NCD980602163_19851001_Warren County PCB Landfill_SERB C_Envion. Sci. Technol. article Polychlorinated Biphenyl Emissions to the Atmosphere in the Great Lakes Regions - Municipal Landfills and Incinerators-OCR

• I
I,,....======---------------------
i, Environ, Sci. Technol, 1985, 19, 942-946
(19) Schniepp, L, E.; Geller, H. H, J , Am. Chem, Soc, 1946, 68,
1646-1648,
(20) Blust, G,; Lohaus, G. Justus Liebigs Ann, Chem, 1953, 583,
2-6,
(21) Hartung, W. H.; Crossley, F, "Organic Syntheses", Collect.
VoL II; Wiley: New York, 1943; pp 363-364,
(22) Renaud, R.; Leitch, L, C. Can, J, Chem. 1954, 32, 545-549,
(23) Martinez, R. L; Herron, J, T.; Huie, R, E. J, Am, Chem,
Soc, 1981, 103, 3807-3820, and references cited therein,
(24) Herron, J, T,; Martinez, R. L; Huie, R. E. Int. J . Chem ,
Kinet. 1982, 14, 201-224.
(25) Bailey, P. S. "Ozonation in Organic Chemistry"; Academic
Press: New York, 1978 (VoL 1), 1982 (Vol, 2),
(26) Herron, J. T.; Huie, R. E. J , Am. Chem, Soc, 1977, 99,
5430--5435,
(27) Herron, J. T,; Huie, R. E.; Int. J, Chem. Kinet. 1978, 10,
1019-1041,
(28)
(29)
(30)
(31)
(32)
The assignment of HC18O18OH in IR spectrum was
on the data in the following: Hatakeyama, S,; Bandowf
Okuda, M.; Akimoto, H. J. Phys, Chem. 1981, :·
2249-2254,
Santilli, D. S,; Dervan, P. B. J, Am. Chem. Soc, 1979,_
3663-3664, :\
Story, P. R.; Morrison, W. H., III; Hall, T. K.; Farine, J.'_
Bishop, C. E. T etrahedron Lett. 1968, 3291-3294. -f.
Story, P. R.; Hall, T. K.; Morrison, W. H., III; Farin
C. Tetrahedron Lett. 1968, 5397-5400.
Srinivasan, R. In "Advances in Photochemistry"; N"
W. A., Jr., Ed.; Interscience Publishers: New York, 1
pp 83-113, and references cited therein.
Received for review June 20, 1984. Revised manuscript rece
January 30, 1985. Accepted April 22, 1985.
Polychlorinated Biphenyl Emissions to the Atmosphere in the Great Lakes :
Region. Municipal Landfills and Incinerators
Thomas J. Murphy,* Leo J. Formanskl, Bruce Brownawell, and Joseph A. Meyer
Chemistry Department, DePaul University, Chicago, Illinois 60614
■ In an effort to identify sources of polychlorinated bi-
phenyls (PCBs) to the atmosphere, the concentration of
PCBs in emissions from several municipal sanitary landfills
and refuse and sewage sludge incinerators in the Midwest
was determined. Sanitary landfills continuously emit the
gaseous products of anaerobic fermentation along with
other volatile materials to the atmosphere. Thus, they can
be continuing sources of vapor-phase contaminants to the
atmosphere. A projection, based on the amount of
methane generated annually from landfills and a PCB to
methane ratio of 0.3 µ,g of PCBs/m3 of CH4 found from
the landfills sampled, indicates that the annual PCB
emissions from sanitary landfills in the U.S. is on the order
of 10-100 kg/year. The concentrations of PCBs from the
incinerator stacks sampled ranged from 0.3 to 3 µ,g/m3, and
the annual emissions per stack sampled were 0.25 kg/year.
The emission rates found here are small compared to the
900000 kg/year of PCBs estimated to cycle through the
atmosphere over the U.S. annually.
Introduction
The presence of measurable concentrations of poly-
chlorinated biphenyls (PCBs) in the atmosphere
throughout the northern and southern hemispheres is now
well established (1-5). The fact that the PCBs in the
atmosphere can exert significant deleterious effects has
been demonstrated in the Great Lakes region where it has
been shown that the atmosphere is presently a major
source of PCB inputs to Lakes Michigan, Superior, and
Huron (5-10). Bioaccumulation by the biota in Lake
Michigan has led to levels of PCBs in adult sports fish (11)
above the FDA limit for interstate commerce of 2 ppm
(mg/kg) (12). Levels in adult fish of all species in all of
the Great Lakes are above the International Joint Com-
mission criteria of 0.1 mg/kg, and adverse health effects
due to their presence have been demonstrated (13).
The amount of PCBs transported by the atmosphere is
quite large. Concentrations of about 7 ng/m3 of PCBs have
been reported in cities and towns of the Midwest (6,
14-16), and concentrations of 0.5-2 ng/m3 have been re-
ported in rural and remote areas (1-5, 17). On the basis
an estimate of 0.05 ng/m3 in rural areas, 5 ng/m3 urban
areas, and a mixed height in the atmosphere of 2
was calculated that the air over the U.S. at any '•
contains about 18 000 kg of PCBs (18). This estima" r
conservative due to the low concentration assumed'.fo
rural areas. If an average residence time in the atmosph~
is assumed to be 1 week, about 900000 kg/year of PG
annually cycle through the atmosphere over the U.S.
works out to an average input to, or deposition from, tlie
atmosphere of about 60 g/ (km2•year). This deposition ra
is in reasonable agreement with that found to be co ·.
into Lake Michigan from the atmosphere (7). ·
Unfortunately, there is little information available o
the sources to the atmosphere of this 900 000 kg/year)>
PCBs. Probable sources include the following: tij
evaporation of PCBs used in the past for such open us ·.
as paints, wood preservatives, plasticizers, etc.; the eva
oration of spilled or leaked PCBs from transformers, larg'
capacitors, hydraulic systems, and equipment contain". ·
large volumes of PCBs and still in service or in storag~·
the evaporation from landfills or incinerators of PCBs fro' ·
materials disposed of in municipal refuse; the evaporatioil
of PCBs improperly disposed of to open areas such as th~
use of waste PCB fluids to oil roads etc; emissions of PCBs·
from engines and furnaces burning liquid or gaseous fuels
containing or contaminated with PCBs; the reevaporation,
of PCBs from land areas where they have been deposited
by wet and dry deposition from the atmosphere.
In the past, PCBs were included in the manufacture q{
a variety of materials that could end up in municipal wastel
Some of these materials are still permitted to be dispos
of in municipal waste. This includes carbonless carbo
paper and most of the billions of small, PCB-containing
capacitors that have been manufactured. Large numbe"
of these capacitors have been used in the ballasts oh
fluorescent light fixtures, in consumer electronics, and ,
the starting capacitor on motors in refrigerators, washin·
machines, air conditioners, etc. There are still no r '.
strictions on the disposal of these capacitors. It has been
estimated that, by 1978, 140 x 106 kg of PCBs had been
disposed of in landfills (19).
With respect to sanitary landfills, since they continu"'
ously generate CH4 and CO2 by the anerobic decomposition
942 Environ. Sci. Technol., Vol. 19, No. 10, 1985 0013-936X/85/0919-0942$01.50/0 © 1985 American Chemical Socle~
d
I.;
5,
' .1.;
,J.
ed
it
ne
is
for
ire
Bs
his
;he
'lte
ing
on
· of
;he
ses
:1.p-
rge
ing
1ge;
·om
ion
the
~Bs
iels
.ion
ted
e of
.ste.
,sed
bon
1ing
Jers
on
d as
1ing
re-
1een
,een
inu-
tion
:iety
of the organic wastes present, and these gases escape from
he landfills, PCBs and all other volatile materials present
in the landfills should be carried out along with them. For
his reason, sanitary landfills are expected to be a con-
inuing source of PCBs to the atmosphere, in contrast to
industrial and hazardous waste landfills in which gases are
ot being continuously generated and vented. The sig-
'ficance of this source of atmospheric PCBs has not been
eported.
, Multiple hearth incinerators are most commonly used
or sewage sludge incineration. These incinerators are
lindrically shaped with a number of horizontal hearths,
~r stages. Burners are positioned toward the bottom of
he incinerator to supply the auxiliary heat necessary to
ory and burn the sludge. These burners heat the stage
above them to ~815 °C. The combustion gases rise
through the incinerator and exit at the top at ~470 °C.
oist sludge solids enter at the top and are moved
iiownward through the incinerator, with a residence time
on each stage of 5-10 min. As the sludge passes through
e hot stages, water and other volatile compounds evap-
,orate, and the remaining combustible matter burns.
· The point is that multiple hearth incinerators, as sam-
led in this project, have countercurrent heat and sludge
flows. They are then optimally designed to evaporate
:volatile materials present in the sludge before they get to "'e high-temperature area of the incinerator. Thus, com-
i unds such as the PCBs, which are quite resistant to
xidation but reasonably volatile, would be expected to be
·vaporized in the upper stages of the incinerator before
:oinbustion could occur. Any removal of PCBs present
,,.. the incoming sludge then would have to occur in the
~t-gas cleanup system.
·since it has been reported.that sewage sludges (20), stack
yiissions from municipal refuse and sewage sludge in-
~1.perators (16, 21), and emissions from sanitary landfills
(2~-24) contain PCBs, this project was undertaken to
etermine if municipal sanitary landfills and/or municipal
, Juse and sewage_~ludge incinerators in the Great Lakes
,.asin could be significant sources of PCBs to the atmos-
1 ere in this region. Besides being sources of PCBs to the
' mosphere, these emissions are from distinct stacks or
ents, point sources in contrast to the diffuse nature of the
o!her possible sources ·of PCBs to the atmosphere. This
_ kes it possible to get estimates of their emission rates. r.
, '·ocedures
There are a large number of municipal and private
'tary landfills located in the vicinity of Lake Michigan ll) Illinois and Wisconsin and upwind of the prevailing
'nds. Requests for permission to sample were made to
tlie operators of sanitary landfill.s that had sections that
~~re completed, sealed, and had vent pipes in place.
J;!ermission was obtained to collect samples from six mu-
iC?_ipal landfills in this region. These were located in
,edium density urban areas whose economy was mostly
m~ustrially based. The areas contained numerous paper,
cneinical, and motor and electrical equipment manufac-
. ' ing companies. At least one accepted some waste Ii-
ors from paper mills that did some waste paper repro-
essing, and several accepted sludges from wastewater
~atment plants. Because of the number and the variety
('industrial and other sources of refuse to these landfills
hi~h could contain PCBs, it was thought that their
e~issions would give some indication of this source of
OBs to the environment.
pas flow from landfills is caused by two different
~chanisms. One is the venting of the gases generated by
·e anaerobic decomposition of organic materials incor-
porated within the landfill. The production rate of the gas
depends on a number of factors (25), including the com-
position of the waste, the temperature and the moisture
content of the landfill, and the age of the landfill. It is
highest just after filling of the landfill, is reasonably con-
stant for any particular landfill over a period of many
months, decreases with time, and can continue for more
than 50 years. The last filling date for the landfill sections
sampled ranged from 1974 to 1981.
Superimposed on this steady flow of gas are variations
caused by changes in the barometric pressure. Because
of the void air space in a landfill and the presence of only
a few vents, a small change in the barometric pressure can
cause a relatively large change in the flow rate through the
vents. At any time then, the direction and rate of gas flow
through the vents is the result-of pressure caused by the
anaerobic gas production and recent barometric pressure
changes. If the increase in the barometric pressure is
sufficiently large, the net gas flow can be into the landfill,
particularly in older landfills. The variable flow rates, and
the air which can be forced into a landfill, greatly com-
plicate the determination of the emissions of PCBs or other
gases and vapors.
The PCB concentration in the landfill atmospheres
should be determined by the equilibrium of the vapor-
phase PCBs with all of the materials exposed (the fugacity
(26) of the PCBs in all of the phases present would be
equal). Thus, it was assumed that in the absence of ba-
rometric pressure changes, the gas that would be vented
from the landfill would have a constant ratio of PCBs to
methane.
It was also assumed that the gas vented from a landfill
would be a mixture of the landfill gas of steady-state
composition and air which was drawn into the landfill
during times of high barometric pressure. To correct for
the air being forced into the landfills during barometric
highs, the CH4, air, and CO2 concentrations of the vented
gases were measured as the samples were being collected
for PCBs. The PCB concentrations were then normalized
to the CH4 concentrations. With respect to the incine.ra-
tors, requests for permission to sample were made to the
operators of municipal refuse and sewage incinerators in
the Great Lakes basin state of Illinois, Michigan, Wis-
consin, and Ohio. Satisfactory arrangements were made
with the operators of two refuse incinerators and three
sewage sludge incinerators.
Experimental Section
Samples of the landfill gases, which were in effect
headspace samples, were collected from two or more active
vents from each landfill. A clean copper tube (0.8 cm i.d.)
was inserted at least 1.5 m into the vent being sampled,
and the vent was sealed around the tube to prevent air
from being drawn into the vent while sampling. Two metal
tubes (2.5 cm i.d. and 20 cm long) containing 20 g each of
6-20 mesh Florisil were connected in series between the
copper tube and the pump. A dry gas meter was used to
determine the volume of gas drawn through the sampling
tubes. Samples of the landfill gases for the determination
of the CH4, CO2, and air concentrations were collected from
the gas stream exiting the sampling pump. A water U-tube
was used to check that the pressure in the vent pipe was
above atmospheric pressure throughout the sampling pe-
riod.
The techniques and procedures for sampling were the
same for the refuse and sewage sludge incinerators. Stack
samples were collected by using isokinetic sampling tech-
niques from the discharge stack of the incinerator, after
the emission control devices, for the determination of the
Environ. Sci. Technol., Vol. 19, No. 10, 1985 943
PCB concentration. A RAC Staksampler was used, and
the gases and aerosols were drawn through a modified EPA
Method 5 sampling train. The sample train was that used
by Haile and Baladi (27) for the sampling of PCBs from
incinerators, with the exception that none of the impingers
used in this project had deflection plates and bicarbonate
rather than hydroxide was used in the fourth impinger.
Two glass tubes (2 cm i.d.) containing 20 g each of 6-20
mesh Florisil absorbent activated at 450 °C were placed
in series between the third and fourth impingers.
Separate particulate samples were not collected because
a particulate filter created a large pressure drop in the
sampling train. The particulates and the PCBs they
contained, however, were collected in the sampling train.
It was expected that, at the stack temperatures of the
incinerators, PCBs would be chiefly in the vapor phase.
After the collection of the stack samples, the water in
the first three impingers was combined and extracted 3
times with hexane. The sample probe and other glassware
1n front of the Florisil tubes were rinsed with methylene
chloride, and these washings were added to the water ex-
tracts. The Florisil from each sample tube, from either
the incinerator or landfill samples, was extracted in a
Soxhlet apparatus with hexane/ acetone for 16 h ( ~8
min/cycle). In most cases the extracts from the first
Florisil were combined with the impinger extracts and
washings from the equipment and treated as one sample.
The Florisil from the second collect_or tube was usually
analyzed separately to determine if breakthrough had
occurred.
In all cases, the organic solutions were dried and chro-
matographed on Florisil with hexane. The PCBs were
separated by temperature-programmed gas chromatogra-
phy (GC) on a 2 mm x 2 m packed column of 3% SP-2100
on 100-120 mesh Supelcoport. A pulsed current, electron
capture detector (ECD) with a 63Ni source was used. The
amounts were determined by digital electronic integration
of the peak areas (CSI Supergrator 3) and the use of the
different response factors determined by the method of
Webb and McCall (28) using the standards and Aroclor
compositions of Sawyer (29).
Samples of the landfill gases were analyzed immediately
upon collection for CO2, CH4, and air by isothermal GC,
with a thermal conductivity detector, on a 1 mm x 0.4 m
copper column packed with activated charcoal (Carbo-
sphere, Alltech Associates). Air (02 + N2), CH4, and CO2
were quantified by the use of response factors determined
on pure samples of the gases.
Sodium sulfate and Florisil were baked at 450 °C before
use. The Florisil was stored at 130 °C. The solvents,
rinsings of the glassware, and extracts of the Florisil were
checked for the presence of ECO-active materials before
use. An average of 14 blank analyses run on the entire
extraction and cleanup procedure showed 8.5 ± 3.3 ng of
PCBs/sample. Overall recovery of PCBs was checked with
spiked samples. It averaged 74 ± 14%. Portions of Florisil
taken on the sampling trips but not used were extracted
and used as sample blanks. The amount of PCBs in the
incinerator samples was usually more than 100 times the
blanks. Therefore, no correction for the blanks was made.
The amounts of PCBs in the landfill samples were typically
10--40 times the blank value, and a correction for the blank
was made.
The PCB standards used to quantify the samples were
periodically checked against PCB standards prepared
separately and against PCB standard solutions from the
U.S. EPA. Also, two incinerator samples were analyzed
by the Grosse Ile laboratory using capillary GC/ECD (30).
Table I. Methane and PCBs in Sanitary Landfill Gases l
' PCB concn, ng of PCBs/,
ng/m3 landfill % CH4 m3 of CH4
A 390
B 135
C 63 16 367
D (8/7 /81) 380 76 500
(8/20/81) 130 30 433
E 37 53 70
F 196 80 236
average 285 ± 170
Table II. PCBs in Municipal Refuse and Sewage Sh1dge"l
Incinerator Emissions ·
PCBs
volume PCB emitted PCBs .}
incin-sampled, concn, per stack, per ton< ) erator m3 µg/m3 kg/year burned, g ,;
Municipal Refuse Incinerators
1 (5)0 1.5-4.5 0.4 ± 0.045 0.35 ± 0.045 0.0023 ± 0.0003
2 (1) 2.6 0.36 0.265 0.0044
3 (2)
4 (2)
5 (3)
Sewage Sludge Incinerators
2, 4 2.0 0.26
1.5, 2.25 0.43 0.048
1-2 b b
0.0057
0.0033
b
• Number of Samples. b Samples contaminated. c Metric torr . .'
The results were in very good qualitative and quantitati
agreement with those reported here. ,1,
Landfill Results
The results from the landfill samples are shown in Tall
I. The PCB concentrations found in the emissions we
all below 0.5 µg/m3• When corrected for the CH4 conterl'
an arithmetic mean ratio of 285 ng of PCB/ m3 of CH4 W _
found. The standard deviation of ±60% was less th-'
anticipated. The results for landfilll 4 indicate that tlie
methane normalization seems to be correcting for eitri -
neous air in the landfill emissions. Samples collected o
different days at this landfill showed a factor of 3 diffe
ence in the PCB concentration, but the PCB/methah
ratios are within experimental error.
The emis_sions consisted chiefly of chlorobiphenyl co
pounds containing only a few chlorines per molecaj~
typical of those found in Aroclor 1242 and 1016. Quali
tatively, they are what one would expect from the evapo,,
ration of Aroclor 1242, 1248, and 1254 type mixtures (31J.:
Incinerator Results
The results of the analyses of the stack samples froifl
the refuse and sewage sludge incinerators are shown _·
Table II. The one refuse incinerator was sampled reiw.-
larly over a period of 2 months, and the results for the five
samples are shown. _ .-
The results are shown as emissions per stack, as well ..
concentrations. As some of the incinerators had more th ·.
one furnace, each with its own stack, the total emissio -
from the plant would be proportional to the averag
number of furnaces operated. The refuse incinerators ha
electrostatic precipitators to lower the particulate emi _
sions, while the sludge incinerators had afterburners an·,
wet scrubbers. , t
Upon analysis, the samples collected from incinerat9'
5 seem to have been contaminated by Aroclor 1260. Thi~.
prevented the quantification of those samples, but th
pattern of the low molecular weight chlorobiphenyl com-__
pouuu:s, w 111cn cou10 oe seen m the spectra, were similar to those found in the samples collected from the other
• cinerators.
• -The mean concentration of the PCBs found in the in-
" erator effluents quantified was below 1 µg/ma, and the
ounts emitted per stack averaged 0.23 kg/year (see
able II). The pattern of the PCBs in the incinerator
issions varied. Generally, the tri-to hexachlorobiphenyl
mpounds dominated (Aroclor 1248 and 1254 type), with
., e lower molecular weight compounds present in higher
ounts. The concentrations of the mono-and di-
,, orobiphenyls tended to be lower than anticipated on
-a.basis of their volatility. This could be due to a higher
estruction rate in the incinerator or to their not being
·esent in the feed.
The results from incinerator 1 indicate that the com-
sition and concentration of the emissions from refuse
cinerators are variable, and they give some indication
fthe variability over a 2-month period. On one occasion,
pies from incinerator 1 showed higher levels of the
:hta-to octachlorobiphenyls commonly found in Aroclor
, •60, though the relative amount of the compounds
· nt were quite different from virgin Aroclor 1260. This
an expected result and probably reflects the variable
mposition of the feed.
n addition to the above samples, three other types of
ples were collected. In 1981 it was reported that PCBs
e present in natural gas due to contamination by PCBs
the distribution system (32). An analysis of four samples
.
1·atural gas collected in Chicago showed 84 ± 14 ng of
· B/ma. Four ambient air samples collected in Chicago
7tside our laboratory during 1980 and 1981 showed 5.5
2 ng of PCB/ma, and four samples of air from our lab-
~ry showed 182 ± 34 ng of PCB/ma. These last results
port those reported by MacLeod (33) that indoor air
•· onments can have elevated PCB levels.
' . cusszon
¥ is estimated that sanitary landfills in the U.S. generate
: 1010 (34) or 24 X 1010 ma /year (35) of methane. By
. of the average PCB/methane ratio found above, and
e estimates of the amount of methane generated an-
y, a release in the range 10-100 kg/year of PCBs from
)tary landfills in the U.S. is estimated.
•,ompared to the estiinate of 900000 kg/year of PCBs
ihe atmosphere, the emissions which were found here
b~ coming from incinerators ( ~0.23 kg/year per stack)
'landfills are not significant. However, perhaps the
est sources of PCBs to the atmosphere are not point
. , ces, and perhaps not all of the PCBs cycling through
.'atmosphre are new to the environment. For instance,
. t of the PCBs deposited from the atmosphere could
vaporate, and there is now even some evidence that
,,iculate PCBs deposited from the atmosphere in large
·es of water may dissolve and reevaporate (31). Thus,
~tmospheric concentration of PCBs may be maintained
~:high recycle rate, leaving only a smaller loss rate to
. ade up with new material. This would increase the
ificance of all sources of PCBs to the atmosphere.
ii the basis of the results reported here, refuse and
~ge sludge incinerators and sanitary landfills are con-
~uting some PCBs to the atmosphere, but they also
"cate that the major sources of PCBs to the atmosphere
yet to be identified.
e would especially like to thank the incinerator and
111 owners for permission to sample and the operators
for their cooperation during the collection of the samples.
We would also like to thank Peter Kmet and the Bureau
of Solid Waste Management of the Wisconsin Department
of Natural Resources for their help and cooperation in this
project.
Registry No. CH4, 74-82-8.
Literature Cited
(1) Bidleman, T. F.; Olney, C. E. Science (Washington, D.C.)
1974, 183, 517-518.
(2) Harvey, G. R.; Steinhauer, W. G. Atmos Environ. 1974, 8,
777-782.
(3) Atlas, E. L.; Giam, C. S. Science (Washington, D.C.) 1981,
211, 163-165.
(4) Tanabe, S.; Kawano, M.; Tatsukawa, R. Trans. Tokyo Univ.
Fish. 1982, 5, 97-109.
(5) Eisenreich, S. J.; Looney, B. B.; Thorton, J. D. Environ.
Sci. Technol. 1981, 15, 30-38.
(6) Murphy, T. J.; Rzeszutko, C. P. J . Great Lakes Res. 1977,
3, 305-312.
(7) Murphy, T. J.; Paolucci, G.; Schinsky, A. W.; Combs, M.
L.; Pokojowczyk, Duluth Environmental Research Labo-
ratory, May 1981, U.S. EPA Project Report R-805325.
(8) Swain, W.R. J. Great Lakes Res. 1978, 4, 398-407.
(9) Strachan, W. M.; Huneault, H.J. Great Lakes Res. 1979,
5, 61-68.
(10) Eisenreich, S. J.; Hollod, G.; Johnson, T . C. "Atmospheric
Inputs of Pollutants to Natural Waters"; Eisenreich, S., Ed.;
Ann Arbor Science: Ann Arbor, MI, 1981; pp 425-444.
(11) Willford, W. A.; Hesselburg, R. J.; Nicholson, L. W. Con/.
Proc.-Natl. Conf. Polychlorinated Biphenyls 1975, EPA-
560/6-75-004, 177-181.
(12) Fed. Regist. 1984, 49, 21514-20.
(13) Jacobson, J. L.; Jacobson, S. W.; Fein, G. G.; Schwartz, P.
M.; Dowler, J. K. Dev. Physchol. 1984, 20, 523-532.
(14) Doskey, P. V.; Andren, A. W. J. Great Lakes Res. 1981, 7,
15-20.
(15) Eisenreich, S. J . Looney, B. B. In "Physical-Chemical Be-
havior of PCBs in the Great Lakes"; Mackay, D.; Paterson,
S.; Eisenreich, S.; Simmons, M., Eds.; Ann Arbor Science:
Ann Arbor; MI, 1983; pp 141-156.
(16) Richard, J. J.; Junk, G. A. Environ. Sci. Technol. 1981, 15,
1095-1100.
(17) Eisenreich, S. J. Bidleman, T. F. Murphy, T. J.; Davis, A .
R.; Banning, D. A.; Giam, C. S.; Priznar, F. J.; Mullin, M.
D. In "The Potential Atmospheric Impact of Chemicals
Released to the Environment. Proceedings of Fo1.1r
Workshops", Miller, J.M., Ed.; U.S. EPA Office of Toxic
Substances, Washington, DC, 1980; EPA 560/5-80-001.
(18) National Academy of Sciences "Polychlorinated Biphenyls";
National Academy of Sciences: Washington, DC, 1979; p
23.
(19) National Academy of Sciences "Polychlorinated Biphenyls";
National Academy of Sciences: Washington, DC, 1979; p
15 .
(20) Furr, A. K.; Lawrence, A. W.; Tong, S. S. C.; Grandolfo,
M. C.; Hofstader, R. A.; Bache, C. A.; Gutenmann, W. H.;
Lisk, D. J. Environ. Sci. Technol. 1976, 10, 683-687.
(21) U. S. Environmental Protection Agency, June 1975,
Technology Transfer Publication, EPA-625/4-75-009.
(22) Bidleman, T. F.; Burdick, N. F.; Westcott, J. W.; Billings,
W. N. In "Physical-Chemical Behavior of PCBs in the Great
Lakes"; Mackay, D.; Paterson, S.; Eisenreich, S.; Simmons,
M., Eds., Ann Arbor Science: Ann Arbor, MI, 1983; p 15-48.
(23) Weaver, G. Environ. Sci. Technol., 1984, 18, 22A-27A.
(24) Murphy, T. J.; Rzeszutko, C. P. July 1978, U.S. EPA Report
EPA-600/3-78-071. .
(25) McBeari, E. A.; Farquhar, G. H. Water Air Soil Pollut. 1980,
13, 157-172.
(26) Mackay, D. Environ. Sci. Technol., 1979, 13, 1218-1223.
(27) Haile, C. L.; Baladi, E. 1977, U.S. EPA Environmental
Monitoring Series Report EPA-600/4-77-048.
(28) Webb, R. G.; McCall, A. C. J. Chromatogr. Sci. 1973, 11,
366-373.
(29) Sawyer, L. D. J . Assoc. Off. Anal. Chem. 1978, 61, 272-281.
Environ. Sci. Technol., Vol. 19, No. 10, 1985 945
I ,I
I