Air Toxics Emission Inventory
for the
Southeast Chicago Area
John Summerhays
Harriet Croke
Air & Radiation Branch
Region V
U.S. Environmental Protection Agency
July 1987
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Table of Contents
Page
Introduction . 1
Methods Used in Inventorying Point Sources 5
Area Source Inventorying Methods 8
Mobile Source Inventorying Methods 13
Wastewater Volatilization Inventorying Methods 17
Inventorying Methods for Hazardous Waste Treatment
Storage and Disposal Facilities 18
Summary of Results 18
Discussion of Results 28
General Observations 36
Bibliography 40
Appendix A Sample Questionnaire
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List of Tables
Table 1. Substances included in Inventory 4
Table 2. Particulate Matter Species Fraction 7
Table 3. Species Fractions Used in Area Source Inventory 10
Table 4. Emission Factors Used in Area Source Inventory 11
Table 5. Highway Vehicle Species Fractions 16
Table 6. Summary of Emissions" from All Source Types 19
Table 7. Area Source Emission Totals 20
Table 8. Highway Vehicle Emissions Totals 21
Table 9. Uastewater Treatment Plant Emissions Estimates 22
Table 10. Emissions Estimates for Facilities Receiving
Questionnaires 23
Table 11. Emissions from Coking Operations 24
Table 12. Point Source Emission Estimates Based on Organic
Species Fractions 25
Table 13. Point Source Emission Estimates Based on Particulate
Matter Species Fraction 27
Table 14. Point Source Emission Estimates Sorted by SCC 29
Table 15. Organic Species Fraction-based Estimates for Facilities
Receiving Questionnaires 33
Table 16. Particulate Matter Species Fraction-based Estimates for
Facilities Receiving Questionnaire 34
List of Figures
Figure 1. Southeast Chicago Source Area and Receptor Area
Page
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Air Toxics Emissions Inventory
for the Southeast Chicago Area
Increasing national attention has focussed on the health risks from "toxic"
(non-criteria) air pollutants that arise in urban areas where a concentrated
level of industrial activity coexists with high population density. Within
Region V. perhaps the most serious combination of concentrated industrial
activity with high population density is in Southeast Chicago. In particular.
the area is one of the foremast locations for integrated steel production and
chemical production of the coatings used in Chicago's substantial manufacturing
economy. This area also has onp of the nation's five permitted PCB incinerators
and has a variety of other facilities for treating, storing and disposing of
hazardous waste. Therefore, Region V, with assistance from the Illinois
Environmental Protection Agency (IEPA) and the Indiana Department of Environ-
mental Management (IDEM), has compiled a comprehensive inventory of "air toxics"
emissions in the Southeast Chicago area.
The inventory described in this report represents the first component of a
three part project. The next component of this project is a modeling analysis,
which will serve to estimate the exposure of Southeast Chicago residents to the
emitted pollutants. The third component will then estimate the health risks
that would be expected from the estimated exposure.
In any inventory of this type, resource considerations require a choice between
developing a screening inventory covering multiple source types using only
readily available information versus developing a more focussed inventory
investigating only a few source types or pollutants. This inventory may he
considered a screening inventory, intended to provide an overview of air
carcinogen emissions in the covered area.
This inventory has been designed to be comprehensive in several respects.
First, this study has attempted to include all source types that emit air
toxics. Second, although the focus of this study is an exposure in a moderate
sized area (approximately 65 square miles), a much broader area was inventoried
to include all sources with potentially significant impacts in the selected
receptor area. Third, this study inventoried for a comprehensive list of
potential carcinogens. Specifically, the inventory included all potential
carcinogens for which a dose-response relationship has been estimated even
including some compounds with minimal evidence of carcinogenicity. This
inventory also included three compounds which are not suspected of being
carcinogens but have been measured at relatively high concentrations in the
area. Unfortunately, apart from these three compounds, the inclusion of
compounds of the basis of noncarcinogenic health effects was judged to be
beyond to scope of this study, due to the relative sparsity of data on dose-
response relationship for such health effects, the uncertainties about presence
and magnitude of threshold concentrations, the uncertainties about the relative
importance of short term peak versus long term average concentrations, and the
analytical difficulties of considering these various parameters. Also, a fourth
substance, mercury, is also not a suspected carcinogen but was included because
a National Emission Standard for Hazardous Air Pollutants has been promulgated
for this pollutant.
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With respect to source types, this study included all source types for which air
toxics emissions could be estimated., The inventory included point sources,
area sources, and mobile sources,, and further included volatilization from
wastewater treatment plants., Emissions estimates for hazardous waste treatment,
storage and disposal facilities (TSDF's) have been difficult to derive but are
expected to become available in the next few months. It must be noted that
there may be source categories which are not included because data for estimating
the emissions are not available,, On the other hand, it is a reasonable hope
that data are available for the most significant categories.,
With respect to spatial coverage, Figure 1 is a map showing both the target
"receptor area" for the exposure analysis and the broader source area included
in the inventory. The target area of the exposure analysis component of this
study is an area approximately 13 kilometers square (8 miles square) for a
total of 167 square kilometers (65 square miles). The specific boundaries of
this receptor area are: north-87th; south-Sibley Blvd/Pulaski St,; west-Western
Ave,; and east-Indiana/Illinois border. In order to include all significant
sources, a substantially larger source area was inventoried. The source area
covers a 46 kilometer (about 29 miles) square area. Since the -prevailing winds
in the area are from the southwest quadrant, the source area is skewed toward
the south and west of the receptor area. The specific boundaries of the source
area are, in terms of UTM coordinates from 4584 to 4620 kilometers northing and
from 420 to 466 kilometers easting in zone 16, This source area extends
approximately 30 kilometers south and west and 16 kilometers north and east
of the center of the receptor area. The inventory further includes a few
additional point sources which are outside this source area but were judged to
be potentially significant sources.
With respect to pollutants covered, the inventory includes 47 compounds for
which quantitative estimates of carcinogenicity (unit risk factors) have been
made. The list of compounds is given in Table 1 and includes 22 nonhalogenated
organics compounds, 17 halogenated organic compounds (including 16 chlorinated
and one brominated organics), and 8 inorganic species (especially metals). It
is important to note that the carcinogenicity of some of these compounds is
quite speculative. Nevertheless, these compounds were included so that any
error would be on the side of being comprehensive. As noted above, the compound
list also included four compounds which are not suspected of being carcinogenic,
but otherwise did not include any compounds on the basis of noncarcinogenic
health effects. It might also be noted that several of the compounds on the
inventory are relatively esoteric. As will be discussed below, the inventory
for Southeast Chicago found emissions for 39 of the 51 compounds.
Some of the pollutants in this study warrant special discussion. First, form-
aldehyde is not only emitted into the atmosphere but it is also photochemically
formed during atmospheric reactions of other organics. Current evidence
indicates that substantially more formaldehyde results from photochemical
formation than from direct emissions. Thus, the ultimate total exposure estimate
is likely to rely more heavily on monitoring data, with the inventorybased
exposure estimate serving only to help characterize the relative importance of
emissions versus photochemical formation. Somewhat similar considerations
apply for a second pollutant, carbon tetrachloride. This compound has an
atmospheric half-life of many years, and so exposure may be more a function of
historic emissions than of current emissions. Thus, monitoring data may again
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SountAST CHICAGO
SOURCE AREA & RECEPTOR AREA
~i
IWIIUS (|IO»I
HOIINCBNOOK |
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Table 1. Substances included in inventory
Acrylamide
Acrylonitrile
Benzene
Butadiene
Coke Oven Emissions
Diethanolamlne
Oimethylni trosamine
Dioctylphthalate
Ethyl Acrylate
Fthylene
Fthylenp Oxide
Formaldehyde
Gasoline Vapors
Isopropylidene Diphenol
Mel amine
Nitrobenzene
Nitrosomorpholine
Polycyclic Organic Matter
Propylene Oxide
Styrene
Terephthalic Acid
CHLORJ_NAJEP_ YOG (17)
Allyl Chloride
Benzyl Chloride
Carbon Tetrachloride
Chloroform
nioxin
Fpichlorohydrin
Fthylene Dibromide*
Ethylene Dichloride
Methyl Chloride
Methylene Chloride
Pentachlorophenol
Perchloroethylene
PCB's
Propylene Dichloride
Trichloroethylene
Vinyl Chloride
Vinylidene Chloride
INORGANIC. (8)
Arsenic
Asbestos
Beryllium
Cadmium
Chromium
Nickel
Titanium Dioxide
Radionuclides
( 4 )
Acetone
Mercury
Toluene
Xylene
*Although ethylene dibromide is not, strictly speaking, chlorinated, it is halogenated
and is included among chlorinated compounds due to chemical similarity.
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may be a more reliable basis for assessing exposure., A third "pollutant" ,
identified here as polycyclic organic matter, is actually a class of aromatic
compounds,. Three of the lightest such compounds, namely napthalene (a two ring
structure)„ anthracene (a three ring structure), and phenanthrene (also a three
ring structure), are both among the most highly emitted and among the least
toxic of this class of compounds., In order to focus on the more significantly
toxic compounds, this inventory includes not only an estimate of total polycyclic
organic matter but also an estimate of "heavy" polycyclic organic matter that
excludes these three compounds, A fourth pollutant, chromium, also in a sense
represents a class of pollutants., In this case the different forms are diffe-
rent valence states, including- Cr*6 (such as found in chromic acid), Cr*3, and
neutral (metallic) chromium. It is known that Cr"^ is the most toxic form, but
it is usually not clear what mix of valence states is present in any set of
emissions. Generally, this inventory conservatively assumed that all chromium
in the most toxic valence,
Methods used in Inventorying Point Sources
The first component of the inventory was for discrete industrial facilities
within (or in a few cases, just outside) the source area0 For 29 of the 88
facilities in the source area, questionnaires were sent to the facility by the
appropriate State agency (Illinois EPA for Illinois sources, Indiana DEW for
Indiana sources). The selection of facilities was intended to include the
sources suspected of having the greatest air toxics impact on the receptor
area. The first step in the selection procedure was to develop rankings of
criteria pollutant impacts on the receptor area. Two rankings were developed,
including one for VOC and the other for total suspended particulate matter
(TSP), based on indices defined as the respective pollutant emissions divided
by distance from source to the center of the receptor area. For the top 25
sources in each ranking, the second step of the selection procedure was a
subjective screening of sources for the probability of emitting compounds of
interest. This second step of the procedure effectively took into account the
fact that VOC and TSP emissions totals are not necessarily indicative of air
toxics emissions. This process led to the selection of 13 facilities. In
addition, all other chemical manufacturing facilities were included, representing
an additional 16 facilities (above and beyond 2 chemical manufacturing facilities
selected on the basis of the ranking procedure),
A copy of a sample questionnaire is included as Appendix A, This questionnaire
asked the companies to make their own estimates of emissions of each of the
substances on the inventory list, and asked for a few other pieces of infor-
mation needed for modeling. Comments regarding the challenges confronted
during the process of companies answering and U,S, EPA processing these ques-
tionnaires are given in a concluding section of this report. It may be noted
here that substantial followup was often necessary to obtain responses, and in
many cases the companies asked U,S,EPA to supply appropriate species fractions
or even to estimate emissions (e,g, from storage tank data). Also, in U,S,EPA's
review of questionnaire responsesB companies were asked in a few cases to clarify
or to confirm their responses.
For the other 59 facilities in the source area, a method labeled the "species
fraction method" was used. The first step of this method is to obtain emission
estimates for total volatile organic compounds and total suspended particulate
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matter for each operation of each facility. The second step of the method is
to obtain species fractions representing the fractions of the total VOC or the
TSP that are emitted as the various individual species. For example, in this
study, the fugitive emissions from purging operations at refineries were esti-
mated to be 2.4% benzene. These fractions are then multiplied times the VOC
or TSP emissions estimate to obtain estimates of emissions of individual
species.
The two main sources of species fraction information were the Volatile Organic
Compound (VOC) Species Data Manual and the Receptor Model Source Composition
Library. The index indicating-which species profiles in the VOC Species Data
Manual (i.e., which sets of species f-ractions) should he applied to which SCC's
was developed by the GCA Corporation for another project (the National Acid
Precipitation Assessment Program) being undertaken by U.S. EPA. Both the
profiles and the index are shown in reference P. 2. The authors developed the
index indicating which sets of metal species fractions from the Receptor Model
Source Composition Library should be applied to which SCCs. This index is shown
as Table 2. For this study, estimates of total VOC and TSP emissions were
taken from the National Emissions Data System (NEDS), which provided emissions
data and identified the Standard Classification Code (SCC) for each operation
at each facility.
One subtle point concerning the use of species fractions with VOC totals con-
cerns compounds that are negligibly photochemically reactive, such as methane
and methylene chloride. In some cases, the VOC emissions may be derived in a
way that excludes these compounds. To the extent this is true, it would be
desirable to apply species-fractions derived on the same basis, i.e., species
emissions as fractions of just the reactive VOC. Unfortunately, it is not
clear what VOC emission estimates exclude the negligibly reactive species.
Therefore, all species fractions were derived and applied on a fraction-of-total
VOC basis. In any case, the negligibly reactive portion of VOC tends to be
small, so that any error here is likely also to he small.
The estimation of emissions by the species fraction method was performed for
all facilities, including facilities that were sent questionnaires. This
provided the opportunity for quality assurance test of comparing the results
of these two methods.
Limited additional information was obtained from a variety of other sources.
Coke oven emissions were based on TSP emissions estimates provided as part of
Indiana and Illinois TSP SIP submittals. Based on information in reference
P.6, emissions of the pollutant identified as "Coke oven emissions" (including
organics soluble in benzene) were estimated as 1.1 times the TSP emissions for
relevant emission points (coke oven charging and leak emissions). Estimates of
benzene emissions from coke by-product recovery plants were obtained directly
from reference P.7, (except for Acme, for which an Illinois EPA estimate was
used). Toluene and xylene emissions estimates were derived from benzene emis-
sions estimates based on information in reference P.7 suggesting that the coke
oven gases are 60-85% benzene, 6-17% toluene, and 1-7% xylene.
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7
Species fraction information for formaldehyde from utility fuel combustion and
from industrial coal combustion was derived from the formaldehyde "locator
document" (Locating and Estimating Air Emissions from Sources of Formaldehyde,
refo P»4e)o This document provided emissions factors in units of grams per
Joule of heat Input, which was multiplied times the heat content of typical
locally used fuels and compared against the standard VOC emission factor to
derive the formaldehyde species fraction.,
Area Source Inventorying Methods
As with point sources, the most, commonly used method for developing area
source emissions estimates was the species fraction method. The categories
inventoried by this method, the species fractions, and other relevant
information are shown in Table 3. In general, the first piece of necessary
information was a county-by-county estimate of emissions from each category
being assessed., This information was generally derived by the State from the
1982Qhj_cago ozone State Implement at ion_£lan_l5IP)° The SIP included VOC
based for £Aflmle_jan_ADJ3£flj^ factors
ne sales or numbprTP tJJBeSL-jaA-^8JbQJlOJpi£JJ&£& TSP pmi SSJJXO— £a£Jbttr» The
SIP provided county VPOC emissions estimates in kilograms per day for 1980 and
1987» Illinois EPA staff converted these estimates to annual emissions (tons/
year) and interpolated to 1984 emissions for Illinois counties, and the authors
performed similar calculations for Lake County, Indiana,,
The second piece of information was then a set of species fra££ions, which
could be multiplied times the county VOC or TSP emi^s 1 ons j£fl_obtflj n county totaj
ecies ejjfTjppSgg^ — mr^nrrs point a thiTd^ step of spatial disaggregati on was
performed „ ThTs step was necessary to support the modeling analysis of
population exposure, since the exposure in the receptor area to emissions is a
function of the spatial distribution of emissions,, For_ejch source category, a
parameter (e.g. _populajJLop ) j-***— ^Lgg£ed whTcTT could be assumegrto
For each source category, then, each
2 k i 1 ometer_ar^squa^re was assigned a fraction of the coafrjacrgmijgions equal
to the grid square "^Traction of the total surrogate parameter in "tKeTcounty .
For example, if a grid had 1% of Cook County's arterial traffic, the grid would
be assigned 1% of Cook County's gas marketing emissions. Note that although
most of the surrogate data were 1985 projections made in 1976, the use of these
data for performing spatial allocations should not introduce any significant
errors.
A second method used for inventorying areas sources was an emission factor
approach., The catefories inventoried by this method, the emissions factors,
and other relevant information are shown in Table 4. This method was used in
different forms for different categories. For heating, the available emission
factors for formaldehyde and polycyclic organic matter (POM) for various types
of fuel use were multiplied times county level estimates of the quantities of
the respective fuels used. These emissions .»ort» t.hpn
to estimate emissions in each of the above grids. For per capita emissions,
(e.g. the emissions fromj/arious consumer products), emissions in each grid
square were estimated T)y"multi plying the per capita emissions factor times the
number of people in the grid square.
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Table 2. Participate Matter Species Fractions
(Taken from Reference P. 3. All data in percent)
.Sgec_1es_ Fraction*
Source Category Arsenjic Cadmiuni Chromium Mercury Nickel
Coal combustion
Oil combustion
Steel making:
Sinter plants
.058% .006% .054%
.015 .001
:ay iron foundries
Asphalt roofing
Glass manufacturing
Gypsum manufacturing
Lime and cement
manufacturing****
Refinery heater
(gas-fired)
Refinery cat. cracker
Municipal incinerator
.012 .006
.023 .003
.050** .050**
.020
.010
.115
.089
.550** .550** 3.000
Open hearth.
basic oxygen furnaces .050** .050** .20
550*
.040%
1.622
Applicable
SCCs
.036
.003
5.330
1-01-002-01,-02.-03.-23
1-02-002-01,-02,-04
1-01-004-01,
1-02-004-01,-04
1-02-005-01,-04
3-06-001-03***
3-03-008-01. -02. -08, -09
-11, -12, -13, -14. -21
-22, -24, -25, -99
.20
.038
.550**
.218
.550**
.011
3-03-009-04, -10, -11, -12, -13
-14, -15, -31, -32, -33, -99
3-04-007-01, -05, -06. -07
-15, -99
.067 3-04-003-01. -20. -31, -40
-50, -51
3-05-001-01, -02, -03, -04, -05
.004 3-05-015-01. -02, -06, -08. -10
.550** 3-05-015-01, -02, -03, -04
.00012 3-05-006-06
-3-05-016-01. -02, -04, -07, -08
-09, -10. -14, -15, -99
.550**
.43
.014
3-06-001-04
3-06-002-01
5-01-001-02
* Although reference P.3. shows data for beryllium, beryllium does not show up for any source
types in Southeast Chicago.
** Where this table (and reference P.3) shows species fraction of .550% and .050%, the original
study reported values of "trace" (0.1 to 1.0%) and "below detection limits" (<0.1%).
*** SCC 3-06-001-03 is for oil-fired process heaters at refineries.
f*** These species fractions are not taken from reference P.3 but are derived from the
"locator documents" references P.4.f and P.4.g.
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9
ss*
For dejacgajsing^ county level emissions estimates were derived from a national
study that estimated tofeal usage of each of the compounds, dlvidejl-tha-±atal
h the total number o_f__employees in the Standard Industrial Classification
levant to the respective compound, and multiplied £h&_ce&»J-feaat
factor tiJH&s^.^^o niimhQje_JoJE_J&jmaljoj/ees in tJbj&sg-jcJLASLSifi cat ions employed
mtlgs^Jjg^^ r.hicagcLAce^ County emissions were then
distributed according to total manufacturing employment, since spatial distri-
bution data were not avaiable for the specific industrial categories. Similarly
for dry cleaning, national emissions data were distributed to county level
estimate using employment data for relevant SICs, which were in turn distributed
to grids in the study area using commercial employment data- For comfort
cooling towers, the draft background, information document for a possible NESHAP
(reference A.13) provided per capita emission factors reflecting the per capita
number of buildings in six building size ranges and emissions factors for each
size range adjusted to reflect the probability of having a comfort cooling
tower and the probability that chromium is used as a corrosion retardanto
These emission factors were provided on a state-by-state basis to reflect the
cooling load in each state,, Reference A013 provided upper and lower bound esti-
mates reflecting disparate emissions testing results,. This study used the more
conservative,, upper bound value; the lower bound value is about 28 times lower.
The ratio of Cook County population versus "other" (nonmanufacturing, non-
coiranerical) employment (3.4 people/"other" employee) was used to adjust the per
capita emission factor to a per "other" employee emission factor, which was
used with gridded "other" employment data to estimate grid-by-grid emissions0
An important subcategory within heating is residential wood combustion. This
category includes woodburning in wood stoves, wood furnaces, fireplace inserts,
and fireplaces. The principal data sources for estimating wood usage were a
contractor study for the Department of Energy and the Department of Energy's
Residential Energy Consumption Survey (RECS) data (References A,7 and A,8),
The contractor study estimated state by state wood usage based on th* heating
degree days for the state, the probable proportions of households using wood as
a primary or secondary heat source, and various surveys indicating the relationship
between these factors and wood usage for each kind of wood user. This survey
indicated a 1981 statewide Illinois usage of 1830,000 dry tons of wood per year
(about 2,150,000 actual tons/year or 1,510.000 cords/year). This translates to
about 0,43 dry tons of wood (about 0,50 actual tons or n.35 cords) per year
per Illinois household. However, the Chicago area is likely to have a lower
percentage of wood burners and a lower rate of wood consumption that the
estimated Illinois average. Therefore, RECS data on the wood usage in central
cities in the Worth Central region of the United States versus the regional
average wood usage were used to adjust the Illinois usage estimates. These
data indicated that in central cities in the North Central U.S., 0,8 million
cords were used per year, which divided by approximately 5.8 million households
represents 0.14 cords/household. By comparison, in the full North Central
region, 10,9 million cords divided by 22075 million households represents 0,48
cords per household. (For reference, these data suggest that the central city
usage of 0.14 cords/year represents 16% of the households burning 0.9 cords/year,
and the regional usage of 0.48 cords represents 21% of the households burning
2,3 cords/year.) Thus, the urban usage may be estimated at 0,14/0,48 or 29% of
the regional usage. On this basis, Chicago area wood usage was estimated to
be 29% of 0.43 dry tons per year, equalling 0.12 dry tons (OdO cords or 0.14
actual tons or 288 pounds) per ypar per household.
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Table 3. Species Fractions used in Area Source Inventory
(except as noted, units are % of VOC emissions)
Category
Gasoline
Marketing
P^TJ.utarvts
Benzene
Toluene
Xylene
Ship and Benzene
Barge Transfer Toluene
Xylene
Fractions
.63%
.64%
.18%
.63%
.64
.18%
Spatial dbn
Parameter
Arterial VMT
Distributed
within port
areas
Reference
A. 3
A.3
Architectural
Surface
Coating
Benzene .18%
Methyl Chloride .27%
Methylene Chloride 3.37%
Toluene 7.60%
Xylene 1.36%
Dwelling units
A.3
Heating
(oil-fired)
Chromium
Nickel
.047%*
5.36%*
**
P.4
Heating fractions are fractions of total suspended particulate emissions.
** Spatial distribution parameter for industrial distillate oil use was
manufacturing employment. Parameter for all commercial/institutional
and residential fuel oil usage was population. Emissions for indus-
trial residual oil and coal usage and for all utility fuel usage were
considered in the point source inventory.
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Table 4. Emissions Factors used in Area Source Inventory
Source Category
Pollutant
Heating
Resid. oil: Comm/Inst* Formaldehyde
Dist. oil: Industrial
Comm/Inst
Residential
Gas: Industrial
Comm/Inst
Residential
Emission Factor
.069 ng/J (10.8 mg/gal)
.10 ng/J (14.5 mg/gal)
Spatial dbn. Ref.
Wood stoves, Fireplaces
D1st. Oil (all users)
Gas (all users)
POM
.038 ng/J ( 41 g/mmcf)
.095 ng/J ( 103 g/mmcf)
.43 ng/J ( 464 g/mmcf)
.078 g/kg wood***
8.7 pg/J (1.4 mg/gal)***
11.2 pg/J (12 g/mmcf)***
Per Capita Emissions
Aerosol Cans
Paint Stripping
Misc. Products
Chlorinated
Drinking Water
Miscellaneous
Methylene Chloride
Methylene Chloride
Formaldehyde
Chloroform
.50 #/capita-yr
.59
.048 "
.029 "
Population
Mfg. emp.
Population
Population
mfg. emp.
Population
Population
dwell, units
population
population
population
Hospital sterilizing Ethylene oxide
Chrome platers
Chromium
2.8#/year/bed (> 200 beds)
.2#/year/bed (< 200 beds)
82.54/year per known facility
***
***
Comfort cooling towers Chromium
Degreasing
Dry cleaning
Methylene Chloride
Perchloroethylene
Trichloroethylene
Perchloroethylene
*****
*****
mfg. emp.
comm. emp,
P.4e
P.4
A.10
A.10
P.4e
P.4c
2.5#/year/1000 "other" "other" emp.
employees****
Author's
survey
A.14
A.13
A.10
A.11
A.12
A.11
*Some of the abbreviations used on this page: Comm/Inst - commercial and institutional
Resid. - Residual: Dist. - distillate: ng - nanograms (10~* grams):
POM - polycyclic organic matter; mfg. - manufacturing: emp. - employment.
**Excludes naphthalene, anthracene, and phenanthrene (see text). Emission
factor for woodstoves and fireplaces is 60% of total POM, for distillate oil
is 90% of total POM. and for gas is 100% of total POM.
***Distributed at actual location.
****"0ther" employees are nonmanufacturing, nonretail employees.
*****Degreasing and dry cleaning emission estimates are derived from national
emissions totals disaggregate to county totals based on employment within
specified Standard Industrial Classification (SIC) Codes. Codes used for
degreasing were 25, 34, 36, 37, and 39, and for dry cleaning were 7216, 7217
and 7218.
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12
,«»
The emission factor is derived from data given in a draft POM "locator document",
entitled "Locating and Estimating Air Emissions From Sources of Polycyclic
Organic Matter (POM)"0 The emission factor of 78.0 mg POM per kg wood reflects
first an exclusion of three lighter-weight POM (napthalene, anthracene, and
phenanthrene) and then a numerical averaging over all uncontrolled wood stoves
and fireplaces (not including three fireplace measurements which did not reliably
measure gaseous emissions,,) Note that this emission factor is 60% of the
emission factor that would have been obtained had the three lighter weight
compounds not been excluded*
A third method used might be called the special survey method. The results of
these surveys are also shown on Table 4. Line oFinie" special surveys was conducted
for chroma plating,, which emits chromium., The chrome plating survey was based
on the "yellow pages" of the telephone directory,, This survey indicated 17
facilities within the Southeast Chicago source area,, Information was then
obtained from U.S. EPA's Office of Air Quality Planning and Standards (OAQPS),
indicating that based on the data obtained in development of a potential NESHAP
for chrome plating, one could assume a national average plant emissions of 33
pounds chromium per year. Unfortunately, the listing of platers in the yellow
pages presumably does not include "captive platers" which perform chrome plating ,_
as one step in manufacturing their own product (e0g«, chrome plating as part of
an auto assembly plant): this listing presumably only includes "job shops" who
specialized in plating work for other customers,, Data from OAQPS suggest that
"job shops" represent about 40% of total plating, so the emissions estimate
here was adjusted accordingly. Note that the result should be quite conservative,
both because in reality "job shops" tend to be disproportionately high emitters
and because the survey assumed that all platers performed chrome plating,
A second special survey was for hospital use of ethylpne=o=x=ide for purposes of
,sterilizing. The first step of this survey was tlTTontact TRe State Department
of Health, which provided an inventory of hospitals in t^e State,, This inventory
showed four hospitals in this study's "receptor area" and a total of 24 hospitals
in the overall source area. The second step was to contact the purchasing
departments of the four "receptor area" hospitals to request information on
annual ethylene oxide usage. The third step was to use this information to
assess an emission factor. The emission factor was developed on a per bed
basis, since the number of beds is an easily obtained piece" of information
which is considered indicative of the patient load and thus the amount of
sterilization taking place at a hospital. (The number of beds does not include
"long term care" beds such as found at nursing homes, since such beds are
expected not be associated with significant ethylene oxide use.) The fourth
step was to multiply the per bed emission factor times the number of beds in
each of the hospitals in the source area.
The results of the four hospital survey were as follows: one hospital (427
beds) used 2430 pounds per year: a second hospital (418 beds) used steam, not
ethylene oxide, for sterilization: a third hospital (176 beds) also used steam,
not ethylene oxide: and a fourth hospital (168 beds) used 80 pounds per year
(only a small part of the hospital's sterilization used ethylene oxide). Four
hospitals is of course a small sample, and so the emissions factors derived are
-------
13
x<=*
very approximate,, Nevetheless, the survey suggested that small hospitals are
less likely to use ethyfene oxide sterilizers then large hospitals, so separate
emission factors were derived- (The outpoint between "large" and "small" was
arbitrarily set at 200 beds.) Also, obviously not all hospitals use ethylene
oxide for sterilizing. Thus, a large hospital emission factor was estimated
by averaging the per bed usage for hospital 1 (2.8 pounds/bed) and hospital 2
(0), and a separate, small hospital emission factor reflected an average for
hospital 3 (0) and hospital 4 (.24 pounds/bed).,
The data used in this survey reflected only Illinois hospitals. Rather than
obtain an inventory of hospitals in Indiana, a per capita approach was used to
estimate hospital usage of ethylene oxide in Northwest Indiana. The per capita
emissions factor used was 0.010 pounds per year, derived from the Illinois
results indicating 22,172 pounds emissions by hospitals serving 2,160,180 people.
Mobile Source Inventorying Methods
As with most of the area source categories, highway vehicle emissions were
inventoried using the species fraction method. For both Illinois and Indiana.
the analysis differentiated between emission on freeways and arterial emissions
(i«6o, emissions on arterial roadways and local streets). In Illinois,
total county level VOC emissions were first derived, adjusted, and dvvidjgd
into freeway and arterial emissions. A variety of species fractions were
deTfve^rancr usea fo~ol5tain courrcy ^level emissions of individual compounds.
Finally, the spatial distribution of these emissions data was estimated accord-
ing to qridded IfaTa on freeway Ind arterial =vejilclg_jT'-i Lg£==&ag^alg4=XVMT)° I"
Indiana, gridded emissions data were already available, from the 1982=ozone
§XP, so it was only necessary to make adjustments and apply species'TracTTons
to obtain the desired inventory. The following discussion documents these
calculations and the basis of the underlying data in more detail.
The Illinois county level VOC emissions data were derived by the Illinois EPA
based on data in the 1982 ozone SIP. These data were logarithmically inter-
polated between 1980 and 1987 to a 1984 base year and converted by Illinois EPA
from units of kilograms per day to units of tons per year. The next step of
the analysis used mobile source emissions models to make a .set of adjustments
from conditions inherent in the SIP to conditions appropriate here and
simultaneously to disaggregate the arterial and freeway exhaust emissions and
the evaporative emissions. The first run, designed to correspond to the SIP
emissions estimate, used MOBILE 2, used a summer temperature of 75°F, the
Federal Test Procedure (FTP) average speed of 19.6 miles per hour (mph), vehicle
mileage and registration data given in the SIP, and areawide averages for VMT
mix and hot start/cold start percentages. Then, two runs of MOBILES were made
to estimate updated, more annual average emissions factors for the Southeast
Chicago area. Both of these runs used an annual average temperature of 50°F,
and the same mileage and registration data as in the SIP. The run for arterials
used a speed of 19.6 mph and hot start/cold start percentages given in the SIP
for the southern Chicago area arterials, and the run for freeways used a speed
of 45 mph and zero percent hot starts and cold starts. The ratio of these
MOBILES results to the MOBILE2 results was multiplied times the SIP-derived
county emissions totals to derive adjusted county emissions totals for arterial
exhaust emissions and freeway exhaust emissions.
-------
14
x«*
A similar procedure was used to estimate adjusted county total evaporative
emissions. However, one additional step in this procedure was to assign all
evaporative emissions to arterials, i.e.,, to reassign emissions to arterials
that otherwise would have been assigned to freeways„ Since most of these
emissions may be assumed to occur at trip ends, this reassignment was intended
to provide a more reliable assignment of these emissions to where they actually
occur,, The results of multiplying the MOBILES evaporative emissions estimates
times the respective traffic volumes indicates that freeway evaporative emissions
in the area are 43% of arterial evaporative emissions., Therefore, the reassign-
ment of evaporative emissions was accomplished by zeroing out the freeway
evaporative emissions and increasing the arterial evaporative emissions by 43%,
Two further adjustments were made that are not reflected in MOBILES- The first
adjustment only affects evaporative emissions. Based on a paper prepared by
UoSo EPA Office of Mobile Source staff, it appears that whereas MOBILES uses a
single miles per day figure and a single trip per day figure for all vehicle
ages in converting from emissions per day to emissions per mi1e9 the use of
model year by model year conversion factors yields a higher gram per mile
emission factor. Based on information derived from the Office of Mobile Source
paper, all evaporative emissions estimates were increased by 28%, The second
adjustment only affects exhaust emissions. Limited work by John Sigsby et al,
at U,S, EPA's Mobile Source Characterization Branch found that exhaust emission
measurements made with the usual, unheated sampling train measured only 77% as
much VOC as a parallel heated sampling train. Therefore, all exhaust emissions
estimates here were divided by 0,77%, i.e., increased by 30%, It must be noted
that these adjustments do not reflect U,S. EPA policy, and especially the
exhaust emissions adjustments is based on a sparse and possibly unrepresentative
data base. Nevertheless, given the uncertainties that exist throughout this
inventory, these adjustments were considered appropriate for use in this study.
The results of the above adjustments may most easily be described in terms of
emissions factors. The unadjusted, MOBILE? based emission estimate translates
to ,833 tons per year per 1000 daily vehicle miles traveled (tpy/1000 miles),
(This is approximately 2,35 g/mile). The various conversions using MOBILES and
adjustments yielded an arterial exhaust emission factor of 1,122 tpy/1000 miles,
an arterial evaporative emission factor of ,878 tpy/1000 miles, and a freeway
(exhaust only) emission factor of ,432 tpy/1000 miles.
The second area of emphasis in the mobile source inventory is species fractions.
The species fractions derived in this study are summarized in Table 4, The
source of the greatest number of species fractions were taken from a paper by
Roy Zweidinger, et al, of U.S. EPA's Mobile Source Characterization Branch
reporting concentration measurements of numerous compounds and of total VOC
near a limited access roadway near Raleigh, North Carolina (reference M,l)0
This paper provided the data for the species fractions for formaldehyde, ethylene,
toluene, xylene and acetone. Since the gas chromatographic method could not
distinguish butadiene from butane, a butadiene species fraction was also derived
from this paper using the butane data in conjunction with an assumption (suggested
by John Sigsby, reference M.6) that 10% of the material reported to be butane is
in fact butadiene. Species fractions for benzene for exhaust emissions and for
evaporative emissions were based on empirical formulae derived by Office of
Mobile Source staff from existing testing data. The input to the calculation
-------
15
x-s*
of fractions used here include national average gasoline benzene content (1.34%)
and aromatic content (3&5/0 and an approximate North Central annual average
reid vapor pressure (12,6).
Ethylene dlbromide fractions were calculated from results reported by John
Sigsby et al. in a separate paper focussing on ethylene dihromide. For exhaust
emissions, the average ratio of EDB emissions to total exhaust hydrocarbon (HC)
emissions is 117,4 ug EDC/g HC, However, because gasoline EDB content is
proportional to lead content and lead content has declined, this figure must be
adjustedo The lead content of Sigsby's fuel was 1,98 g/gallon. The actual
1984 lead content data are derived from a Motor Vehicle Manufacturers Association
survey, indicating that the average lead content of 1984 leaded gasoline was
Io07 g/gallon and indicating that leaded gasoline was 42.6% of total sales.
Assuming that emissions are proportional to gasoline sales (i.e., more pollu-
ting cars also consume more gasoline), these data indicate a 1984 EDB species
fraction of 2701 ug EDB per gram of gasoline vehicle exhaust HC emissions.,
The local percentages of gasoline vehicles exhaust to total vehicles exhaust
for arterials and freeways was then used to derive the species fractions shown
on Table 50
For evaporative emissions, Sigsby et al reported a best fit equation that EDB
evaporative emissions in ug/mile = 42 + (48 x HC emission g/mil). This
equation reflects FTP operation, so an emission factor for Chicago vehicles
operated as in the FTP was input into this equation. The result was adjusted
for lead content the same way the exhaust species fraction was. The result was
17.1 ug EDB per gram evaporative HC emissions. Since diesel fuel results in
minimal evaporative emissions, no adjustment from gasoline evaporation to total
evaporation was necessary,
Sigsby et al. also measured for but did not find any ethylene dichloride in
either their exhaust or their evaporative emissions. Therefore, zero species
fractions were used for this pollutant.
The final step in deriving Illinois emissions estimates was to determine the
spatial distribution. The most recent and applicable data available for this
purpose are 1985 VMT projections made in 1977. However, despite how long ago
these projections were made, these data should be reasonably accurate for indi-
cating the spatial distribution of emissions.
In Indiana, the 1982 ozone SIP provided direct estimates of emissions by
traffic zones. Nevertheless, most of the same adjustments made in the Illinois
inventory were also necessary in the Indiana inventory. The SIP provided
summer and and winter emissions estimates for 1980 and 1987, so SIP data on
monthly traffic volumes was used to estimate annual emissions totals. A county
total 1984 emissions estimate was derived by logarithmic interpolation between
1980 and 1987 totals, and the ratio of the 1984 to the 1980 county totals was
calculated for use in converting 1980 emissions data to 1984 estimates. For
arterials. Northwest Indiana vehicle operating characteristics were assumed to
be similar to those in the southern Chicago area, so the same conversions and
disaggregations from MOBILE2 total emissions to MOBILES arterial exhaust and
evaporative emissions were used. For freeways, where the vehicle mix includes
-------
Table 5. Highway vehicle species fractions
Species Fraction (in %)
Pollutant Exhaust Evaporative
Benzene 3.14% 1.09%
Butadiene .0345% 0
Ethylene dibromide .OOZ5%/.0018%* .0017%
Formaldehyde .763% 0
Ethylene 7.15% 0
Toluene 6.59% 6.3--;
Xylene 5.84% 3.8
Acetone .072% 0
Benzo(a)Pyrene .040%/.061%* 0
* Separate figures are for arterial/freeway exhaust emissions. The differences
result from the differences in vehicle mix.
-------
17
-<
more trucks, a separate Northwest Indiana conversion factor was calculated with
the Indiana vehicle mix, translating to an emission factor of .652 tpy/1000
daily miles,, The same adjustments as in Illinois were made to reflect possible
undermsasuremant of exhaust emissions and undercalculation of evaporative
emissions., Finally, all of the same species fractions were used in Indiana as
were used in Illinois.
Hastewater Volatilization Inventory Methods
National concern has arisen about volatile organics dissolved in wastewater but
then volatilizing into the atmosphere. This volatilization can occur during
aeration and during other processing- at sewage treatment plants, during transit
through the sewer system, and during "pretreatment" of company treatment
facilities. Unfortunately, methods for assessing the extent to which volatili-
zation rather than biodegradation or transference into sludge and for assessing
losses within the sewers and at industrial pretreatment facilities are highly
uncertain,, Therefore, no attempt was made here to quantify the effect of these
factors.
The basis of the emissions estimates derived in thJlSLJAjJidj^Ar^jiiMSMrements i of
wastewater concentrations made at f5k-Sgisi^u^ft_Jx£aJungja^_^lajL£s7 The~Southea=sT=='
Chicago source area includes two major sewage treatment plants, both of which
have substantial industrial input: the Calumet plant, and the Hest-Southwest
(Stickney) plant. At both plants, a special set of measurements of a broad set
of organics were taken on seven consecutive days at each of these plants.
Measurements were simultaneously made of the same organics not just in the
incoming wastewater but also in the sludge and the treated effluent.
Unfortunately, the mixing and variable retention times inherent in the treatment
process mean that a given influent measurement cannot be directly compared to any
single effluent measurement. Nevertheless, calculations were made to assess
whether the quantities in the sludge and the treated effluent for each compound
were. a substantial fraction of the quantities in the inluent.
*$•
To estimate emissions, the conservative assumption was made that all of the
volatile contaminants coming into these plants actually volatilize. Thus,
emissions were calculated as simply the product of the wastewater concentration
for each pollutant times the volume of wastewater treated.
This study only includes emissions at the sewage treatment plant. An employee
of the Metropolitan Sanitary District indicated there is little if any indus-
trial pretreatment, and in any case there was no information available to
estimate any emissions. A more serious omission is the absence of any estimate
of emissions out sewer system openings. These emissions may he close to zero
or may be on the same order of magnitude as emissions of material reaching the
sewage treatment plant. However, no estimate was attempted here, because any
estimate would be highly speculative.
Some wastewater treatment plants use chlorine to disinfect the incoming material.
This leads to some formation of chloroform, which may be presumed ultimately to
volatilize. However, an employee of the relevant Metropolitan Sanitary District
stated that these plants^ dojnf norfnrm rhiojdLaatJjgg. so none of this source of
chloroform was assumed. (Note, however, that the area source inventory assumes
that the drinking water is chlorinated and therefore releases chloroform.)
-------
18
Inventory Methods for Hazardous Haste Treatment Storage and Disposal Facilities^
Emission estimates for this source category are being developed hy a contractor
and have not yet been completed. Although the facilities have been identified,
the methods to be used have not yet been selected. Emission estimates for this
category will be included in the inventory as soon as they are available.
Summary of Results
A summary of the emissions from all categories of emissions is provided in
Table 6. This table shows emissions estimates for each of the 40 compounds
found in this inventory. One column in this table shows totals of point source
emissions estimates, one column shows area source totals, one column shows
highway vehicle totals, one column shows total emissions from the two wastewater
treatment plants. Estimates of emissions from hazardous waste treatment storage
and disposal facilities are not yet available,, A final column on this table
shows total emissions from all facility types in the Southeast Chicago source
area.
Following Table 6 are several tables showing the emissions estimates for the
various source types. A summary of area source emissions is shown in Table 7.
This table shows the estimates of total emissions of each species for each
source category within the full Southeast Chicago source as well as the por-
tions of this total within each county. For reference, this table also shows
what population in the Southeast Chicago source area resides within each county,
what the percentages of these populations these are of the respective total
county populations, and what percentage of the 2,361.474 Southeast Chicago
source area residents live in each county. These data illustrate that even
though barely a third of Cook County is within the source area, this county
still dominates the overall source area. By comparison, the receptor area has
395,969 people. Thus, while the receptor area has about 8% of the area in the
source area, it has 16.5% of the total source area's population.
Table 8 shows similar information for highway vehicle emissions as Table 7
shows for area source emissions. Table 9 shows emissions from the two waste-
water treatment plants.
Following Table 9 are four tables representing the point source inventory.
Table 10 shows emissions estimates for those 29 facilities to whom question-
naires were sent. Table 11 shows coke oven emissions estimates from the four
facilities in the area with operating coke oven batteries. These emissions
estimates are taken from a draft background information document for a proposed
coke oven NESHAP, based on questionnaires sent to these firms as part of the
NESHAP development. Table 12 shows emissions estimates for organic species for
the other 59 facilities present on the NEDS. Table 13 shows emissions esti-
mates for metals for these other facilities that are estimated to have such
emissions.
One special entry in Table 13, next to the entry for Commonwealth Edison's State
Line plant, is an estimate of polycyclic organic matter from this facility.
Although this table is the most convenient location in this report to place
this emission estimate, this estimate was in fact estimated by special methods.
Specifically, this emission estimate was derived from reference P.5 on fuel use
at this plant multiplied times an emission factor taken from reference P.4.
-------
Table 6. .Summary of Emissions from all Source Types
Pollutant
Benzene
Methylene chloride
Perchloroethylene
Trichloroethylene
Chloroform
Formaldehyde
Vinyl chloride
Vinylidene chloride
Ethylene
Ethylene dichloride
Ethylene dibromide
Butadiene
Ethylene oxide
Methyl chloride
Benzyl chloride
Styrene
Gasoline vapors
Toluene
Xylene
Acetone
Arsenic
Cadmi urn
Chromium
Mercury
Nickel
"Heavy POM"
Total POM
Coke oven emissions
Diethanolamine
Epichlorohydrin
Propylene oxide
Acrylonitrile
Pentachlorophenol
Acrylamide
Ethyl acrylate
Mel amine
Carbon tetrachloride
Nitrobenzene
Titanium dioxide
PCRs
Beryllium
Point
Area Mobile
STP
Total
4860.0
7.6
171.0
10.2
.8
29.6
.1
568.8
.2
12.2
16.1
.3
.05
4.2
1972.1
836.3
522.8
21.2
19.8
105.9
3.8
6.5
.01
.01
740.9
.07
.1
.6
10.5
.003
.03
.4
.3
.8
.4
.3
.04
.001
43.9 1113.4 2.0
1490.3 23.6
1126.2 16.4
401.4 5.2
34.2 2.0
, 122.4 229.5
.03
2137.7
2.0
1.0
91.3
12.3
12.0 .2
3.7
6.6
5221.8 20396.5
372.6 2977.6 18.9
70.1 2343.6 43.3
21.4 507.3
1.3
16.3
12.3 12.8
18.6 12.8
6019.3
1521.5
1313.6
416.8
37.0
381.5
.1
.03
2706.5
2.2
1.0
103.5
28.4
12.5
3.8
10.8
25618.3
5341.2
3293.3
1051.5
21.2
19.8
107.2
3.8
22.8
25.3
31.4
740.9
.07
.1
.6
10.5
.003
.03
.4
.3
.8
.4
.3
.04
.001
-------
Table 7. Area Source Emissions Totals
Category
Pollutant
emissions (tons/year)
Total Cook DuPage Will Lake. In.
Gasoline
Marketing
Ship 4 Barge
Transfer
Degreasing
Architectural
sfc. coating
Aerosol cans
Paint stripping
Dry cleaning
Misc. products
Drinking water
Heating
(except wood
stoves)
Wood stoves
Chrome plating
Hospital
steri 1 izing
Comfort cooling
benzene
toluene
xylene
gasoline vapors
benzene
toluene
xylene
perchl oroethyl ene
trichloroethylene
methylene chloride
benzene
methyl chloride
methylene chloride
toluene
xylene
methylene chloride
methylene chloride
perchl oroethyl ene
formaldehyde
chloroform
formaldehyde
nickel
chromium
"Heavy POM"
Total POM
"Heavy POM"
Total POM
chromium
ethylene oxide
chromi urn
32.9
33.4
9.4
5221.8
3.0
3.1
.9
242.2
401.4
295.4
8.0
12.0
150.2
338.8
60.6
590.3
454.4
884.0
56.7
34.2
65.7
16.3
.143
3.4
3.4
9.1
15.2
.7
12.3
.46
30.1
30.5
8.6
4771.6
1.4
1.4
.4
194.2
332.4
277.8
6.7
10.1
126.3
284.8
51.0
502.2
364.7
714.7
48.2
29.1
54.3
10.8
.09
2.2
2.2
7.8
13.0
.7
10.4
.39
.2
.2
.05
30.8
0
0
0
1.2
2.3
2.0
.04
.06
.7
1.6
.3
12.5
9.8
21.8
1.2
0.7
1.0
.2
.002"
.04
.04
.1
.2
0
.6
.01
1.4
1.5
.4
230.0
.1
.1
.04
3.1
4.7
3.3
' .2
.3
3.4
7.7
1.4
15.4
9.4
15.1
1.5
.9
1.1
.2
.002
.05
.05
.2
.3
0
0
.01
1.2
1.2
.3
189.4
1.5
1.5
.4
43.7
62.1
12.2
1.1
1.6
19.8
44.7
8.0
60.2
70.5
132.4
5.8
3.5
9.2
5.0
.047
1.1
1.1
1.0
1.7
0
1.3
.05
-------
Table 8. Highway Vehicle Emissions Totals (in tons/year)
Pollutant
Benzene
Butadiene
Gasoline vapors
Ethylene
Formaldehyde
Ethylene dibromide
Polycyclic organics
Toluene
Xylene
Acetone
Arterial Exhaust
823.fi
80.0
1871.7
201.2
.7
10.5
1731.4
1520.8
18.7
Freeway Exhaust
llfi.7
11 2
1 A • L.
266 0
(,\J*J * \J
28 3
c. \J • J
.07
2 3
c. • «s
240.2
214.5
?_7
Evaporative
173.1
onooc c
cUjyo. b
.3
1006.1
608.3
Total
1113.4
01 7
71 . O
on o rt £ c
20396. 5
°1 07 7
c 1 J/ . /
OOQ C
£.£.? * 5
1.0
1 O Q
1C . O
2977.6
2343.6
91 A
-------
Table 9. Wastewater Treatment Plant Emissions Estimates
Pol Jutant
Benzene
Methylene chloride
Perchloroethylene
Trichloroethylene
Chloroform
Vinylidene chloride
Ethylene dichloride
Methyl chloride
Styrene
Chlorobenzene
Toluene
Xylene
Acetone
Calumet
1.7
3.3*
1.4
.8
.7*
.03
.4
.2
4.6
.7
12.0
8.7
301.0
West-Southwest
.3
20.3*
15.0*
4.4*
1.3*
1.6
2.0
3.0*
6.9
34.6
206.3
*Because contaminant quantities in the treated effluent are a significant
fraction of the quantities in the raw influent (suggesting limited
volatilization), these amounts represent the difference between influent
and effluent quantities.
-------
Table 10. Emissions Estimates for Facilities Receiving Questionnaires
Nalco Chemical
Methyl chloride
Benzyl chloride
Diethanolami ne
Epichlorohydrin
Formaldehyde
Pentachlorophenol
PMC
Desoto
Titanium dioxide
Acrylamide
Ethylacrylate
Mel amine
Propylene oxide
Styrene
Formaldehyde
Toluene
Xylene
.0016 tpy
.048
.065
.10
.278
.003
.20 tpy
.025
.375
.25
.075
1.95
.080 "
2.7
2.1
Formaldehyde
Toluene
.0015 tpy
Stolt Terminals
Perchloroethylene
Tri chloroethylene
Methylene Chloride
Benzene
Toluene
Xylene
Acetone
Clark
Oil
Benzene
MORECO (Formerly Motor Oil Refining)
Arsenic
Beryllium
Cadmi urn
Chromium
Nickel
Benzene
Carbon Tet.
Chloroform
Methylene Chloride
Nitrobenzene
PCB
Trichloroethylene
Toluene
.047 Ib/yr.
.0011
.18
.32
.015
!.3
.77
.77
.77
.41
.039
.77
McKesson Chemical
Trichloroethylene
Perchloroethylene
Toluene
Xylene
Acetone
Union Oi1
Benzene
Amoco
Benzene
Toluene
Conoco
Benzene
1.73 tpy
6.55
5.68
1.09
3.09
1.45
1.17
15. tpy
2.9 tpy
2.0
7.2
5.7
6.8
3.59 tpy
.39 tpy
1.6
.09 tpy
18.
Koppers
Styrene
.83 tpy
Marbon Div./Anderson Devel.
Styrene .19 tpy
Butadiene 8.75
Keil
Shell
Ford Motor
Benzene .06 tpy
Methylene Chloride 1.
Perchloroethylene 1.
Toluene 70.1
Xylene 165.8
Acetone 1.6
Sherwin Williams
Titanium Dioxide .06 tpy
Chromium .001
Toluene 2.31
Xylene 1.347
Acetone .07
Emissions were estimated to be zero for
F.ttiylene Dichloride .004 tpy
Benzene
.88 tpy
Stauffer, IN'
Perchloroethylene .010 tpy
Methylene Chloride .113
Trumbul
3 M
Si gnode
Dynagel
Getty
Stauffer
Asphalt
Invite
Diamond Shamrock
PVS
Unichema (formerly Darling)
Mobil Chemical
Texaco
-------
Table 11. Emissions from coking operations
L (All data in tons per year)
Coke Ovens*
Byproduct Plants
Interlake
LTV Steel
(Chicago)
Inland Steel
U.S. Steel
"Coke oven emissions"
68.61 tpy
23. 27 .
406.14
242.83
Benzene
474.4 tpy
225.8
1303.4
2666.8
Toluene
75.2 tpy
35.8
206.8
423.0
Xylene
26.2
12.5
71.9
147.1
Total
740.85 tons/year
4670.4 tpy 740.8 tpy
257.7 tpy
*These are total emissions of "coke oven emissions" (benzene soluble organics)
that are emitted from charging and l*aks at the coke ovens.
-------
•A»L= 1*. PC:NT SOURCE EMTSSIQNS ESTIMATES BASED
:N ORGANIC SPECIES FRACTIONS
1-*:
154?
1T4C
1540
174C
1*40
1?4C
1T4T
1?4C
154C
174C
1*4?
1'4C
1'4-
1740
154?
1-4C
154C
PLTI OLANT NCME
i «H*R:C«N HETBL OECQR
: Vtf: L3'8 CONTAINERS
5 M " 'iiTH PBPER cc
6 1ILE3 LAEC5ATORIES -
e
ir
11
i:
if
:c
24
3*
42
r4
5P
61
69
PC
el
87
PC
94
98
IOC
117
ETH 136UT HCHO
CcMISSICNS IN TONS/TEAR)
ACE CTC PR.O ACN MCL
EDC PERC VCL XYL BENZ TOL STTR
'7'r TMiri'AL CAN CCHP
C:TN PKOPUCTS-ARSO P
r-a*X TjPNINALS COPP.
-• U H*CTPIC SPECIAL
CHTCSO: ^INISHEO MET
C"TrN CIL t CHEM CC
:BLUHPT *TE?L CCMPAN
CH'CAGC HEIGHTS BAR
"HI-ALL CAP MFG cc PL
BI'CC ?TL CC - CHICA
IWfiN GG^OCN CO
BLLIED TUEE t CONOUI
*?*c?s - ELS
M-TALS cc
. INC. 9IVE
CB"AVELLr MD30 PRCDU
•E'RTPCLTTAN
P32C
FTO
10
CHCMTCAL CO
5»rCRA*T CCPP. OF AM
U * *T£(FL - 1CUTM WC
TN-E-LAKI: - CHICAGO
LTV STEEL CCNPANT IN
CH'CAGC ?rT«%PINT
CA-CTLL !HC - CCNHOO
A*-?:CAN CAN CO
9LrC G'AVURF INC
NA'TCNAL CAN COPP
PHTEM HFG.CS.
MEfO °ACIC AGING
LARE-RTVcR TERMINALS
lOrRC AMERICAN GRAPH
NA'IINAL CAN CORP -
UH'CN CHEMICALS 3IV.
CO - MILL COUNTY
C PIPELINE co c
.0
11.8
1.8
2«.l
.2
5.8
1.4
.0
.0
.0
.0
9.7
.0
.0
.0
.0
.0
3.8
.0
.0
2.S
.0
.0
.2
79.3
.0
.0
.0
.0
.0
5.8
.0
.0
2.1
.0
.1
.0
.0
2.8
.2
.0
.0
.0
.0
.4
.0
.0
.0
.0
.0
.0
.0
.2
.0
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, .0
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.0
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.0
.0
.0
.2
.2
.0
.0
.3
.1
.0
.0
.3
.0
.0
.0
.0
2.3
.0
.0
.1
.6
.0
.9
.1
.1
.0
4.2
6.S
.2
.0
.1
.0
.0
.0
.0
.0
.1
.0
.0
.2
2.6
.0
70.7
27.3
10.3
.0
.0
.0
.2
6.9
27.9
12.6
7.5
.0
10.3
13.5
.0
.0
40.1
124.'
.0
3.6
15.6
.0
.3
10.9
1.4
4.8
.0
.3
21.9
.0
22.8
2.0
1.0
24.4
1.7
.3
11.7
25.4
.0
.0
.0
.0
.c
.0
.0
.0
.0
.0
.0
.0
.0
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.0
.0
.0
.0
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.0
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9. T
.0
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.0
5.6
27.9
12.6
6.1
.0
.0
13.5
.0
.0
40.1
10.1
.0
.0
.0
.0
.0
8.9
.0
.0
.0
.0
.0
.0
.0
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.0
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11.7
16.2
.0
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. .0
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.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
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17.4
50.0
3.»
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11.4
.0
.8
.0
11.2
5.0
.0
..o
6.6
5.4
22.9
.0
16.0
111.3
.0
5.1
28.5
.0
6.2
.0
.0
.0
.0
.0
.0
.0
16.5
.0
5.5
22.4
.0
1.9
4.7
12.. 8
.2
8.2
12.7
.0
.0
.0
17.4
2.1
.0
.0
1.6
.0
.0
1.9
7.0
.0
.0
4.1
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.0
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.0
.2
.0
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1.1
2.6
.0
.9
.0
.0
.0
.0
.0
.0
.0
.0
.0
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.0
.0
1.3
.0
2.4
43.0
123.4
4.3
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8.2
.0
?.*
5.8
11.2
5.0
6.5
.3
5.2
5.4
16.5
.1
16.0
262.4
.0
12.8
70.5
.2
4.5
9.2
21.5
.5
.0
.0
327.6
.0
1S.1
29.8
4.4
35.4
25.3
1.5
4.7
11.5
.5
5.7
9.2
.0
.0
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. 0
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.0
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.0
.0
.0
-.0
.a
.4
..0
.0
-------
PLANT NAME
ETH 13BUT HCHO
(EMISSIONS IN TONS/TEAR)
ACE ETC PR.O ACN NCL
EOC PCRC VCL XrL BENZ TOL STfR
336?
:-»«r
2?*?
2*60
11-
127
::i
rcc
crcF 650 H
a*" PIP?LINF ST JOHN
NI-SC7 ?rAN H NITCHE
U.'.STfEL C •:AN»
~L~M KN7X COUNOR» AN
-a-- CM: tir.r HUN re t*1
r • -"'jc^T nr N510U9
rNLflfJl S'?TL INDIANA
TNLAN1 S'TCL INCIANA
LTV -TTPL crrpANt
US'CN CAi"BIOc C?»P L
U»<*ON TANK CAR CCMPA
.0
.3
.0
.3
108.3
7.8
.0
.0
.0
.0
.0
39.1
4.3
93.9
112.7
50.*
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
1.7
1.2
.0
.0
.0
.0
.3
.7
.0
.4
.0
.2
1.2
.2
.0
1.4
.0
.4
.0
l.B
2.5
.1
.2
.0
.0
.0
.0
.0
3.9
.0
.0
.1
.0
.7
.0
.0
.0
.0
1.4
.0
.0
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.0
.0
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.0
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.9
.0
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.0
.0
.0
.0
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.0
.3
.c
.0
.0
.0
.0
.0
.0
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.0
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.0
.0
.0
.0
.0
.6
.0
.0
.0
.0
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.0
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.0
.0
.0
.0
.2
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
.0
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3.9
.0
.0
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.0
.0
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.0
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.1
.0
.0
• .a
.0
.0
.0
.0
2.1
.0
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1.6
.0
2.3
.0
4.7
.2
.0
.3
.0
4.2
.0
.0
.0
.0
.0
.0
.3
.5
.0
.1
.0
.1
.6
.0
34.6
2.0
47.8
34. 5
2.2
.0
.1
.0
.0
1.3
.2
.7
1.6
.0
l.S
.1
3.4
.6
(.0
.8
2.4
4.5
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.0
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.a
.0
C--- 5-? 'LAN'S)
E'H
568.842
HCHO
29.218
ETO
1.610
ACN
1.050
EOC
.176
VCL
.210
BENZ
167.085
SMR
1.190
139UT ACE PR.O
3.480 513.189 .490
NCL PERC XTL TOL'
.315 166.287 402.238 1125.369
- ETHTLEN?
=*0
ACN
rrc
VCL
9"NZ
ETHTLENS OXIDE
ACPTLONITRILE
=THTLCNE DICMLOPIOE
VINYL CHLORIDE
- STTREN5
13BUT- 1.3-SUTftOrENE
ACE - ACET3NE
PR.C - PPOPrLENE OXIDE
MCL - METHtL CHLORIDE
PERC - PEP.CHLOROETHYLENE
XTL - XTLENE
TOL - TOLUENE
-------
'fiFLc 1?. STINT
S3U»C: EMISSION
^ MATTER
ESTIMATES EASED ON
SPECIES
CN-Y
NT NIHr
AS
EMISSIONS IN
NI
HG
1'4C
1S4C
1T4C
lt4C
1540
154?
1-4"
Mtr^^PC - ~L"
6TLS-L:>«5 "L
?, IMC. -IVE
? S^'LL SIL CCMFANY ,
i! ::~N 9-
:i :ALUME
1540 to srrs^ai
154? 44 VJLCAN
f 4 IS
5? Sr
ce "C-eLrMEAC LIME CC
-I "i"«LEVEAE LIME CC
"3 it * *TeeL ~ SCUTW U ^
"? H-f-LaKS - CHICAGC
?: L*V STEEL CCMCANY IN
1G6 Cir!?r?3 INC
ICE *5?KET7 ENGIMEE»ING
154" 11- LAfE-PTVER -cPMINALS
154? 1Z1 VA'ICHAL CA»1 CCPP -
8?2C 21 ??f «D - HILL CCUNTY
236? 11" MI"SCC CEAN H MITCHE
2?*C 120 U. '.STCEL CCC-P. C-A~Y
2260 :iO ?:H"CMH=AL~H EDISCN«
2360 ?C5 tLtU KNCX FCUNOPY AN
216C ::s sa?* CHICAGC MUNICI?
2~^v ?16 INLAV? -TE=L INDIANA
2?.*~ ?1* :NLA'!3 STEEL INCIANA
236C ?lc
.CGI
.000
.013
.011
.053
.OOC
.582
• C02
.030
.000
.335
2.239
1.962
.929
.54-"
.000
.OOC
.5 1C
.135
1.175
6.S99
.633
.012
.004
.014
.261
1.035
2.784
.OOC
.3CO
.302
.011
.CCS
.COO
.581
.COO
.000
.000
.309
3.2?3
1.962
.929
.547
.000
.OOC
.053
.014
1.175
6.63?
.065
.OC1
• CC&
.083
.261
.954
2. 784
.004
.OCl
.017
.044
.C49
.030
2.453
.014
.009
.02E
1.488
17.646
1S.6C4
5.C70
2.980
.003
.002
.475
.125
6.396
35.972
.589
.069
.018
.026
1.166
5.228
15.059
.081
.016
.012
.000
.036
.000
.115
.263
.000
.COO
2.984
.125
.097
.000
.000
.049
.032
.352
.093
.000
.266
.436
1.265
.OOC
.010
.000
.066
.093
.OOC
.OOC
.00(
.001
.OOC
.00<
.00
,00(
.00
.00(
.001
.001
.001
.00)
.00
.00
.001
.00
.00
.00
.00
.00
.00
.00
3.33
.00
.00
.00
Ȥ ^ r*
L J.C
'LAN* NftME
EKISSICNS IN
AS en CR
H6
21.144 19.612 105.564
6.479
3.83)
J? =STIMATPD TC EMIT .012 TCNS/YEA* pen
C3 - CAOMIUK
HG - MERCURY
-------
28
so*
Discussion of Results u
The most important question that can be addressed with the results reported in
Tables 6 to 13 is what source types contribute most significantly to emissions
of air toxicants in the Southeast Chicago area. The first place to look for
this kind of information is Table 6, This table shows the contribution from
each general kind of source toward the emissions of each pollutant. Obviously,
the relative contribution from each kind of source varies for different
pollutantSo For example, benzene, ethylene, and toluene are about equally
emitted by point and mobile sources,, Methylene chloride, perch!oroethylene,
and trichloroethylene, on the other hand, are emitted predominantly by area
sourceso Formaldehyde and acetone, much of which come from combustion, are about
equally emitted by area and mobile sources. The metal species are predominately
emitted by point sources. Butadiene is estimated to be emitted almost entirely
by point sources. Sewage treatment plants lead to almost half of the area
chloroform emissions, but emit less than three percent of any of the other
compounds inventoried.
The other tables show more detailed information about particular sources or
source types that contribute to those various pollutant emissions- For benzene,
the major fraction of benzene emissions from point sources comes from steel
mills (coking operations), and about three quarters of the mobile source benzene
emissions come from exhaust emissions on arterials. Methylene chloride is
emitted in similar quanties from aerosol can usage and paint stripping.
Perchloroethylene emissions mostly arise from dry cleaning but also arise in
significant quantity from degreasing. Trichloroethylene emissions are almost
exclusively from degreasing. Formaldehyde emissions are mostly from combustion
by automobiles and by furnaces used in space heating, though an estimated 10%
arises from volatilization out of assorted consumer products. Ethylene is
emitted predominantly by steel mills and by automobiles. About half the
butadiene is emitted by an oil-fired utility power plant and the other half is
emitted by the steel mills. Steel mills are also the dominant source of
chromium, arsenic, and cadmium.
Another way of analyzing the point source inventory is shown in Table 140 This
table summarizes the point source emissions of each organic pollutant by standard
classification code (SCC). Note that this table only includes emissions from
facilities to which no questionnaire was sent, since the questionnaire responses
did not identify SCC's for each set of pollutant emissions.
Perhaps the best means of judging the relative importance of emissions of
different compounds from different source categories is to compare the health
risks posed by each set of emissions. This comparison, however, requires a
dispersion analysis of the exposure to the area's residents from these emissions
and then a risk assessment using dose-response data for each compound to translate
exposure into risk. A thorough dispersion analysis is planned but has not been
completed, and many of the dose-response relationships are subject to question0
Indeed it must be highlighted that many of the compounds may not in fact be
carcinogens, notwithstanding the availability of an estimate of carcinogenicity
per unit concentration. Thus, a review of the emissions data and available
dose-response data provide only a qualitative comparison of the relative
importance of different pollutants.
-------
TAELF :*. POINT £OURC? EMISSIONS ESTIMATES SORTED B»
STANDARD CLASSIFICATION CODE CSCC)
sec
VCC *
A. 3RGANICS
ETM. 13 BUT FORM ACETONE ETO
PRO
ACN CHCL3 EDC PBRC VINTLCL XTL. BENZENE TOL SffR.
10100231
1C100202
10100203
10I0022?
101C06G1
K20020:
102CC?0*
102COIC1
10200r?l
1G2C0511
io:co;o2
moon*
102007?7
1C5-T106
20:0020;
•>Cl0?p(»
3130CEJ3
30300-5C1
303007M
30700933
•»C??09?4
105C169*
1090019S
•30199<9S
?SOCC*"9
193CC691;
19090702
40250101
4CC00201
4C230S01
40200P01
40200610
40290?C1
4
-------
«/>:'%:*:x
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4C:M?:?
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4C?-n<;?<)
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4'!s.'3co
54.000
17.000
2C1.0?C
37.010
2.000
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4*. CIO
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72.770
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l.COC
:i7. .0
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vcc :*
:TM.
FC«M CCETONF ETC PRC ACN CHCLS EDC PERC VINUCL KTL. BENZENE TOL srru.
T'BL
1-6-7.«4i "«e.E 3.' 29.2 513.2 1.6
1.0
.2 166.3 .2 402.2 167.1 1125.4 1.2
nrr:
F'H
:rC
- ?THTLENE
- cC«JHetO =
- -TMTLENr CKIOE
- FTHTLENE CICHLOPIDE
- VINYL CHLOBIOE
13EUT- 1,3-BUTADTENE
ACE - ACET3NE
PR.C - PBOPflENE OXIDE
HCL - HETHfL CMLCPICE
PERC - PERCHLPRCETHYtENE
XYL - XYLESE
TOL - TCLUSN?
-------
NICK-L
10I032ri
10103232
1010C2C3
10130222
102302C2
102*0204
1C2334C1
1C2CC404
13230501
?033C?<31
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-------
32
^
One finding from a review of emissions and dose-response data is ironically and
unfortunately that the compounds that appear most significant are associated
with sme of the greatest uncertainties. Polycyclic organic matter may be the
largest contributor to area risk, but is clearly one of the most uncertain
estimates in the inventory. This "pollutant" is actually a class of compounds
with widely varying toxicities, and measurement of emission factors for this
spectrum of compounds is difficult and has been done only a small number of
times for any given source category. Emissions of polycyclic organic matter,
which emanate mostly as products of incomplete combustion, are estimated to be
emitted in similar quantities from residential wood combustion (including
wood stoves and fireplaces) and from highway vehicles, with a smaller contribu-
tion from other home heating and only a minor contribution from point sources.
A second compound that may contribute significantly to the total risk is chromium.
An important uncertainty here relates to the different valence states of chro-
mium, each of which has different level of toxicity. Unfortunately, while
for the two major area sources all emissions are the most toxic form (Cr*6),
for the largest source of chromium (steel furnaces) there is little basis for
estimating the distribution among valence states. For this inventory, these
emissions were conservatively estimated to he all the most toxic form.
Other pollutants that may make significant contributions to the total risk
include coke oven emissions, arsenic, formaldehyde, benzene, and butadiene.
Note that photochemical formation of formaldehyde, which may contribute an
order of magnitude more than direct emissions, was not included in this study.
There is also significant uncertainty on the most appropriate estimate of the
human carcinogencity of formaldehyde.
As implied by the above discussion, area and mobile sources may contribute most
of the risk, but point sources also contribute significantly to the total risk.
Wastewater treatment plants appear to contribute only a very small fraction of
the total risk. Note that emissions estimates are not yet available for
hazardous waste treatment storage and disposal facilities, and so no estimate
can yet be made of their contrbution to the total risk. Once again, however,
a more quantitative evaluation of the relative risks caused by various source
types and various pollutants must await the full dispersion and risk assessment
that is planned.
As mentioned previously, for point sources that were sent questionnaires,
emission estimates were also made using the species fraction approach. This
may be viewed as providing quality assurance for the methods used here. The
questionnaire results were shown in Table 10. The results of the species
fraction approach for organics is shown on Table 15 and for particulate species
is shown in Table 16. The sum of questionnaire emission estimates for each
compound from the relevant companies is also shown on Table 15 and 16 to facili-
tate comparison of the results. Note that only 15 of the facilities to whom
questionnaires show up on Tables 15 and 16, since these tables are based on
updated NEDS data in which many of the smaller facilities (including several
chemical plants) have been discarded.
-------
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-------
35
x*^
The results in Tables island 16 indicate that total emissions according to
questionnaire responses in general were found to he substantially lower than
total emissions estimates using the species fraction approach., In some cases,
the difference was dramatic: species fractions were higher than questionnaire
totals for benzene by a factor of 16, for styrene by a factor of 25, and for
formaldehyde by a factor of 566, Also, the species fraction approach estimated
some emissions of several compounds which were not found in the questionnaires,
including ethylene oxide, propylene oxide, acrylonitrile, and vinyl chloride.
In other cases, the species fraction totals were only moderately higher than
questionnaire totals, such as for toluene (a factor of 6) and xylene (a factor
of 2,6), or even lower (for cadmium the species fraction total was 2 times
lower than questionnaire totals), IR yet other cases, however, some relatively
common chemicals, specifically methylene chloride and trichloroethylene were
not estimated to occur using the species fraction approach but were found in
the questionnaire responses. Further, it is not surprising that relatively
esoteric compounds such as diethanolamine and epichlorohydrin were found with
questionnaires and were not found with species fraction approach.
In order to make an overall comparison among the multiple compounds, it is
useful to make a qualitative review that considers dose-response relationships
as well as emissions. This review suggests that overall the species fraction
approach leads to a substantially higher estimate of risk than questionnaire
responses.
The results as just discussed by the questions of why the differences arise and
what kinds of sources have the greatest differences. In general, differences
between the two sets of results may arise either from differences in total
emissions estimates (i.e., total VOC or TSP) or from differences in species
fractions. Unfortunately, the questionnaire did not ask for total emissions
estimates, so it is difficult to distinguish these two origins of discrepancies.
Nevertheless, some enlightenment comes from looking in detail at three types of
sources: chemical plants, refineries, and miscellaneous manufacturing operations.
Chemical plants exhibited the most dramatic between species fraction results
and questionnaire results. For these facilities, the species fraction approach
appears to rely on a national mix of chemical production,. The result, not
surprisingly, bears little resemblence to the chemicals produced and emitted in
the Southeast Chicago area. It is these facilities which were estimated to but
have been affirmed not to emit ethylene oxide, propylene oxide, acrylonitrile,
and vinyl chloride. On the other hand, these facilities did emit non-zero
quantities of butadiene, fliethanolamine, epichlorohydrin, for which the species
fraction approach estimated little or no emissions.
The second source type, refineries, generally requested U,S, EPA assistance
particularly in estimating species fractions. Thus, regardless of the actual
accuracy of the species fraction used, any discrepancy between species fraction
results and "questionnaire results" is caused by a discrepancy in total VOC
estimates. For example, for the Texaco refinery, the species fraction approach
estimated substantial emissions whereas the questionnaire response indicated
that the facility had largely shut down. It is interesting to note further
that the species fraction approach predicted substantial refinery emissions of
chromium, from combustion of chromium-containing oil for heating. This is
illustrative of the possibility in some cases that the species fraction approach
may find substantial emissions which are not suspected by the sources themselves,
-------
36
;*•
The third source type, miscellaneous manufacturing operations, sometimes shows
surprisingly good correspondence between species fraction results and question-
naire results and sometimes shows firms estimating zero emissions where species
fractions indicate substantial emissions. It is possible in some of these
latter cases that the firms use solvents for example that are mixtures which,
unknown to the firms, contain the compounds of interest.
In summary, the species fraction approach often given reasonable screening
estimates of emissions, but the results sometimes differ substantially from the
emissions estimates made by the firms themselves. Particularly for chemical
plants, the use of national default species fraction cannot be expected to pre-
dict what chemicals are used at local facilities. For other facilities, however,
the species fraction are generally at least comparable to source estimates, and
in fact the species fraction may in some cases be more accurate than the source's
own estimation of its emissions mix. In some cases, inaccuracies were a result
of inaccurate VOC/TSP emissions data in NEDS. In general, though, in the
context that this inventory is intended as a screeening inventory, the species
fraction approach appears to give reasonably reliable emissions estimates for
this purpose.
General Observations
Substantial interest has arisen in the urban air toxics problem. The inventory
described in this report is part of a unique project to assess one urban air
toxics "hotspot". It is anticipated that this inventory will facilitate the
development of other, similar urban area inventories. Therefore, it is
appropriate to discuss the process of inventory development and make other
comments that might he useful to other groups developing similar inventories
for other areas.
Given the goal of compiling a comprehensive inventory, this inventory necessarily
relied heavily on information available in the literature. Even for the point
source portion of the inventory, resource constaints led to sending direct
questionnaires to only 29 out of 88 facilities. For the other 59 sources,
emissions estimates for VOC and TSP were available as part of NEDS. By neces-
sity, literature information, particularly information from the VOC Species
Data Manual and the Receptor Model Source Composition Library, were used to
assess the toxic compound components of these VOC and TSP emissions estimates.
Fortunately, the above two references provide relatively complete information
on point source species fractions. Unfortunately, species fractions for area
source categories were much more difficult to obtain. For the point source
inventory, the inventory appears to be relatively complete, and the principal
question is the accuracy of the available estimates. For area sources, there
is more of a question as to the completeness of the inventory. That is, it is
more evident in the area source inventory than in the point source inventory
that the ability to inventory emissions is limited by the availability of
information with which to make estimates.
-------
37
x«*
For mobile sources, substantial literature review was necessary as part of this
project, but the result~appears to be a fairly complete and seemingly relatively
reliable inventory,, For wastewater volatilization, the inventory appears
relatively complete (with the notable exception that emissions out of sewers
are not estimated), though the assumption of 100% volatilization and the
reliance on a handful of influent samples leads to questions about reliability.
For treatment, storage and disposal facilities, the estimates here, despite
being the best available estimates, must be considered highly uncertain, due to
uncertainties in waste composition, waste quantities, propensities to volatilize,
and the insurmountable difficulties of addressing "special waste" landfills and
unauthorized landfills.
Part of the process of developing the inventory was developing a plan for
compiling the inventory. This was a useful endeavor, since it helped in defining
the source area and the compounds to inventory, and helped in organizing what
source types warranted investigation. At the same time, it must be noted that
much of the character of the inventory development process was a function of
what information was available in the literature. Thus, for example, the
inventory includes methylene chloride emissions from its use in aerosol cans
and does not include butadiene from oil-fired home heating, simply because ,,
emissions factor data were available for the one category and not for the
other. As a result, a major portion of the work in compiling this inventory
was performing literature review, exploratory work which could not be antici-
pated in the work plan.
Regarding the literature which was found useful, this report includes a complete
bibliography of literature used in this study. The VOC Species Data Manual and
the Receptor Model Source Composition Library have already been identified as
key data sources for addressing point sources. Most of the literature used in
the mobile source inventory was obtained from U.S. EPA's Mobile Source
Characterization Branch of the Atmospheric Sciences Research Library in Research
Triangle Park, North Carolina, based on considerable work they have performed
on the subject.* The literature for area source categories was more diverse,
including literature focussing on per capita emissions (based on national
consumer VOC usage), literature focussing on particular categories such as wood
stove emissions, as well as literature from a few broad-based inventory efforts.
The wastewater volatilization estimates did not rely on any literature data.
One other series of documents which were reviewed was the documents known as
"locator documents" (e.g., "Locating and Estimating Air Emissions from Sources
of Formaldehyde"). However, these documents did not lead to very many of the
emissions estimates used in this study. This is partly because most of the
facility types described in these documents are not present in the Southeast
Chicago source area. This is also partly because many of the emission factors
provided in these documents rely on information that is not readily available.
For example, the chromium locator document provides an estimate of the quantity
of chromium emissions per quantity of chrome-containing refractory brick, but
the available information on the brick production does not differentiate the
various kinds of brick refractories. Thus, the locator documents, while
providing some information useful in this study, more often seems oriented
toward focussed investigations of individual sources or source types than
toward general inventories.
-------
38
s*
One surprising aspect of^ the process of completing this inventory was thp effort
associated with the questionnaires. Numerous companies misplaced the question-
naire,, For some companies, plant personnel were unable to process the question-
naire, and we had to send another copy of the .questionnaire to company head-
quarters. We attached to each questionnaire the NEDS information on the company,
thinking this would simplify their response, since the companies could just
confirm the accuracy of NEDS. This was a mistake: companies felt obliged to
have accurate information on every detail on NEDS, and often needed information
to decipher which point of their facility corresponded to which point on NEDS.
Finally, substantial follow-up work was necessary, particularly where responses
appeared incomplete or where companies did not know the composition of the
materials they processed.
This report would not be complete without discussion of needs for further
investigation0 The goal of this project was to obtain a comprehensive inven-
tory of air toxics emissions, so almost by definition any element of the
inventory could be improved through further investigation., Nevertheless, it
is possible to identify specific elements of the inventory for which further
investigation would particularly improve the overall inventory. Perhaps the
most important need identified in this study is the need for improvement of
point source species fractions. Part of an investigation of this issue would
be a more detailed investigation of the cause of the discrepancy found here
between species fraction-based emission estimates and questionnaire responses,
which would presumably help identified means of improving the reliability of
the species fractions. Even apart from this investigation, it is clear that
significant improvement to the inventory could be obtained by performing a
broader set of species fraction measurements and doing the collateral work of
assessing which operations (e.g., hy SCC) can be characterized with which sets
of species fractions. A second important need is the development of more area
source emission fractors (e.g., metals from electroplating and butadiene from
home heating) and improvement of existing area source factors (e.g., benzene
fractions for various portions of the petroleum/gasoline marketing chain and
the composition of coatings used in house painting and auto refinishing),
A third important need is to improve emissions estimates for polycyclic organic
matter, as emitted by highway vehicles, by wood stove use,'and by other heating
uses. Relatively few measurements have been made of the relevant emission
factors. Also, for wood stoves, there are significant uncertainties in wood
usage in the urban setting of Southeast Chicago area, and there are significant
undertainties about the impact of differences between actual and laboratory
stove operating characteristics on emissions. In addition, since this is not a
single compound but rather a complex mixture of compounds, any assessment of
the biological toxicity of the emissions would benefit from a more thorough
understanding of the composition of the emissions. Fourth, some studies have
indicated that formaldehyde formation from photochemical reactions can cause
greater exposure than direct formaldehyde emissions and in fact can represent a
major component of ambient toxicity. No effort was made to assess photochemical
formaldehyde formation in Southeast Chicago. A need exists for a simple method.
-------
39
x-**
using methods such as correlations with monitored ozone or photochemical box.
modeling, which could approximate photochemical formaldehyde formation without
requiring long-term formaldehyde monitoring. Fifth, a number of improvements
could be made in the inventory of emissions from treatment, storage, and disposal
facilities, both in the estimation of waste quantities of particular compounds
and in the estimation of the degree of volatilization. Although the emissions
from these source types are relatively small, the public interest in this
general category translates to an interest in these improvements.
Other needs for further investigation exist in the other source types. For
mobile sources, the adjustments, particularly the adjustment to reflect the
possibility that standard measurement techniques may only measure 77% of total
exhaust, warrant further investigation. For wastewater volatilization, further
investigation could address volatilization from sewers, collection of a more
robust set of influent samples, and refinement of the fraction of influent that
volatilizes.
Another set of further investigations represent a broadening of the emission
investigation. One such broadening is to include emissions of compounds with
non-cancer health impacts. Note that the impacts of such compounds are often a
function of short-term average concentrations, and so such an emissions inventory
would probably have to address peak short-term average emission rates. A second
such broadening would be to assess the impact of potential emissions controls,
such as the ozone control program, the total suspended particulate program, or
such strategies as a focussed permit review program.
This report describes the completion of a project to estimate emissions of a
broad list of potential air toxicants in the Southeast Chicago area. At the
same time, this report signals the beginning of a modeling assessment of
population exposure to these pollutants. It is also hoped that this report
will facilitate the beginning of other projects in other urban areas to assess
emissions of potential air toxicants.
-------
RiM iography
information on Illinois and Indiana emissions/activity
T.I. National Fmissions r»ata System (NFDS) - a computer data hasp maintained by
M.S. FPA containing data on point sources (including npprat.ing character-
istics and emissions of criteria pollutants as obtained hy State AgenciesU
1. 2. 1QR? Ozone STP Rpvisions hy minois and Tndiana for thp Chicago/Northwest
Indiana Area - a collective term for numprous suhmittals most relevantly
including a vnr. emissions -inventory. These suhmittals were the primary
hasis for area and mobile source county emissions totals and for various
characteristics affecting mobile sourcp emissions. Three specific references
included in the SIP are:
T.3. P.M. Sellars, A.M. Kiddie, I. .A. Raci , R..1. Rosy, R.n. Green, Oevelopment of
the Area Sourcp Fmissions Tnvpntory for the 1QR? Ozonp State Implementation
Plan for thp Thicago Metropolitan Rpgi on of Illinois and Indiana. RCA Corp.,
'
1. 4. "IQfl? State Implementation Plan Suhmittal for Northeastern Illinois," Chicago
Area Transportation Study, ,1unp ?df 1QR7. fThis is the highway vphiclp
emissions inventory in Illinois' 1QR? ozone plan for Chicago.)
T.S. "Mohile Source ^missions Inventory for Lake and Porter Counties, Indiana,"
Rernardin, l.ochmueller K Associates, September 1QR?.
T.fi. Rridded Illinois socio-economic data - a computer file containing gridded •
socioeconomic data (p.g., arterial and freeway VMT and manufacturing
employment) for use in spatially distributing area and mohile source emissions.
1. 7. 1QRO Census of Population - Illinois (PC(l)-AlR) and Tndiana (PCM)-Alfi) -
contains maps of the urbanized arpa and population data.
i.R. Cpnsus data - comput.prizpd population and dwelling unit data at the hlock
group level were taken from Rureau of Census data stored on the Graphical
Exposure Modeling Systems (GFMS).
T.I, Wastewater Concentration data - data were obtained ^rom the Greater Chicago
Metropolitan Sanitary ni strict, in letters fPrank nait.nn to Charles Sutfin)
dated npcemher 17, iQRfi, and April 7, 19R7.
T.in. Hazardous waste handling data - extensive state data on the quantities of
each waste code generated, treated, stored or disposed hy each facility
were obtained from TFoa and TPIFM. (This report does not document final
emission estimates for this category, however.^
1. 11.. "Fst.1mat.es of M.S. Wood Fnergy Consumption from 1.Q7Q to IQfll" (np,F/FTA 0341),
Fnergy Information Administration, nepartment of Fnergy - provided state
by state estimates of wood usage per household. (The authors used these
data as cited in separate references.
T.I?. "Inventory of Health rare Facilities and Need net.ermi nation by Planning
Arpa", Illinois nepartment of Public Health - provided data on local hospitals.
-------
Point_ Source References
P.I. Volatile_0rgarn_c_Cornpou_nH_J_VOC_)_^pecj_es_pata_Mamjal, Office of Air Quality
Planning" and Standards", USEPA". EPA Report * EPA-4"50/4-80-015. July 1980 -
contains 174 profiles and 134 organic species, including 19 species from
this study.
P.?. Compiling Air Toxics Emissions Inventories, Office of Air Duality Planning
and Standards. EPA Report #450/4-86-OOfi, June ] 98fi - contains an index
of which species profiles to use for which standard Classification Code
(SCC), and contains a variety of other useful types of information.
P.3. Receptor Model Source Composition Library. Office of Air Quality Planning
and Standard's", EPA Report # EPA-450/4-85-00?. November 1984 - covers
roughly 80 SCC's and 30 metals, including 6 metals in this study (arsenic.
beryllium, cadmium, chromium, mercury and nickel).
P.4. "Locator documents" e.g.. Locating and Estimating Air-Emissions From Sources
of forma_l_d_e_hy_de_. EPA Report"* EPA-450/4-84-007e, March 1984 - TTeri¥s of
documents providing emission factor data and, for source types with a modest
number of facilities, source location. Such documents are available for:
a. Acrylonitrile (EPA-450/4-84-007a)
h. Carbon Tetrachloride ( " -007b)
c. Chloroform ( " -007c)
d. Ethylene Dichloride ( " -007d)
e. Formaldehyde ( " -007e)
f. Nickel ( " - -007f)
g. Chromium ( " -007g)
h. Manganese ( " -007h)
i. Phosgene ( " -007i ^
j. Epichlorohydrin ( " -007j)
k. Vinylidene chloride ( " -007k)
At time of report preparation, draft "locator documents" were also avail-
able for chlorohenzenes. ethylene oxide, polychlorinated Mphenyls, and
polycyclic organic matter. For a great majority of these pollutants,
these reports indicated a probable absence of major point sources. How-
ever, the Southeast Chicago area does contain sources for which species
fractions and emission fractions could be derived based on the locator
documents for chromium, nickel, formaldehyde, and polycyclic organic
matter.
P.5. Steam Electric Plant Factors, 198?, National Coal Association - provided
heat content ~data for »ariou"s fuels, e.g., RTU/1000 gallons oil. (This
study used Commonwealth Edison fuel data). These data were used to convert
emissions factors from units of emissions/heat content (e.g., g/Joule) to
units of emissions/quantity fuel (e.g., g/1000 gallons oil).
P. fi. C o k e_ Oven Emiss i o rvs_ fr om Wet-Coal Ch a r geoMSy -Product C ok e Oven Ra tteries —
Ba c k g'r ou n d In forma t i o n~ for P ro p o s ed St a n d a rd s, Draft F.fsTOAOPS. "August 1986.
P. 7. Benzene Emi s s i o n s _frpm Cqk_e Ry-Product Recovery P_1_ant_s _--_ Background
Information for"P'roposed" Standards. Draft Ffs. OAQPS, TPA Report *4"5'n/3-83-01fia.
-------
Area Source References
A.I. W.H. Lamason, "Technical Discussion of Per Capita Emission Estimates for
Several Area Sources of Volatile Organic Compounds", paper presented at
Air Pollution Control Association meeting, June 21-26, 1981 - this is the
fundamental source for most of the per capita emission factors.
A.2. End Use of Solvents Containing Volatile Organic Compounds, The Research
Corporation of Hew England (for OAQPS, USEPA), FPA Report f EPA-450/3-79-032,
May 1979 - provides additional information for calculating per capita emission
factors.
A.3 Improvement of the Emissions Inventory for Reactive Organic Gases and Oxides of
Nitrogen In the South Coast Air Basin. Systems Applications, Inc.. and Radian
Corporation (for Calfornia Air Resources Board), May 1985 - provided species
profiles for gasoline marketing, architectural surface coating (see especially
the main text chapter on "species profile development" and Appendix E).
A.4. "Locator documents" - see reference data and description urlder point source
references. Specific documents from which area source emissions factors
were used included the formaldehyde, chloroform, chromium, nickel and
draft polycyclic organic matter locator documents.
A.5. Hazardous Air Pollutants: Air Exposure and Preliminary Risk Appraisal for
15 U.S. Counties, Appendix E. "Area Source Emission Factor Documentation."
Versar, Inc. and American Management Systems, September 1984 - although
the documentation is scant and the reliability of the data are uncertain,
this report provides useful species profiles for rtegreasing: other profiles
here were superseded by other references.
A.6. Steam Electric Plant Factors - see reference data under point source
references. Again, fuel heat content were used to convert from emissions
per Joule to; emissions/quantity fuel burned.
A.7. Estimates of U.S. Wood Energy Consumption, 1949-1981, by Applied Management
Sciences for Dept. of Energy - supplied Illinois wood usage estimates.
A.8. Residential Energy Consumption Survey: Consumption and Expenditures April
1982 through March 1983, Energy Information Agency (Oept. of Energy) -
supplied regional wood usage information used to adjust from statewide to
urban wood usage,
A.9. R.L. Gay, W.T. Greene, J.J. Smith, "A National Assessment of Residential
Wood Combustion Air Pollution Impacts," Nero and Associates, March 15,
1985 - showed U.S. Dept. of Agriculture wood usage estimates.
A.10. Survey of Methylene Chloride Emission Sources, USEPA Report #450/3-85-015,
June 1985 - References A.10, A.11, and A. 12 document national emission
estimates and procedures underlying county estimates for degreasing emis-
sions of these compounds.
-------
A.11. Survey of Perchloroethylene Emission Sources, U.S. EPA Report #450/3-85-017,
June 1985 - see note under A.10. Also supplied similar information for dry
cleaning.
A.12. Survey of Trichloroethylene Emission Sources, U.S. EPA Report #450/3-85-021,
June 1985 - see note on A.10.
A.13. Chromium Emissions from Comfort Cooling Towers - Background Information for
Proposed Standards (Draft EIS), Office of Air Quality Planning and Standards,
March 1987 - provided per capita emission factors used to derive a per
"other" (nonmanufacturing; nonretail) employee emission factor.
j
A.14. Phone conversation with OAQPS staff (Al Vervaert), October 30, 1986 -
provided data for crude emissions estimates for chrome plating.
Mobile Source References
M.I. R.B. Zweidinger, J.E. Sigsby, Jr., S.B. Tejada, F.D. Stump, D.L. Dropkin,
W.D. Ray, and J. W. Duncan, "Detailed Hydrocarbon and Aldehyde Mobile Source
Emissions from Roadway Studies," Environmental Sciences Research Laboratory -
provided the majority of exhaust emission fractions.
M.2. J.E. Sigsby, Jr., S.B. Tejada, W.D. Ray, J.M. Lang, and J.M. Duncan, "Volatile
Organic Compound Emissions from 46 In-use Passenger Cars," Environmental
Sciences Research Laboratory - provided evaporative emission fractions,
and documented the possibility of unheated sampling trains under-measuring
exhaust emissions.
M.3. J.E. Sigsby, Jr., D.L. Dropkin, R.L. Bradow, J.M. Lang, "Automotive Emissions
of Ethylene Dibromide," Environmental Sciences Research Laboratory, presented
at Passenger Car Meeting, Troy, Michigan, June 7-10, 1982 - provided exhaust
and evaporative emissions data for ethylene dibromide, and documented absence
of ethylene dichloride.
M.4. Conversations with staff of Office of Mobile Sources staff - provided data
for estimating exhaust and evaporative emissions fractions for benezene.
M.S. User's Guide to MOBILES (Mobile Source Emissions Model) - MOBILES provided
data on total highway vehicle emissions factors and the components of the
total from each vehicle type.
M.6. Personal communication from John Sigsby to author (comments on draft report)
dated January 30, 1987 -- reports that butadiene has been found to be between
5 and 20% of n-butane.
Uastewater Volatilization References
Apart from local wastewater concentration data, no references were used,
since simplying assumption of 100% volatilization was used.
-------
Illinois Environmental Protection Agency 2200 Churchill Road, Springfield, IL 62706
14. 1
MoasrcJi Uaatrjr Co.
140 Kast Ilia Street
Catcaft. llltatls
fitttloata:
Tht Illtatts CM aad USEPA art ••!•§•< ta a ctaatrattft tffort ta caaatla aa
lavtatary of atr aslftsfoaa of salacttd saastaatat fa /Mr araa. At aatatrKad
by tat mtatts Cavtroaaaatal Prefect!** Act aad ta* federal Cloaa Air Act. M
arc coat111 of tfels ln»«ot»ry s* Out M CM «SMSS antd^U* kMltft favacts
o* tat rvsfaims of tlw Santftiast CMcaf* art*. F«r Qrpts «f laaixat an
bdM iaelidcd 1a ttff fnforaatlo* fatterlaf tfftrU 1*tf1w1a»a)
M*afacturliig/>rDCc«sia9 factlUf**, *arM M«rcu* (stcft AS §a*»1lM *t*tf
and dry cIcaMrt). '•oftflt sacrccs*
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Illinois Environmental Protection Agency 2200 Churchill Road. Springfield. IL 62
Paft.2
III* total 3 1s a •vtstlattalro »»1cft Idtttfflts otfttr iaftrattloa Baadad. I
atttrtl. this ajtastloMuIrt stats atrtsslots astlnstts far each oparatlot U
>ttr facility for oocft of tftt llstod cttjoutds mlcft yoo tajr aarft. and sat*
atdltional itforaatiot htlpful it asttMttf tftt possibility of attBSpftarlc
rtltasts. Plaast fill att a «Mft1otMlrt tar aacft optratlot ar prodtctlot
11M It yotr facility as idottlflod (tr as should bo idtttlflta) It
Attachment 2.
Atucfttttt 4 rtojuasts additional Information at sncttdary air atJlssloas
ratvltltf frat platt opt rat loot Itmlvtitj •tsttvattr. Hajgld vastas. aad soli
vast**.
wu that la tJ» afe«€aca of tftt rtajmt** 1«f«mat1o«. aartwl
your facility «<11 b* tstiMtcd Mi«d MI tat fOC a* T» aan»slo« oo protrld* sftMlo: bo Uft
coafldMtU). plaaso frorlda Jastlflcation ««d looatlfjr tfta lafotvotlaa) yo»
wlcft kapt cMfldontlal at tfto t1«a jra« lotorit It. IlllMts EFA will folio*
tfto procoduras 91*011 IB tfto Stato of I1l1a0fs Rftlos tod RafMlat1«m. Tltlo -K
Chapter II: Part U1 for ftanillof roojMtU far coafldoatlalitjr. «a* WSCFA wl
Fallont to ass*
to tfto ptftllc
•Itftoot furtftor attic*.
dllaf
follow tfto procrtoros fllvaa 1o 40 Cfl Soct1o« 2.100 at m.
a cUioi «f co«f1de«tl«Mty •okas tfto lofomatloft avaTTaFlo
Pltast svbsrtt tftt ranoastad lafomatloa by Santanter 30. 1!
tht USCPA's copy to Ntrrlat Crota (SAft.2ft). USCPA, 230 S. Dtarbort. OUcaoo,
IL 60604. If ytt Htuld I1kt additional itfomatian rt«ard1tf tftt
quastlotnairt or tftt projact it atntral. ploast call Joan Sftrnck of tf staff
1217/782-1 CM) or Jtbt SttBtrhays (312yOt*-4047) or Or. Htrrlnt Crtte
(312/353-UJ09) tf tftt USCPA Itflot V off lea. Ut «otld also bt happy to shar
vita you. at rtnjttst. a dtscrlptlot tf tftt plat for estimating missions of
otfttr sa«ircts and sovrca typos 1o tftt arta. Ut art loocltf forward to yntr
coottratlan It this off art.
Sltctrcly.
• f y. ' r~'
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i protection Agency 2200 Churchill Road, Springfiel
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N E 0 5 POINT
STATEdO: ILLINOIS
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Illinois Environmental Protection Agency 2200 Churchill Road. Springfield, IL 62706
ATTACWCMT 3 "
A. Mtottf/ to* c*o«tc«1 listed ea Attocfem A *ricfe 1s oso* or cr*otod ojr
orocosft/storcgo/tflspoul ooorotloo*.
wlssfea strMM (stKk. ^roc«ss. f«fU1v«. st»r«ft tmk.
pi MM prorl^t tUt f«11ow1iif UfpfMtlM o« tft* s*t«t tf
for tftt 19ti c«l«no«r jr««r.
htlffet frs« irwno.
«MUr of «1 sitoa potot
For oac* cDovfcol s«asu>c« ioootlflotf IB port A «*1cft ts In tirts •
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Tooo/Tr
Mot oir pollotio* cootrol «rt In ploco.for Uls eorfsstoo ttr*m
Control Cfiovlcal IOBBVOI tfffcloncjr
(AtUCtBMt 1)
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Illinois Environmental Protection Agency 2200 Churchill Road, Springfield, IL 62706
ATTAOMBft 3
ttt I** C4lft»4«r /«*r 41* /•• Mft aty tMKtw«il*4 rtlMMS
Qf 4% Of titt S«tatMCM iatrt1fft« 11 Hit A?
for ttcn SMCH str»a» associate nit* aa •Mch«*jrit4 roloatt 11st for u» total
coltntfar ytar
loapmind fpMJtttr «•*«•« 10 air
1a attactMrit 1)
VS
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Illinois Environmental Protection Agency 2200 Churchill Road. Springfield. IL 6270
mission OF POTHTUUT raxc SIBSTAMCCS
Socoafer? oaltstoaa «rt taaaa air oatfsafaaa rtsaltlag froa taa trtataant
•r ilsaasal of vastaaatar 11«i14 «MtM «r WH4 vaftUs. F*r t«cJ»
•r ilsaasal of vastaaatar,
prvctss Mitt rtnMB «to1cli cMttlw tn» or aon tMlc
fey f 1111 •§ <• tl» Uftlc toltm If uapll* 4au an
• test ntlMtt f«r tacfc M
•oat or *1saa*al aattood (if aartloaa of taa stroaa ara
traataavaiaposod of 41fforaatljr aaacrtaa aataats aaaorataly far oaca taalc
T«U1 «Dlo« of
Total v»1«» of )1ojHid wosto
Tatal voMaw of offlaaat 41scaaraaa to sawr tystaa aal par da/.
Saaataaca Total % af Sakstaaea Ptaar Traataaat/
itloa Svaataaca Wacaaraod to Bfaaaaal of
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