE IV-9 MARINE RADIONUCLIDES CONCENTRATIONS (pCi/kg)

Plymouth 6 Duxbury Mn-65 Co-60 Zn-65 Cs-137 Third Quarter (

Algae exp.

1.3 7.2 0.2 0.2 obs.

None None None None l

Mussels exp.

0.1 7.2 11 0.1 obs.

<30

<70

<30 Quahogs exp.

0.1 7.2 11 0.1 obs.

<20

<50

<30 Clams exp.

0.1 7.2 11 0.1 j

obs.

<30

<40

<60 40+20 Fish exp.

0.1 0.7 0.4 0.2 obs.

None None None None Fourth Quarter Algae exp.

3.5 2.4 0.06 0.1 obs.

None None None None Quahogs exp.

0.2 2.4 3.2 0.05 obs.

<20

<30

<20 f)

Clams e xp.

0.2 2.4 3.2 0.05 obs.

<10

<30

<20 Fish exp.

0.4 0.2 0.1 0.08 obs.

None None None None i

l Footnotes:

(1)

Fe-55 expected at 13 pCi/kg (Algae), 350 pCi/kg (invertebrates) and 53 pCi/kg (fish).

(2) Ce-141 observed at 100+50 pCi/kg, 0.02 pCi/kg expected.

30

TABLE IV-10 MARINE RADIONUCLIDES CONCENTRATIONS (pCi/kg)

Green Harbor Mn-54 Co-60 Zn-65 Cs-137 Third Quarter Algae exp.

0.02 0.1 0.003 0.003 obs.

None None None None II)exp.

Mussels 0.001 0.1 0.1 0.002 obs.

<40

<90

<40 Clams ( )

exp.

0.001 0.1 0.1 0.002 obs.

<30

<70

<30

'l Fish exp.

0.002 0.01 0.005 0.003 obs.

None None None None l

Pourth Quarter j

Algae exp.

0.04 0.03 0.0007 0.001

)

obs.

None None None None Mussels exp.

0.003 0.03 0.04 0.0007 obs.

<20

<30

<50

<30 Clams exp.

0.003 0.03 0.04 0.0007 obs.

<20

<50

<20 Fish exp.

0.004 0.003 0.002 0.001 obs.

None None None None l

l Footnotes:

(1)

Fe-55 expected at 4.6 pCi/kg 31 j

TABLE IV-11

. MARINE RADIONUCLIDES CONCENTRATION (pCi/kg)

E11isville hb-54 Co-60 Zn-65 Cs-137 I

Third Quarter Algae (1) exp.

0.04 1.9 0.06_

0.07 obs.

<90

<200

<60 Inverte$ exp.

0.02 1.9 2.9 0.03 brates obs.

None None None None Fish exp.

0.04 0.2 0.1 0.05 obs.

None None None None Fourth Quarter I) l Algac exp.

0.9 0.6 0.02 0.03 I

obs.

110+70

< 60

< 100

< 60 Inverte-exp.

0.07 0.6 0.8 0.01 l

brates obs.

None None None None Fish exp.

0.09 0.06 0.03 0.02 obs.

None None None None Footnotes:

(1)

Fe-55 expected at 14 pCi/kg.

(2)

Fe-55 expected at 9.4 pCi/kg (3)

Zr/Nb-95 observed at 3400+300 pCi/kg; Ru-103 at 1100+130 pCi/kg; Ce-141 at 5700+600 pCi/kg; Ce-144 at 800+600 pCi/kg., Expected values were:

Zr/Nb-95, 0.008; Ru-103, <0.00001; 'Ce-141, 0.005; and Cc-144, 0.02, 32

d TABLE IV-12 5

MARINE RADIONUCLIDES CONCENTRATION PARAMETERS ( }

LOCATION MIXING RATIO TRANSIT TIME (days)

Rocky Point 0.2 (Algae 6 Mussels) 0 0.03 (Fish) 5 Manomet Point 0.02 5

Plymouth 6 Duxbury 0.03 5

E111sville 0.008 10 Green Harbor 0.0004 50 s

Average Discharge Flow:

3.00 E05 gallons / minute (1)

Derived from reference (1), pp. A-48 6 A-49.

l l

l t

33

l l

REFERENCES 1.

Pilgrim Station, Unit 1, Appendix I, Evaluation Submitted in Accordance With 10 CFR50, Appendix I, Boston Edison Company, Boston, MA April 1977.

2.

Regulatory Guide 1.109, " Calculation of Annual Doses to Man From Routine Re-leases of Reactor Effluents for the Purpose of Evaluating Complinace with 10 CFR Part 50, Appendix I;"

U.S. Nuclear Regulatory Commission, March 1976.

3.

Regulatory Guide 1,111, " Methods for Estimating Atmospheric Transport and Dispersion of Gaseous Effluents in Routine Releases From Light-Water-Cooled Reactors," U.S. Nuclear Regulatory Commission, March 1976.

4.

Nishita, H.,

Romney, E.M., and Larson, K.H.

(1961).

Uptake of Radioactive l

Fission Products by Crop Plants.

J. Agr. Food Chem. 9, 101.

l S.

Menzel, R.G. (1965). Soil-Plant Relationships of Radioactive Elements. Health Physics.

11, 1325.

6.

Broseus, R.W.

(1970).

Cesium-137/ Strontium-90 Ratios in Milk and Grass From Jamaica.

M.S.

Thesis, New York University.

l 7.

Eisenbud, Merril. (1973).

Environmental Radioactivity, second edition, l

Academic Press, NY.

i 8.

Maine Yankee Atomic Power Co., 1977, Environmental Surveillance Report No. 9, Vol. 2, p. 48.

)

1 9.

Desrosiers, A. E.,1977, " Bioaccumulation Factor for. Tellurium in Marine Inverte-brates," paper read at the Health Physics Society Meeting, Atlanta, Georgia.

10.

Yankee Atomic Electric Co., 1977, Annual Radiological Environmental Surveil-lance Report, p. 4.

l l

34

ML20238A380

Text

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