United States Air and Radiation EPA420-D-99-002a
Environmental Protection March 1999
Agency
&EPA Estimation of Motor Vehicle
Toxic Emissions and
Exposure in
Selected Urban Areas
Volume I
DRAFT
> Printed on Recycled Paper
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EPA420-D-99-002a
March 1999
of
in
I
DRAFT
Assessment and Modeling Division
Office of Mobile Sources
U.S. Environmental Protection Agency
Prepared for EPA by
Sierra Research, Inc.
Radian International Corporation
Energy and Environmental Analysis, Inc
EPA Contract No. 68-C7-0051
Work Assignment No. 0-07
NOTICE
This technical, report does not necessarily represent final EPA decisions or positions.
It is intended to present technical analysis of issues using data which are currently available.
The purpose in the release of such reports is to facilitate the exchange of
technical information and to inform the public of technical developments which
may form the basis for a final EPA decision, position, or regulatory action.
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Estimation of Motor Vehicle Toxic Emissions
and Exposure in Selected Urban Areas
Volume I
Table of Contents
page
1. Summary 1
Modeled Areas and Control Scenarios 1
Methodology 2
Results 4
2. Introduction 10
Background 10
Project Scope 10
Organization of the Report 12
3. TOG and CO Modeling Methodology 14
TOG Emissions 16
CO Emissions 23
4. Toxics Emissions Modeling Methodology 29
Exhaust Emissions 29
Evaporative Emissions 47
Diesel Particulate Emissions 48
5. Development of Area-Specific Model Inputs 50
Specific MOBILE Inputs for This Study 50
Area-Specific Toxic-TOG Curves 57
Area-Specific Evaporative Benzene and MTBE Fractions 61
Input File Development 61
PARTS Input Files 61
6. Motor Vehicle Toxics Emissions Estimates 63
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Table of Contents, continued
7. Toxics Exposure Estimates .
page
. 71
1990 CO Exposure Estimates 71
CO Emissions Estimates 73
Reactivity and VMT Adjustments 74
Modeled Urban Area Toxics Exposure Estimates 77
Risk Assessment 87
9. References
89
Appendix A Revised TOG and CO Inputs Used in the MOBILE Emissions Modeling
Appendix B Methodology to Account for Normal/High Emitter Distributions in
T2AATOX
Appendix C Equations Used to Generate Toxics Fractions for Non-Complex Model
Vehicles
Appendix D EPA's Suggested Methodology to Determine Toxics Fuel Effects from the
Complex Model
Appendix E Model-Year-Specific Technology Fractions
Appendix F Evaluation of CARB UC-FTP Database
Appendix G Summary of T2ATTOX Code Changes to Implement Revised Toxics
Emissions Estimation Procedures and Description of Model Function
Appendix H Sample Toxic-TOG "Curves" for 1990 Phoenix Summertime Fuel
Appendix I Sample Evaporative Fraction Input File for 1990 Phoenix Summertime
Fuel
Appendix J Sample T2ATTOX Input File for Phoenix
Appendix K Sample T2ATTOX Output for Phoenix
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1. SUMMARY
Under Work Assignment 0-07 of U.S. Environmental Protection Agency (EPA) contract
#68-C7-0051, Sierra Research, Inc. (Sierra), in conjunction with subcontractors Radian
International Corporation (Radian) and Energy & Environmental Analysis, Inc. (EEA),
has performed a number of tasks related to the assessment of motor vehicle air toxics
emissions, exposure, and risk assessment. As described below, emissions and exposure
estimates were prepared for the following air toxics: benzene, acetaldehyde,
formaldehyde, 1,3-butadiene, MTBE, and Diesel paniculate. The analysis was performed
for nine selected urban areas in the U.S. under a variety of control scenarios. Estimates
were prepared for calendar years 1990, 1996, 2007, and 2020. Although risk estimates
were not prepared as part of this study, the modeling framework to perform those
calculations, with the unit risk factor for each toxic as a variable input, was developed.
Modeled Areas and Control Scenarios
This work assignment was carried out to support possible regulatory action required by
Section 202(1) of the Clean Air Act (as amended in 1990), which calls for EPA to
promulgate regulations containing reasonable requirements to control hazardous air
pollutants (HAPs) from motor vehicles and motor vehicle fuels. In addition, the results
may also be used to estimate cancer risk in the regulatory impact analysis for proposed
Tier 2 tailpipe emissions standards. Under this work assignment, on-road motor vehicle
air toxics emissions and exposure estimates were prepared for nine urban areas consisting
of Chicago, Denver, Houston, Minneapolis, New York City, Philadelphia, Phoenix,
Spokane, and St. Louis. Modeling was performed for 1990, 1996, 2007, and 2020, and
separate estimates were prepared for winter, spring, summer, and fall. The forecast years
include four control scenarios that were defined in consultation with EPA:
0. Baseline fuels and emission rates, assuming the implementation of a National
Low-Emission Vehicle (NLEV) program;
1. Baseline emission factors with an assumed national gasoline regulation limiting
sulfur levels to 40 ppm;
2. Scenario 1 with more stringent tailpipe hydrocarbon emission standards for light-
duty cars and trucks (i.e., reflecting possible Tier 2 standards); and
3. Scenario 2 with an assumed increase in light-duty Diesel truck implementation
equivalent to 50% of total light-duty truck sales beginning in model year 2004.
-1-
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Methodology
Emissions Estimates - The methodology used to prepare the emission estimates for this
study was similar to the approach used by EPA in its development of toxics emission
rates for the 1993 Motor Vehicle Related Air Toxics Study (MVRATS). In that
approach, the MOBILE model is used to generate total organic gas (TOG) emissions from
on-road motor vehicles by vehicle class and model year. Toxics fractions, developed as a
percentage of the toxic compound of interest contained in TOG emissions, are then
applied to the MOBILE-based TOG gram per mile (g/mi) results to arrive at toxic
emission rates in g/mi or milligrams per mile (mg/mi). The toxics fractions are
developed as a function of vehicle type (e.g., light-duty versus heavy-duty), fuel type
(gasoline versus Diesel), and technology type (e.g., non-catalyst versus catalyst).
Although there are similarities between the emissions methodology used in the 1993
MVRATS and the methodology used in this study, there are also a number of areas in
which improvements were made. These include the following.
The on-road motor vehicle TOG emission rates were based on a version of
MOBILESb that EPA recently modified for the Tier 2 Study to incorporate
updates to the model expected with the release of MOBILE6. These updates
included revised base emission rate equations, incorporation of off-cycle
emissions effects, revised fleet characteristics, and revised fuel effects.
The emissions response (both in terms of TOG and toxics) of newer technology
vehicles to changes in fuel parameters was based on an evaluation performed with
the Complex model for reformulated gasoline. This model was not available at
the time the 1993 MVRATS was completed.
Instead of applying a single toxics fraction to each technology or model year, the
emissions impacts of particular fuel formulations on late-model vehicles were
assessed separately for normal and high emitting vehicles. The approach used to
implement this methodology relied on the development of "toxic-TOG curves"
that plotted the target fuel toxic emission rate (in mg/mi) against the base fuel
TOG emission rate (in g/mi). Different toxic-TOG curves were developed for
each of the 72 fuel formulations* investigated in this study. The MOBILE model
was then revised to apply the calculated TOG emission rate to the toxic-TOG
curve to determine the corresponding toxic emission rate.
Because of the vast number of model runs required in this effort, the process was
automated as much as possible. Software was developed to create area-specific input
files and to process the model output into a format that could be easily used in the
ensuing exposure calculations.
Nine urban areas were evaluated, each having different fuel formulations in winter and summer. In
addition, three different formulations were used to reflect the 1990, 1996, and 2007/2020 baseline runs,
with a fourth used for the national 40 ppm sulfur scenario. Thus, a total of 72 different fuels (9 areas x 2
seasons x 4 fuels) were evaluated in this project.
-2-
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Exposure Estimates - Once the toxics emission rates were developed, toxics exposure was
estimated according to the following formula:
TOXExposure(Mg/m3) L^OExposure(Mg/m3)/COEF(g/mi)J1990 x TOXEF(g/mi)
where TOX reflects one of the six toxic pollutants considered in this study. Because
some of the toxic pollutants evaluated in this study (e.g., 1,3-butadiene) have a different
photochemical reactivity than CO, the exposure concentrations were adjusted to account
for atmospheric transformation. In addition, because the CO ratios are based on the 1990
calendar year, an adjustment was made to account for the increase in VMT relative to
1990. These adjustments were developed in consultation with EPA.
The 1990 CO exposure estimates above were based on recent modeling performed under
contract to EPA with the Hazardous Air Pollutant Exposure Model (HAPEM). These
estimates were provided to the study team for each of the modeled urban areas and
represent only that portion of CO exposure attributable to on-road motor vehicles.
Separate exposure estimates were provided by quarter and for three different demographic
groups: (1) total population, (2) outdoor workers, and (3) children 0 to 17 years of age.
Outdoor workers were selected because they represent the highest exposed demographic
group, while children are generally considered a very sensitive demographic group.
Similar to the toxics emissions estimates, the 1990 CO emission factors were based on a
modified version of MOBILESb that incorporated many revisions expected to be
implemented with MOBILE6. This included revised base emission rates, incorporation
of off-cycle effects, and revised oxygenated fuel effects.
The 1990 CO emission factors, toxics emission factors (all calendar years and scenarios),
and 1990 CO exposure estimates were compiled in a FORTRAN routine to generate
exposure estimates according to the formula above. Estimates are prepared according to
urban area, calendar year, season, control scenario, vehicle class, demographic group, and
toxic compound.
Risk Assessment - Although the original work plan drafted for this study included the
analysis of cancer risk, EPA requested that cancer risk estimates not be prepared at this
time because work is still underway to develop appropriate unit risk factors to assign to
each toxic. Instead, Sierra was instructed to develop a modeling methodology that would
allow EPA to input appropriate unit risk factors at a later date. This was accomplished
within the FORTRAN routine developed to calculate exposure.
Within the exposure model, estimates of individual cancer risk are calculated with the
following formula:
CANfcd = TOXExposure.Adj (tlg/m3) x (UR / YPL)
where TOXExposure.Adj (^m3) is the toxic exposure estimates adjusted for VMT growth and
atmospheric transformation; UR is the unit risk in cancer cases or deaths per person
-3-
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exposed in a lifetime to 1 |ig/m3 of the toxic compound of interest; and YPL is years per
lifetime (typically assumed to be 70 years).
To calculate the total cancer cases for the population, the individual cancer risk defined
above was simply multiplied by the population subject to the toxic compound exposure,
i.e.,
CANPop = CANtod x Population
The above calculations are carried out for each of the modeled urban areas investigated in
this study.
Results
Toxics Emissions Estimates - The results of the toxics emissions analysis are presented in
Section 6 of this report, and a summary of annual-average toxic emission rates is given in
Table 1-1 for Chicago and Phoenix. Reviewing the fleet-average toxics emission factors
in that table, the following observations can be made:
Significant reductions in fleet-average toxics emissions are observed between
1990 and 2020 with no further vehicle or fuel controls. This is a result of fleet-
turnover resulting in full implementation of the federal emission control
regulations currently on the books.
Implementation of Scenario 1 (national 40 ppm sulfur limit) has no impact on the
Phoenix runs. That is because it was assumed that Phoenix would continue to use
CARB "Cleaner Burning Gasoline" (CBG), which already has sulfur levels below
40 ppm on average.
For the Chicago runs, Scenario 1 has the largest impact on benzene and
1,3-butadiene emissions. Aldehyde emissions are less affected under this
scenario.
Because it is assumed that gasoline dispensed in Chicago will use either ETBE or
ethanol as an oxygenate, MTBE emission rates are zero for all scenarios.
Moderate reductions are observed with Scenario 2 (potential Tier 2 controls) in
2007. However, by 2020 fleet-turnover impacts result in fleet-average toxic
emission reductions on the order of 15% to 25%.
Implementation of Scenario 3 (increased light-duty Diesel truck sales) results in
reductions in benzene, acetaldehyde, 1,3-butadiene, and MTBE (where used).
However, formaldehyde emissions show a slight increase. Obviously, Diesel PM
emissions increase substantially under this scenario.
-4-
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Table 1-1
Annual Average On-Road Motor Vehicle Toxics Emission Rates
for Chicago and Phoenix
(Units: nig/mi)
Pollutant
Benzene
Acetaldehyde
Formaldehyde
1,3-Butadiene
MTBE
Diesel PM
Area
Chicago
Phoenix
Chicago
Phoenix
Chicago
Phoenix
Chicago
Phoenix
Chicago
Phoenix
Chicago
Phoenix
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Calendar Year
1990
119.7
...
134.4
...
17.9
...
16.3
...
55.2
...
...
58.9
...
...
16.5
...
...
13.7
...
...
0.0
...
...
102.7
...
...
93.5
...
...
92.9
...
1996
53.3
...
71.2
...
17.8
...
14.2
...
29.4
...
...
32.0
...
...
7.2
...
...
7.7
...
...
0.0
...
...
4.0
...
...
53.6
...
...
61.2
...
2007
24.2
23.0
21.9
19.6
16.7
16.7
16.0
14.6
7.4
7.2
6.9
6.6
3.8
3.8
3.7
3.9
13.1
13.1
12.8
13.0
13.1
13.1
12.8
13.1
3.0
2.7
2.6
2.6
2.2
2 2
2.2
2.2
0.0
0.0
0.0
0.0
48.0
48.0
47.7
41.5
23.4
23.4
23.4
38.7
23.4
23.4
23.4
38.7
2020
14.9
13.8
10.4
8.3
10.1
10.1
7.7
6.4
4.4
4.2
3.4
3.2
2.4
2.4
2.1
2.2
8.0
8.0
6.8
6.9
7.7
7.7
6.7
6.9
2.1
1.9
1.6
1.4
1.6
1.6
1.3
1.3
0.0
0.0
0.0
0.0
27.3
27.3
26.1
20.1
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
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Toxics Exposure Estimates - A summary of motor vehicle air toxics exposure is given in
Table 1-2 for Phoenix and Chicago. As with the toxic emission rate estimates, motor
vehicle air toxics exposures are projected to decrease substantially between 1990 and
2020, even without additional controls on vehicles and fuels. Although the results for all
modeled urban areas are not shown in Table 1-2, the benefits of Scenario 1, a national
gasoline rule limiting sulfur to 40 ppm, are greatest in areas that do not have a pre-
existing reformulated gasoline program such as Minneapolis. Areas with an RFG
program show more moderate decreases in motor vehicle toxics exposure, depending on
pollutant, as a result of a national gasoline sulfur limit. The more stringent light-duty
vehicle emission standards modeled in Scenario 2 in general show greater decreases in
toxics exposure than the other control scenarios modeled in this effort, particularly for the
2020 calendar year run. Finally, the increased light-duty Diesel penetration scenario
modeled in Scenario 3 results in substantial increases in Diesel particulate exposure
levels, although benzene and 1,3-butadiene exposure is decreased. It should be kept in
mind that the exposure estimates for acetaldehyde and formaldehyde do not include any
adjustments to account for atmospheric transformation.
As discussed above, exposure estimates were prepared for three different demographic
groups: total population, outdoor workers, and children 0-17 years of age. (The
estimates given in Table 1-2 are for the total population.) The exposure to air toxics for
outdoor workers is generally about 20% higher than for the total population, while
exposure for children is typically slightly below the total population. This is observed in
Table 1-3, which shows the annual-average benzene exposure for the three demographic
groups analyzed in this study for Chicago under the control scenarios described above.
As seen in the table, benzene exposure is highest for outdoor workers (which is the
highest exposed demographic group), while children and the total population show
similar levels of exposure.
Finally, Table 1-4 presents annual-average on-road motor vehicle exposure results for
benzene for all modeled urban areas. As seen in that table, areas with high benzene
exposures in 1990 include Minneapolis, New York, and Phoenix, while Houston and St.
Louis fall on the lower end of the scale. Because Minneapolis is not subject to in-use
motor vehicle control programs (i.e., inspection and maintenance; reformulated gasoline)
as stringent as those in New York, the reduction in exposure levels between 1990 and
2020 is not as great.
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Table 1-2
Annual-Average Exposure Results for Chicago and Phoenix
Total Population - All On-Road Vehicles
(Units: ug/m3)
Pollutant
Benzene
Acetaldehyde
Formaldehyde
1,3-Butadiene
MTBE
Diesel PM
Area
Chicago
Phoenix
Chicago
Phoenix
Chicago
Phoenix
Chicago
Phoenix
Chicago
Phoenix
Chicago
Phoenix
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
14.4
14.4
14.4
14.4
8.4
8.4
8.4
8.4
14.4
14.4
14.4
14.4
8.4
8.4
8.4
8.4
14.4
14.4
14.4
14.4
8.4
8.4
8.4
8.4
14.4
14.4
14.4
14.4
8.4
8.4
8.4
8.4
14.4
14.4
14.4
14.4
8.4
8.4
8.4
8.4
14.4
14.4
14.4
14.4
Calendar Year
1990
0.997
...
1.923
...
...
...
0.149
...
0.245
...
...
...
0.459
...
0.915
...
...
...
0.100
...
0.150
...
...
...
0.000
...
2.109
...
...
...
0.776
...
1.379
...
...
1996
0.567
...
1.419
...
...
...
0.189
...
0.312
...
...
...
0.312
...
0.638
...
...
...
0.057
...
0.112
...
...
...
0.000
...
0.049
...
...
...
0.566
...
1.205
...
...
2007
0.308
0.292
0.279
0.249
0.456
0.456
0.437
0.397
0.094
0.091
0.088
0.084
0.101
0.101
0.098
0.103
0.167
0.166
0.162
0.165
0.352
0.352
0.344
0.350
0.028
0.026
0.025
0.025
0.045
0.045
0.044
0.045
0.000
0.000
0.000
0.000
1.267
1.267
1.260
1.095
0.295
0.295
0.295
0.488
0.614
0.614
0.614
1.015
2020
0.235
0.218
0.164
0.131
0.378
0.378
0.288
0.236
0.069
0.066
0.054
0.050
0.086
0.086
0.076
0.080
0.126
0.125
0.107
0.109
0.281
0.281
0.244
0.253
0.025
0.022
0.018
0.016
0.044
0.044
0.036
0.034
0.000
0.000
0.000
0.000
0.994
0.994
0.950
0.731
0.273
0.273
0.273
0.647
0.631
0.631
0.631
1.495
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Also Table 7-11
Table 1-3
Annual-Average Exposure Results for Benzene in Chicago
by Demographic Group for All On-Road Motor Vehicles
(Units: ug/m3)
Demographic
Group
Total
Population
Outdoor
Workers
Children
0-17 Years
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
10.1
10.1
10.1
10.1
8.2
8.2
8.2
8.2
Calendar Year
1990
0.997
1.200
0.980
1996
0.567
0.683
0.557
2007
0.308
0.292
0.279
0.249
0.371
0.351
0.336
0.300
0.303
0.287
0.274
0.245
2020
0.235
0.218
0.164
0.131
0.283
0.262
0.197
0.158
0.231
0.214
0.161
0.129
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Table 1-4
Annual-Average Exposure Results for Benzene
Total Population - All On-Road Vehicles
(Units: ug/mS)
Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
8.1
8.1
8.1
8.1
6.9
6.9
6.9
6.9
11.3
11.3
11.3
11.3
18.0
18.0
18.0
18.0
7.8
7.8
7.8
7.8
14.4
14.4
14.4
14.4
13.6
13.6
13.6
13.6
6.0
6.0
6.0
6.0
Calendar Year
1990
0.997
...
0.922
...
0.787
...
1.923
...
2.106
...
1.071
...
1.923
...
1.492
...
0.690
...
1996
0.567
...
0.871
...
0.530
...
1.414
...
0.903
...
0.642
...
1.419
...
1.194
...
0.634
...
2007
0.308
0.292
0.279
0.249
0.526
0.470
0.452
0.403
0.328
0.314
0.303
0.272
1.055
1.035
0.995
0.859
0.527
0.503
0.482
0.430
0.290
0.273
0.261
0.232
0.456
0.456
0.437
0.397
0.682
0.600
0.577
0.511
0.302
0.289
0.276
0.246
2020
0.235
0.218
0.164
0.131
0.430
0.368
0.285
0.227
0.244
0.229
0.178
0.145
0.978
0.955
0.795
0.587
0.354
0.331
0.246
0.198
0.210
0.193
0.145
0.116
0.378
0.378
0.288
0.236
0.515
0.431
0.330
0.262
0.234
0.218
0.163
0.130
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2. INTRODUCTION
Background
The 1990 Amendments to the Clean Air Act added requirements for hazardous air
pollutants (HAPs), or air toxics. For the most part, those requirements are spelled out in
Section 112, which focuses on stationary and area sources. In addition, other sections of
the Act include provisions for air toxics. In particular, Section 202(1) contains two
requirements specific to motor vehicles:
By May 15, 1992, EPA was to complete a study of the need for, and feasibility of,
controlling emissions of toxic air pollutants associated with motor vehicles and
motor vehicle fuels. That study was to focus on the categories of emissions that
pose the greatest risk to human health (or about which significant uncertainties
remain), including benzene, formaldehyde, and 1,3-butadiene.
By May 15, 1995, EPA was to promulgate regulations containing reasonable
requirements to control HAPs from motor vehicles and motor vehicle fuels. At a
minimum, those regulations were to apply to benzene and formaldehyde.
The result of the first directive was the "Motor Vehicle-Related Air Toxics Study,"
(MVRATS) finalized by EPA in April 1993.l Although emission standards specific to air
toxics were included in the reformulated gasoline rulemaking promulgated in December
1993,2 EPA has yet to adopt HAP emissions regulations for motor vehicles required
under the second directive above. This work assignment was carried out to support
possible regulatory action required by Section 202(1). In addition, the results may also be
used to estimate cancer risk in the regulatory impact analysis for proposed Tier 2 tailpipe
emissions standards.
Project Scope
Under this work assignment, on-road motor vehicle air toxics emissions, exposure, and
cancer risk were estimated for nine urban areas consisting of Chicago, Denver, Houston,
Minneapolis, New York City, Philadelphia, Phoenix, Spokane, and St. Louis. Modeling
was performed for 1990, 1996, 2007, and 2020. The forecast years include four control
scenarios that were defined in consultation with EPA:
-10-
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0. Baseline fuels and emission rates, assuming the implementation of a National
Low-Emission Vehicle (NLEV) program;
1. Baseline emission factors with an assumed national gasoline regulation limiting
sulfur levels to 40 ppm;
2. Scenario 1 with more stringent tailpipe hydrocarbon emission standards for light-
duty cars and trucks (i.e., reflecting possible Tier 2 standards); and
3. Scenario 2 with an assumed increase in light-duty Diesel truck implementation
equivalent to 50% of total light-duty truck sales beginning in model year 2004.
The methodology used to determine motor vehicle toxics emission rates, exposure, and
cancer risk consisted of the following steps:
1. On-road motor vehicle toxic pollutant emission factors (in mg/mi) were generated
using a modified version of the MOBILESb emission factors model. That model,
known as T2ATTOX, has been revised to allow the user more flexibility to model
the impacts of off-cycle operation and fuel sulfur effects. In addition, that model
allows the user to input toxics fractions (by model year and technology) that are
applied to total organic gas (TOG) emission rates calculated by the model. This
step involved the development of TOG base emission rate equations (BERs) as
well as toxics fractions.* The toxic pollutants evaluated in this study included
benzene; formaldehyde; acetaldehyde; 1,3-butadiene; MTBE; and Diesel
particulate (which was estimated with the PARTS model). Toxic pollutant
emission rates were calculated for each of the urban areas, calendar years
(separate estimates for quarters 1 to 4), and control scenarios included in this
study.
2. On-road motor vehicle carbon monoxide (CO) g/mi emission factors were
developed for each of the urban areas included in the study using the Tier 2
Analysis Tool (T2AT). These calculations were performed for calendar year 1990
to be consistent with the CO exposure estimates described in Step 3 below.
3. CO exposure estimates (in |ig/m3) were calculated previously for the nine urban
areas included in this study for calendar year 1990. Using the CO emission
factors developed in Step 2 above, ratios of CO exposure (adjusted to reflect only
the on-road motor vehicle contribution to the inventory in each urban area) to the
CO emission factor for 1990 were developed. These ratios were prepared for the
entire population, children under 18 years of age, and outdoor workers (the
highest exposed demographic group) for quarters 1 to 4.
As described in Section 4 of this report, the final methodology developed for this project uses a slightly
different approach for estimating exhaust toxics emission rates. (See the discussion of toxic-TOG curves
in the text.)
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4. Using the toxic pollutant emission rates and the CO ratios described above,
estimates of toxic exposure were developed for each urban area, calendar year (by
quarter), and control scenario investigated in this study. These estimates were
calculated according to the following formula:
TOXExposure(Mg/m3) LCOExposure(Mg/m3)/COEF(g/mi)J1990 x TOXEF(g/mi)
where TOX reflects one of the six toxic pollutants considered in this study.
Because some of the toxic pollutants evaluated in this study (e.g., 1,3-butadiene)
have a different photochemical reactivity than CO, the exposure concentrations
were adjusted to account for atmospheric transformation. In addition, because the
CO ratios are based on the 1990 calendar year, an adjustment was made to
account for the increase in VMT relative to 1990. These adjustments were
developed in consultation with EPA.
5. Using the toxic pollutant exposure concentrations generated in Step 4, a
methodology to estimate cancer risk was developed that applies cancer potency
estimates (i.e., unit risk factors) for each toxic to the exposure estimates. Because
cancer potency estimates were not finalized for inclusion in this work assignment,
the model developed to compile the emissions and exposure data was structured
to allow the user to input alternative potency estimates. Based on these inputs, the
model calculates cancer risk for the entire population, the highest exposed
demographic group (i.e., outdoor workers), and children 0-17 years of age. Total
cancer cases for the entire population of each modeled urban area can be
estimated, and the model includes an algorithm to estimate nationwide motor
vehicle toxics exposure, cancer risk, and cancer cases.
This project was conducted by Sierra Research, Radian International, and Energy &
Environmental Analysis. Sierra served in an oversight capacity and had primary
responsibility for generating on-cycle toxics fractions, TOG base emission rate equations,
and the CO emissions estimates. In addition, Sierra was responsible for generating
exposure estimates and developing the model to estimate cancer risk. Radian was
responsible for constructing T2ATTOX and PARTS input files, modifying the model to
incorporate the methodologies developed during the course of this project, and
performing the model runs. Finally, EEA performed an analysis of off-cycle speciated
data to generate off-cycle toxics fractions.
Organization of the Report
This report is bound as two separate volumes. This volume (Volume I) contains a
description of the study, the methodologies used to generate toxic emission rate and
exposure estimates, and a summary of the results. Volume n contains detailed toxic
emission rate and exposure estimates calculated for each of the study areas, years, control
scenarios, seasons, and demographic groups evaluated in this effort.
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Immediately following this introduction, Volume I continues with Section 3, which
describes the modifications to the MOBILESb modeling methodology for calculating
TOG and CO emissions to account for a number of planned revisions for MOBILE6.
This includes revised base emission rate equations, inclusion of off-cycle emissions
impacts, revised fuel sulfur and oxygenate effects, and revised fleet characteristics.
Section 4 presents the modeling methodology used to estimate motor vehicle air toxics
emission rates. Section 5 details the specific MOBILE inputs used for the emissions
modeling performed in this study, while Section 6 summarizes the results of the toxics
emissions modeling. Section 7 explains how the emissions data were combined with
1990 CO exposure data to generate toxics exposure estimates for this study. The results
of that modeling are also briefly discussed in that section. Finally, Section 8 presents a
summary of risk assessment, and describes how the exposure model developed for this
study was structured to allow the user to input alternative unit risk factors to calculate
individual cancer risk and estimated cancer cases. A listing of the references cited in this
report is contained in Section 9.
Volume n of this study consists of only of tables that summarize the results of the
evaluation. The two primary sections of that volume are:
Modeled Urban Area Toxics Emission Estimates; and
Modeled Urban Area Toxics Exposure Estimates.
###
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3. TOG AND CO MODELING METHODOLOGY
As outlined in the previous section of this report, estimates of total organic gas (TOG)
and carbon monoxide (CO) emission rates are needed for this study. As such, EPA's
MOBILE model served as the basis of those estimates. The latest "official" version of
EPA's on-road motor vehicle emission factors model is MOBILESb, which was based on
the MOBILESa model. Although MOBILESb was released in October 1996, the changes
made to the model were minimal relative to MOBILESa, consisting primarily of
(1) revisions to account for the effect of regulations that had been finalized after the
release of MOBILESa, and (2) revisions to inspection and maintenance (I/M) program
inputs to reflect program designs being pursued by states that were not included in the
MOBILESa model. The most substantive change to CO modeling between MOBILESa
and MOBILESb was a result of including the impacts of the gasoline detergent additive
regulation in the MOBILESb model.
Most of the algorithms included in MOBILESb are based on data and analyses performed
nearly six years ago. (MOBILES was released in December 1992. That model was
updated and released as MOBILESa in March 1993 to correct errors found in the original
release of the model.) Since that time, a significant amount of data has been collected on
in-use emissions performance, vehicle operational characteristics, and the impact of fuel
parameters on emissions. Because of that, EPA is now in the process of updating
MOBILESb to reflect the latest knowledge on vehicle emissions. In fact, a modified
version of the model was developed to estimate the emissions impacts of possible Tier 2
controls. As discussed in the documentation prepared for that model,3 which is termed
the Tier 2 Analysis Tool (T2AT), the modified MOBILESb model was developed as a
"surrogate for MOBILE6," addressing four primary areas of development: (1) basic
emission rates, (2) off-cycle effects, (3) fuel effects (primarily sulfur), and (4) fleet
characteristics.*
To be consistent with the modeling performed for the Tier 2 Study, the analysis of air
toxics performed under this work assignment made use of many revisions expected to be
incorporated into MOBILE6. Although a number of the factors have been revised by
EPA since the release of the T2AT results, the same elements of the model were
addressed in the emissions estimates performed for this study. These include the
following:
EPA has also developed a toxics version of T2AT, termed T2ATTOX. The T2ATTOX model was the
basis of the emissions estimates prepared in this study.
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Base Emission Rates - The base emission rates (BERs) used in this study were
updated by EPA based on more recent test data. The revised BERs reflect much
lower deterioration rates than the current factors in MOBILESb. This shift was
directed at mid- to late-1980 model year vehicles and later. Thus, the net impact
of this change is to lower fleet average in-use emission rates for future calendar
years (i.e., the impact of fleet turnover is greater than that predicted by
MOBILESb).
Off-Cycle Effects - Concern about inconsistencies between ambient
measurements and inventory estimates led to a closer evaluation of the basis of
emission factor estimates in the late 1980s. As a result, the 1990 Clean Air Act
Amendments directed EPA to assess the magnitude of "off-cycle" emissions and
develop regulations for their control. During the early 1990s, a significant effort
to better define in-use vehicle operation was undertaken by EPA and CARB. The
result of that effort was the development of driving cycles more representative of
true vehicle operation (i.e., higher speed and acceleration). In addition,
Supplemental Federal Test Procedure (SFTP) regulations were adopted that will
control off-cycle emissions starting with the 2000 model year (2001 for NLEVs).
The net result of adding off-cycle emissions impacts is to increase emissions for
pre-SFTP vehicles, which are then decreased in future years as SFTP controls are
implemented and the fleet turns over.
Revised Fuel Effects - The impact of both gasoline sulfur and oxygen levels will
be revised in MOBILE6. The impact of gasoline sulfur levels has been found to
be more pronounced for low-emission vehicles than for older technologies (at
least on a percentage basis); thus, this analysis addresses only the impacts of fuel
sulfur on LEV-category vehicles. For oxygenated fuels, draft correction factors
have been proposed by EPA that indicate the oxygenated fuel CO benefits for
late-model vehicles are much lower than those predicted by MOBILESb. These
revised factors were incorporated into the CO estimates prepared for this study.
Revised Fleet Characteristics - Because of the high sales fraction of light-duty
trucks relative to passenger cars in the last several years, estimates of the car
versus truck VMT split are being revised for MOBILE6. Current indications are
that there will be a large shift to light trucks with MOBILE6, with the trend
continuing beyond 2010. Because of the higher per-mile emission rates of light
trucks relative to passenger cars, this shift will result in an increase in fleet-
average emissions in the future. In addition to the car/truck VMT fractions,
vehicle age distributions are being revised for MOBILE6 that will likely result in
an older vehicle fleet than currently predicted by MOBILESb. However, in the
short-term, continued use of local data is preferable. These modifications were
also incorporated into the emissions estimates prepared for this study.
Described below are the specific changes made to the MOBILE inputs to incorporate the
revisions outlined above. Note that the model used in this analysis was a toxics version
of T2AT developed by EPA called T2ATTOX. That model was provided to us by EPA
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and contained modifications to allow the estimation of motor vehicle air toxics emission
rates. Although that model was ultimately revised by the study team to streamline
calculations and modify several specific aspects of the methodology, it served as the basis
for the emissions estimates prepared for this study.
TOG Emissions
The first step in estimating toxic emission rates from on-road motor vehicles was to make
revisions to the MOBILESb TOG inputs and calculation methodology to better reflect the
anticipated structure of MOBILE6. Properly characterizing TOG emissions is important
because both exhaust and evaporative TOG emission rates serve as the basis of the toxics
emissions estimates, i.e., toxic emissions are generally estimated by assuming a certain
fraction of TOG consists of the compound of interest. For example, benzene typically
comprises 3% to 4% of light-duty gasoline vehicle exhaust TOG emissions. Thus, a
vehicle with a TOG emission rate of 1.0 gram per mile (g/mi) would be expected to emit
between 0.03 and 0.04 g/mi benzene.*
As outlined above, EPA is currently in the process of revising the MOBILE model to
better reflect current knowledge and data on in-use emissions. Although none of the
revisions planned for MOBILE6 have been finalized, it is possible to make educated
assumptions regarding the nature of those revisions. This was done during the
development of the emissions estimates for the Tier 2 Study, and EPA continues to refine
its estimates of in-use emissions. For this study, EPA provided inputs or revisions to the
following model parameters related to TOG emissions estimates:
Base emission rate equations;
Off-cycle corrections;
Fuel sulfur impacts for low-emission vehicles; and
Fleet characteristics (e.g., registration distributions).
A review of these parameters and the approach used to incorporate them into the model is
discussed below.
Base Emission Rate Equations - EPA provided the base emission rates to be used in this
study in terms of non-methane hydrocarbons (NMHC), which were subsequently
converted to a TOG basis for input to the MOBILE model. Because toxics emissions
were estimated out to 2020 in this effort, future-year emission rates were an important
element of the analysis. For this evaluation, it was assumed that a national low-emission
vehicle (NLEV) program would be implemented beginning in model year 2000 for areas
This value could actually be more or less, depending on the benzene and aromatic content of the gasoline.
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in the Ozone Transport Region (OTR) and in model year 2001 for non-OTR regions.
Four sets of baseline BERs were provided by EPA, representing various levels of control:
Non-I/M, Non-OTR NLEV implementation schedule;
I/M, Non-OTR NLEV implementation schedule;
Non-I/M, OTR NLEV implementation schedule; and
I/M, OTR NLEV implementation schedule.
In addition to the above, a separate set of BERs was provided to reflect possible Tier 2
emission standards. These factors were effective with the 2004 model year.
A summary of the revised NMHC BERs for light-duty gasoline vehicles (LDGVs), light-
duty gasoline trucks under 6,000 Ibs. gross vehicle weight rating (LDGTls), and light-
duty gasoline trucks over 6,000 Ibs. gross vehicle weight rating (LDGT2s) is contained in
Table 3-1. The BERs in that table reflect the I/M, Non-OTR emission rates. In addition,
the 2004 and later model year BERs reflect vehicles certified to proposed Tier 2
standards.
Table 3-1
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Table 3-1
Revised FTP-Based NMHC BERs Used in Emissions Analysis
I/Ma, Non-OTR NLEV Implementation
Vehicle
Class
LDGV
LDGT1
LDGT2
Model
Year
1981-82
1983-85
1986-89
1990-94
1995-2000
2001-03
2004+
1984-89
1990-94
1995-2000
2001-03
2004+
1984-89
1990-96
1997-2003
2004+
ZM
(g/mi)
0.308
0.197
0.240
0.167
0.145
0.059
0.036
0.398
0.266
0.179
0.076
0.036
0.398
0.266
0.218
0.036
DR1
(g/mi/lOK)
0.115
0.039
0.046
0.016
0.010
0.006
0.005
0.018
0.015
0.010
0.006
0.005
0.018
0.015
0.010
0.005
DR2
(g/mi/lOK)
0.162
0.107
0.034
0.019
0.010
0.009
0.088
0.039
0.021
0.011
0.009
0.088
0.039
0.025
0.009
Flex Point
(10,000 mi)
1.528
2.223
2.126
8.903
7.872
8.103
4.409
2.133
9.063
8.287
8.103
4.409
2.133
9.254
8.103
-------
Several items are worth noting with respect to the revised BERs contained in Table 3-1.
First, only 1981 and later BERs are included for LDGVs, and only 1984 and later are
included for LDGTs. That is because the earlier model year BERs did not change relative
to MOBILESb. Second, although these are I/M-based emission rates, the impact of I/M is
accounted for only in the 1995 and later model year LDGV/LDGT1 categories and the
1997 and later LDGT2s. That is because the earlier model year vehicles are corrected for
I/M effects with alternative credit files that were developed by EPA. Finally, significant
reductions in the base emission rate equations are observed in 2001 as a result of the
NLEV program, and then again in 2004 as a result of potential Tier 2 controls. Also of
note is that although the LDGT2 category is not part of the NLEV program, it was
modeled in this effort as being controlled by potential Tier 2 regulations. This becomes
important in the future as more trucks are certified in the heavier weight classes.
To put the revised BERs in perspective, they have been plotted against the MOBILESb
base emission rates in Figure 3-1. The two top lines in that figure represent non-I/M
hydrocarbon emissions for Tier 0 and Tier 1 vehicles modeled by MOBILESb. The four
bottom lines in the figure reflect the revised BERs used in this analysis. The Tier 0 and
Tier 1 rates do not include the effects of I/M, so they are directly comparable to the
MOBILESb factors.* The NLEV and Tier 2 rates do include I/M. As seen in the figure,
the revised BERs are significantly lower than the MOBILESb estimates.
In addition to making revisions to the light-duty vehicle NMHC emission rates,** BERs
for heavy-duty gasoline vehicles (HDGVs) and heavy-duty Diesel vehicles (HDDVs)
were also revised. Again, the modified rates were provided by EPA and are summarized
in Table 3-2.
A final adjustment that was made to the BER equations before formatting them for use in
the T2ATTOX model was to adjust the NMHC values to a TOG basis. (For the
calculation of air toxics, the T2ATTOX model requires alternative BERs to be input in
terms of TOG.) These adjustments were provided by EPA and are a function of vehicle
class and technology. For example, the following TOG/NMHC correction factors were
used for light-duty gasoline cars and trucks:
Non-catalyst - 1.0988
Oxidation catalyst - 1.1725
Three-way catalyst - 1.1687
Three-way + oxidation catalyst - 1.3829
Note that the MOBILESb rates are reported in terms of total HC (which included methane), while the
revised rates are in terms of NMHC. Correcting the MOBILESb results to an NMHC basis would lower
those rates, but only slightly.
At the request of EPA, light-duty Diesel cars and trucks were assigned the same NMHC emission rate as
gasoline vehicles for Tier 1 vehicles, Tier 2 vehicles, and NLEVs.
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3.5
Comparison of MOBILESb and Revised HC Base Emission Rates
Used in Analysis of Motor Vehicle Air Toxics
O
3 -
2.5
^ 2 -\
1.5 -
M5b-1992
M5b-Tier1
Tier 0(1992)
Tier 1
NLEV
Tier 2
0.5 -
0
6 8 10
Odometer (10,000 mi)
12
14
16
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Figure 3-1
Table 3-2
Revised NMHC BERs for HDGV and HDDV Vehicle Classes
Vehicle Class
HDGV
HDDV
Model Year
1994-2003
2004+
1994-2003
2004+
ZM (g/bhp-hr)
0.364
0.277
0.283
0.257
DR (g/bhp-hr/1 0,000 mi)
0.023
0.018
0.0
0.0
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These factors were used to generate model-year specific TOG/NMHC ratios by weighting
each model year by the fraction of each technology in the fleet. Those calculations were
performed by EPA and the results were submitted to Sierra in spreadsheet form. A
summary of the TOG/NMHC ratios used in this study, by model year and vehicle class, is
contained in Appendix A. In addition, the resulting BERs, in the format used by the
T2ATTOX model, are also summarized in Appendix A.
Note that the emission factors provided by EPA were based on low altitude. Because
Denver was one of the urban areas modeled in this study, adjustment for high-altitude
operation had to be made. This was accomplished by determining the ratio of (BERKgh_
Alt/BERLow.Alt)Mobile5b and applying that ratio to the revised low-altitude base emission rates.
Note that this adjustment was applied only to the zero-mile level, since the low-altitude
and high-altitude deterioration rates in MOBILESb are the same.
Off-Cycle Effects - Off-cycle corrections were also provided by EPA for use in this
analysis. Those corrections, consisting of separate adjustments for aggressive driving
behavior and air conditioning (A/C) usage, are different for I/M versus non-I/M areas.
(This is based on the fact that normal-emitting vehicles have a different off-cycle
response compared to high-emitting vehicles. Since I/M influences the fraction of
normals and highs in the fleet, there is a different adjustment for each area.) For 1981
and later model year vehicles, the correction factors provided by EPA were formatted as
multiplicative adjustments. For pre-1981 model year vehicles, however, three different
sets of emission factors (zero-mile levels and deterioration rates) were provided: (1)
uncorrected; (2) corrected for aggressive driving; and (3) corrected for aggressive driving
and air conditioning usage. Separate I/M and non-I/M factors were not provided for the
pre-1981 model year vehicles.
To simplify the modeling, the pre-1981 emission factors were combined with the
MOBILESb-calculated mileage versus age estimates for the 1990 and 1996 calendar
years. (For the 2007 and 2020 analyses, pre-1981 model year vehicles are no longer in
the fleet; thus, there is no need to calculate pre-1981 off-cycle corrections for those
calendar years.) The resulting emission rates were then used to calculate multiplicative
correction factors on the same basis as the 1981 and later model year factors provided by
EPA. For example, in 1996, a 1980 model year LDGV is projected to have accumulated
155,210 miles. Thus, using the BER equations provided by EPA (reported in terms of a
zero-mile level and a deterioration rate), emission rates for the three cases outlined above
are:
ZM PR Miles Emissions
(1) Uncorrected: 0.313 + 0.178*15.521 = 3.076g/mi
(2) Agg Driving: 0.384 + 0.216*15.521 = 3.737 g/mi
(3) Total Off-Cycle: 0.399 + 0.224*15.521 = 3.876 g/mi
The 1981 and later adjustment factors were based on a separate aggressive driving factor
and a separate A/C factor that, when multiplied together, give the total off-cycle factor.
Thus, the aggressive driving element in the example above is calculated as:
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AGG1980MY = 3.737 / 3.076 = 1.215
and the overall off-cycle factor is:
OCCF1980MY = 3.876 / 3.076 = 1.260
The A/C factor is then calculated as follows:
OCCF1980MY AGG1980MY A/C1980MY
A/C = 1.260 / 1.215 = 1.037
1980MY
The results from this evaluation are summarized in Table 3-3 for pre-1981 model year
vehicles, along with the factors for 1981 and later model year vehicles (which were given
directly in terms of multiplicative factors). Note that the aggressive driving factor
calculated above for the 1980 model year is slightly different than that shown in the table
because of rounding differences. The off-cycle TOG correction factors shown in
Table 3-3 are for the LDGV vehicle class for 2007 and later calendar years. (The 2007
calendar year is shown here so that a complete range of model years can be compared -
the 1996 evaluation year captures pre-1981 factors.) A complete set of off-cycle factors
used in this analysis is contained in Appendix A.*
Several points can be made with respect to the TOG off-cycle corrections contained in
Table 3-3. First, the off-cycle effects are greatest for 1981 to 2000 model years. Beyond
2000, the impact of the SFTP regulations take effect and the off-cycle impact is
substantially reduced. Second, the difference between the I/M and non-I/M rates is very
slight. Finally, the impact of air conditioning is very small, with a maximum of a 4%
increase with the 1981 to 1994 model year group.
The aggressive driving element of the off-cycle correction factors was applied to the FTP-
based TOG emission factor for all seasons, while the A/C adjustment was applied only to
the spring and summer runs. As described below, a more sophisticated methodology was
used to evaluate the impact of A/C usage on CO emissions. However, because the impact
of A/C usage on TOG emissions is so small, a more simplistic approach was used.
Finally, the multiplicative off-cycle factors in Table 3-3 were applied to the temperature-
corrected FTP-based emission rates. Although some type of correction for temperature is
probably warranted, there are no data with which to make such an adjustment. Thus, the
aggressive driving factor likely results in a slight over-estimate of TOG emissions at low
temperature.
Note that the off-cycle files in Appendix A contain toxics multipliers that are used to account for the
difference in toxics fractions between FTP operation and in-use operation. These multipliers are described
in the next section of the report.
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Table 3-3
TOG Off-Cycle Correction Factors
2007 and Later Calendar Years"
Model
Year
1965-1967
1968-1969
1970-1971
1972
1973
1974
1975
1976-1979
1980
1981-1994
1995-2000
2001
2002
2003
2004
Non-I/M Factors
AggDrv
.079
.091
.083
.130
.129
.128
.140
.139
.210
.228
.287
.218
.149
.051
.010
A/C
.016
.018
.016
.025
.024
.024
.026
.026
.037
.040
.010
.003
0.995
0.985
0.980
I/M Factors
AggDrv
1.079
1.091
1.083
1.130
1.129
1.128
1.140
1.139
1.210
1.230
1.290
1.220
1.150
1.052
1 010
A/C
.016
.018
.016
.025
.024
.024
.026
.026
.037
.040
.010
.003
0.995
0.985
0980
The pre-1981 model year factors reflect those used in a 1996 calendar year run.
Fuel Sulfur Impacts - Data recently collected by the Coordinating Research Council
(CRC) and the auto industry have indicated that the impact of gasoline sulfur levels is
more pronounced for low-emission vehicles than for older technologies (at least on a
percentage basis). Because of this effect, EPA included sulfur adjustments in the
emissions estimates prepared for the Tier 2 study. Such an adjustment was necessary
because LEVs are expected to be certified with low-sulfur fuel (approximately 40 ppm S),
while in-use fuel (in 1990) has been estimated to have a fuel sulfur level of 339 ppm.
Thus, the LEV-category emission factors in this study were corrected from a 40 ppm S
basis to a 339 ppm S basis. This was accomplished by using correlation equations
provided by EPA. This resulted in a multiplicative adjustment of 1.44 for LDGVs and a
multiplicative adjustment of 1.30 for LDGTls. Because the MOBILESb model includes
an in-use fuel correction (part of which includes an adjustment for the difference in sulfur
levels between certification fuel and in-use fuel), the factors above had to be further
revised before use in the model so that the sulfur effect was not double counted. This was
accomplished using the same approach as that outlined in the documentation prepared for
the Tier 2 Study.3 The final factors used in this study were therefore 1.36 for LDGVs and
1.23 for LDGTls. These factors are included in the TOG base emission rate equations
presented in Appendix A.
Fleet Characteristics - Two primary revisions to the modeling conducted in this study
were made to account for more recent information on the fleet make-up. These included
modifications to the LDGV, LDGT1, and LDGT2 registration distributions (i.e., the
fraction of vehicles making up the fleet by vehicle age) and modifications to the VMT
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mix used to compile vehicle-class-specific emission rates into an overall fleet average.
The registration distributions were modified to reflect the fact that vehicles are remaining
in the fleet for a longer period of time. This effect was incorporated into the 2007 and
2020 model runs. (The locality-specific registration fractions were used in the 1990 and
1996 calendar year analyses.) The VMT mix was revised to account for the large increase
in light-duty truck sales (e.g., minivans and sport-utility vehicles) over the last several
years. Revised registration and VMT mix inputs were provided by EPA and are
consistent with the values used in the Tier 2 Study. (More detail on the specific values
used in this study is given in a later section of the report.)
CO Emissions
As outlined above, the TOG emissions estimates formed the basis of the toxics emissions
estimates prepared for this study. As such, TOG emissions were calculated for the four
calendar years evaluated in this work (i.e., 1990, 1996, 2007, and 2020). On the other
hand, the CO emissions estimates were needed only for the 1990 calendar year. That is
because they were used only to calculate the [COExposure(ug/m3) /COEF(g/mi)]1990 ratios. Those
ratios were then combined with the toxics estimates to generate toxic exposure estimates
for each scenario.
As with the TOG emissions estimates, a number of changes related to CO were made to
the MOBILESb model to implement revisions planned for MOBILE6. These include:
Revised base emission rate equations;
Application of off-cycle correction factors; and
Revised oxygenated fuels effects.
A discussion of how these revisions were implemented for this study is included below.
Base Emission Rate Equations - The base emission rate equations supplied for this
element of the study were also developed by EPA. Revised emission factors were
provided for 1981 through 1990 model year LDGVs, and for 1984 through 1990 model
year LDGTls and LDGT2s. (Although the file containing the BERs included pre-1981
model year vehicles, those BERs are the same as the existing MOBILESb factors.) A
review of the BERs indicates that the revised factors include lower deterioration rates
than the baseline MOBILESb factors, similar to the TOG factors. A summary of the
revised BERs is provided in Table 3-4, and the BER inputs used in the modeling are
contained in Appendix A.
Because revised factors were supplied only for low-altitude areas, a correction for high
altitude was needed for the Denver runs. This was accomplished by determining the ratio
of (BERKgh.Alt/BERLow.Alt)Mobile5b and applying that ratio to the revised low-altitude base
-23-
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emission rates. Note that this adjustment was applied only to the zero-mile level, since
the low-altitude and high-altitude deterioration rates in MOBILESb are the same.
The BERs contained in Table 3-4 were used in conjunction with the T2ATTOX model to
generate CO emissions estimates for this study. That model was used because it is
capable of accepting more detailed sets of alternative BERs than the MOBILESb model
(e.g., variable flex points). Although T2AT could have been used for this purpose, the
non-toxics portion of the T2ATTOX code is no different when that model is used to
generate HC, CO, and NOx emissions estimates, and it was used in this case because the
code was immediately available for the off-cycle and oxygenated fuels revisions
described below.
Table 3-4
Revised FTP-Based CO BERs Used in Emissions Analysis
Vehicle
Class
LDGV
LDGT1
LDGT2
Model
Year
1981-82
1983-85
1986-89
1990
1984-89
1990
1984-89
1990
ZM
fe/mi)
4.301
2.813
2.795
2.188
6.045
5.382
6.045
5.382
DR1
(g/mi/lOK)
2.441
0.191
0.696
0.076
0.496
0.245
0.496
0.245
DR2
(g/mi/lOK)
3.037
1.650
0.556
1.094
0.717
1.094
0.717
Flex Point
(10,000 mi)
1.50
2.16
1.85
5.34
5.37
5.34
5.37
Off-Cycle Corrections - CO off-cycle correction factors were also provided by EPA for
use in this analysis. Those corrections were provided in the same format as the TOG
factors described above, and the same processing of those results occurred for use in the
T2ATTOX model (i.e., the pre-1981 factors were converted to multiplicative
adjustments). A summary of the CO off-cycle factors used in this analysis is contained in
Table 3-5 for LDGVs, and the complete set of factors is contained in Appendix A.
Of note in Table 3-5 is that the off-cycle correction factors are much larger for CO than
for TOG, particularly the A/C correction (which was almost non-existent in the TOG
analysis). When modeling the impacts of aggressive driving CO effects, there is concern
that at low temperature (which causes greatly elevated CO emissions) a multiplicative
adjustment may overstate the magnitude of the off-cycle increase. Thus, for this study,
the aggressive driving element of off-cycle effects were incorporated by first determining
a CO "offset" at 75 °F, adjusting that estimate for fuels effects (i.e., in-use fuel and
oxygenates), and then adding it to the temperature-corrected CO value estimated by the
model. A similar approach was taken to incorporate the A/C effect, but this was only
-24-
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done when the ambient temperature was over 69 °F as described below. These
adjustments were performed within the "BEF" subroutine in T2ATTOX.
Table 3-5
LDGV CO Off-Cycle Correction Factors
Model
Year
1965-66
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981 -91
Non-I/M Factors
AggDrv
1.328
1.324
1.370
1.365
1.375
1.371
1.432
1.426
1.419
1.574
1.568
1.560
1.552
1.543
1.861
1.611
A/C
1.217
1.215
1.237
1.235
1.240
1.238
1.265
1.263
1.260
1.321
1.319
1.316
1.313
1.310
1.407
1.326
I/M Factors
AggDrv
1.328
1.324
1.370
1.365
1.375
1.371
1.432
1.426
1.419
1.574
1.568
1.560
1.552
1.543
1.861
1.630
A/C
1.217
1.215
1.237
1.235
1.240
1.238
1.265
1.263
1.260
1.321
1.319
1.316
1.313
1.310
1.407
1.340
The aggressive driving component was calculated for all model runs, while the A/C
adjustment was applied only during periods of higher temperature (i.e., above 69 °F).
Further, between 69° and 85 °F, the A/C adjustment was interpolated between 1.0 and the
factor shown in Table 3-5. The 85°F point was chosen because it represents the
temperature corresponding to a 52% compressor-on fraction,4 which was the basis of the
estimates given in Table 3-5. The factors were linearly scaled between 85° and 108°F,
with the upper end of that range representing a 100% compressor-on fraction. Finally, the
model-year-specific factors given in that table were adjusted for the fraction of vehicles
assumed to be equipped with functioning air conditioning systems. These estimates were
based on data contained in EPA's draft air conditioning activity effects recommended for
MOBILE64 and are summarized in Appendix A.
Oxygenated Fuels Effects - The impacts of oxygenated fuels on CO emissions modeled in
this effort were based on estimates prepared by Sierra under contract to API.5 Sierra
worked closely with EPA staff during the development of those estimates, and, in fact,
EPA has recommended that the results of that study be used in the MOBILE6 model6 to
estimate the emissions impacts of oxygenated fuels on pre-1994 model year vehicles.
Because the current analysis is aimed at the 1990 calendar year, estimates for Tier 1 and
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more advanced technologies were not needed. In addition, because the analysis
referenced above only considered 1981 and later model year vehicles, the CO oxygenated
fuel effects were revised in this analysis only for 1981 to 1990 model year vehicles;
existing MOBILES oxygenated fuels impacts were retained for pre-1981 model year
vehicles as well as for heavy-duty gasoline vehicles.
The oxygenated fuels impacts used in this analysis are summarized in Table 3-6. As
observed in that table, the fuel oxygen impact is a function of emitter category and
technology, i.e., vehicles equipped with adaptive learning (ADL) computer logic are less
sensitive to oxygen in the fuel than are older technology vehicles. However, one
shortcoming of this approach is that the fraction of the fleet equipped with ADL systems
has not been estimated by model year. For this analysis, we needed only the fraction of
vehicles equipped with ADL systems for 1986 and later model years (pre-1986 model
year vehicles were analyzed separately, without regards to ADL capability).
Table 3-6
Recommended CO Effects From the Use of Oxygenated Fuels
for Matched RVP Blends at 75 °F
Emitter
Category
Normal
High
Technology
1988+TWC/ADL
1986-87 TWC/ADL
1986+ TWC/No ADL
1981-85TWC/CL
OX/OLb
Non-Catalystb
1981+TWC/CL
OX/OLb
Non-Catalystb
CO Impact Per
Wt% Oxygen
-3.1%(n=133)a
-4.8% (n=104)
-5.7%(n=151)
-4.0% (n=73)
-9.4%
-6.6%
-5.3%(n=134)a
-9.4%
-6.6%
Typical
MTBE Blend
(2.7 wt% O)
-8.4%
-13.0%
-15.4%
-10.8%
-25.4%
-17.8%
-14.3%
-25.4%
-17.8%
Typical
Ethanol Blend
(3.5wt%O)
-10.9%
-16.8%
-20.0%
-14.0%
-32.9%
-23.1%
-18.6%
-32.9%
-23.1%
a Sample size shown in parentheses.
Open-loop and non-catalyst factors are based on an EPA analysis used to support oxygenated fuel impacts in
MOBILE4.1 and MOBILES.7
Based roughly on the fraction of vehicles in the EPA emission factors database that were
also included in the Complex model database (which, by design, had to be equipped with
ADL), the following phase-in of ADL systems was assumed for this analysis:
1986 to 1987 - 50% equipped with ADL;
1988 to 1989 - 75% equipped with ADL; and
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1990 to 1991 - 90% equipped with ADL.
Using the ADL technology weightings above (as well as the catalyst type technology
weightings used elsewhere in this analysis), oxygenated fuel factors for normal and high
emitting vehicles were generated for 1981 to 1991 model years, and the results are shown
in Table 3-7 for LDGVs. Based on discussions with EPA, the light-duty truck categories
were assumed to lag passenger cars in terms of ADL technology implementation by five
years. Thus, the 1986+ TWC/No ADL factors from Table 3-6 were used to represent all
1986 to 1990 model year trucks. The final factors used in this analysis are summarized in
Appendix A.
Table 3-7
Model- Year Specific CO Benefits from Oxygenated Fuel for LDGVs
(Reductions are in Terms of % per wt% Oxygen)
Model
Year
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
Normals
% Red
5.5
5.8
5.3
4.3
4.4
5.4
5.3
3.8
3.8
3.4
3.4
g/mi
4.9
4.9
4.9
4.9
4.9
3.2
3.2
3.0
3.0
2.8
2.8
Highs
% Red
6.5
6.6
6.3
5.5
5.6
5.4
5.4
5.3
5.3
5.3
5.3
g/mi
20.5
20.5
20.5
20.5
20.5
20.5
20.5
20.5
20.5
20.5
20.5
Because different oxygenated fuels impacts are applied to normal-emitting vehicles and
to high-emitting vehicles, a method to estimate the fraction of normals and highs in the
fleet (as a function of vehicle or mileage) was needed. This was accomplished by first
determining the average CO emission level of the normal- and high-emitting vehicles
used to generate the CO impacts listed in Table 3-6. These averages were used to
compute the mean normal and high emission rate in the model-year-specific factors
shown in Table 3-7.
From Table 3-7, the mean CO from a 1988 normal-emitting LDGV is 3.0 g/mi and the
mean CO from a high-emitting vehicle is 20.5 g/mi. If the mean CO emission rate of a
1988 LDGV in calendar year 1990 is 7.0 g/mi, then the fraction of normal emitters in the
fleet at that point (N) can be determined as follows:
7.0 g/mi = 3.0*N + 20.5*(1-N)
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Solving the above equation for N results in 77.1% of the fleet being normal emitters and
22.9% of the fleet being high emitters. The impact of oxygenated fuel (assuming 3.5%
oxygen by weight) can then be estimated as follows (taking values from Table 3-7 for the
1988 model year):
Non-oxygen CO = 3.0*0.771 + 20.5*0.229 = 7.01 g/mi
Oxygen CO = 3.0*0.771*(1-0.038*3.5)
+ 20.5*0.229*0-0.053*3.5) = 5.83 g/mi
Thus, an overall oxygenated fuel benefit of 16.8% (i.e., 1 - 5.83/7.01) is estimated for this
case. This same general approach was used to determine the oxygenated fuel impacts for
all 1981 and later model year cars and light trucks. This methodology was incorporated
into the T2ATTOX model by making revisions to the "FUEL" subroutine.
###
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4. TOXICS EMISSIONS MODELING METHODOLOGY
Once the revisions to the methodology and inputs needed to estimate TOG emissions
were finalized, it was necessary to develop an approach to generate air toxics estimates.
As described below, the approach utilized for exhaust emissions makes use of "toxic-
TOG" curve in which the FTP-based g/mi TOG emission rate was used to extract the
corresponding mg/mi toxic emission rate. In this way, the differences in toxics fractions
between normal- and high-emitting vehicles were accounted for in the calculations. For
evaporative emissions, a simpler method was used in which the mass fraction of each
toxic (as a fraction of TOG emissions) was applied to the evaporative emissions estimates
calculated by the standard MOBILESb routine contained within the T2ATTOX model.
Finally, Diesel PM emissions were estimated directly from EPA's PARTS model. Each
of these elements of the toxics modeling performed for this study is presented in this
section of the report.
Exhaust Emissions
Previous EPA Estimates - During the development of the 1993 Motor Vehicle Related
Air Toxics Study, EPA spent considerable effort developing estimates of on-road motor
vehicle air toxics. At that time, the number of motor vehicle test programs that measured
air toxics was limited, and because most of the available data were from low-mileage,
well-maintained vehicles, EPA found it difficult to develop a direct gram per mile (or
milligram per mile) toxic emission rate reflective of the in-use fleet. Instead, available
emissions data were used to estimate air toxics emissions as a fraction of the total organic
gases (TOG) emitted from the test vehicles. Those estimates were then applied to output
from an emission factor model (MOBILE4.1 in the case of the EPA MVRATS) to
estimate air toxics from the in-use fleet.
In developing emission estimates for motor vehicle air toxics, EPA found that the toxics
fractions were a function of a vehicle's emission control system design and fuel type (i.e.,
gasoline versus Diesel). Thus, toxics fractions were developed separately for each of the
following technologies:
three-way catalyst (TW CAT),
three-way plus oxidation catalyst (TW+OX CAT),
oxidation catalyst (OX CAT),
-29-
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no catalyst (NO CAT),
light-duty Diesel vehicle (LD Diesel), and
heavy-duty Diesel vehicle (HD Diesel).
A summary of the toxics fractions for benzene, 1,3-butadiene, formaldehyde, and
acetaldehyde from the 1993 MVRATS is contained in Table 4-1. Several items are worth
noting with respect to this table. First, although the benzene fractions are reported as
single values, EPA developed equations for the gasoline technologies that estimated the
benzene fraction as a function of fuel benzene content and fuel aromatic content (i.e., as
fuel benzene and aromatic content go up, so does the benzene fraction in the exhaust).*
The benzene fractions shown in Table 4-1 are based on the fuel parameters specified in
the Clean Air Act for baseline gasoline (i.e., RF-A in the Auto/Oil Air Quality
Improvement Research Program). Second, although the 1,3-butadiene, formaldehyde,
and acetaldehyde fractions are shown as single values, EPA found those to vary as a
function of whether the gasoline contained oxygenate. (The values in the table assume no
oxygenate.) For example, a fuel containing MTBE would result in higher formaldehyde
fractions than shown in Table 4-1.
Table 4-1
Exhaust Toxics Fractions as a % of TOG Emissions
Used by EPA in the 1993 Motor Vehicle Related Air Toxics Study
Technology
TWCAT
TW+OX CAT
OX CAT
NO CAT
LD Diesel
HD Diesel
Benzene3
5.27
2.87
4.05
4.05
2.29
1.06
1,3 -Butadiene
0.57
0.44
0.44
0.98
1.03
1.58
Formaldehyde
0.87
1.37
1.39
2.69
3.91
2.80
Acetaldehyde
0.47
0.45
0.44
0.62
1.25
0.75
a The benzene fractions for gasoline-fueled vehicles are based on 1990 industry-average gasoline, which
contained an average of 1.53 vol% benzene and 32 vol% aromatics.
Note that oxygenate was determined not to have a significant direct impact on the percentage of benzene
in exhaust, and it is not a parameter in the equations developed by EPA. However, to the extent that the
addition of oxygenate reduces the concentration of benzene and aromatics through dilution effects, it
indirectly affects the percentage of benzene in exhaust hydrocarbons.
-30-
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Also of interest in Table 4-1 is the fact that benzene and 1,3-butadiene fractions are
higher for more advanced emission control technology (i.e., the TW CAT technology).
However, the lower overall TOG mass from those vehicles more than compensated for
the increased toxics fractions, and a net reduction in toxics emissions resulted from newer
technology vehicles in EPA's analysis.
Complex Model for Reformulated Gasoline - Following the release of the 1993
MVRATS, EPA finalized the reformulated gasoline (RFG) regulations. As part of those
regulations, the Complex model8 was developed that allows refiners to assess whether
particular fuel formulations meet the RFG performance standards (i.e., percent reductions
of VOC, NOx, and toxics). That model calculates the emissions impacts of alternative
gasoline formulations relative to the baseline 1990 industry average fuel defined in the
1990 Clean Air Act Amendments. The fuel parameters included in the calculations are
listed below.
Oxygenate content (wt %) and type (i.e., MTBE, ethanol, ETBE, or TAME)
Sulfur content (ppm)
RVP (psi)
E200 (%)
E300 (%)
Aromatics (vol %)
Olefms (vol %)
Benzene (vol %)
In addition to VOC and NOx, the Complex model estimates the impact of varying fuel
formulation on benzene, acetaldehyde, formaldehyde, 1,3-butadiene, and polycyclic
organic matter (POM) exhaust emissions. Because the Complex model was based on a
much larger database than the toxic fractions used in the MVRATS, EPA has been
criticized in the past for not using the Complex model results in that study. However,
that criticism is not warranted, since the Complex model was not available at the time the
emissions analysis was performed for the MVRATS. In addition, the Complex model has
its own limitations. First, the database used to develop the Complex model included only
1986 to 1990 model year vehicles, so it cannot be used to predict toxic emission rates
from older technology vehicles, and projecting results onto future technologies introduces
uncertainty into the analysis. Second, only gasoline-fueled light-duty cars and trucks
were included in the Complex model database, so it cannot be used to predict toxics
emissions from Diesel vehicles, heavy-duty gasoline vehicles, or motorcycles.
The above limitations notwithstanding, the Complex model remains the most robust tool
currently available with which to estimate toxics emissions from late-model vehicles,
particularly when alternative fuel formulations are being investigated. For that reason,
the Complex model was used in this study to generate toxics emissions estimates from
light-duty vehicles equipped with three-way catalyst systems. For this analysis, EPA
provided an "unconsolidated" version of the Complex model that generated separate
emissions estimates as a function of technology, e.g., port fuel injection (PFI) was broken
out separately from throttle body injection (TBI). In addition, results were reported
-31-
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separately for normal-emitting vehicles and for high-emitting vehicles. With this level of
detail, it was possible to generate model-year-specific toxics fractions and emission rates
by applying the appropriate technology sales mix to each model year and vehicle class. In
addition, because the response to differing fuel formulations is often much different for
high-emitting vehicles relative to normal-emitting vehicles, modeling those effects
separately resulted in improved toxics emissions estimates.
A sample output from the unconsolidated Complex model is given in Figure 4-1. For that
particular run, the fuel parameters for Chicago in the summer of 1990 were used. As
outlined in the figure, the model first calculates a percentage change for exhaust VOC,
exhaust benzene, acetaldehyde, formaldehyde, and 1,3-butadiene based on the difference
in fuel parameters between the baseline gasoline (as defined in the Clean Air Act) and the
target fuel. These percentage changes are then applied to baseline emission rates (in
mg/mi) to arrive at the target fuel emission rate. For the winter runs, the baseline fuel
specifications are slightly different. In addition, the winter runs held the RVP to 8.7 psi
for both the baseline and target fuel because RVPs typical of wintertime fuels (e.g., on the
order of 13.5 psi) are outside the range of the Complex model. Finally, because
temperature corrections were applied within the modified MOBILE model developed for
this study, the technology-group-specific baseline emission rates in the summer version of
the Complex model were not modified to reflect winter temperatures.
As part of this study, MTBE emissions were also estimated. However, the standard
version of the Complex model does not calculate MTBE emissions separately. Thus,
EPA provided Sierra with an unpublished version of an MTBE model that is patterned
after the Complex model.9 It should be noted that the MTBE model contains a strong
caveat that the regression analyses upon which the model was based have not been peer
reviewed, and therefore the results are subject to some uncertainty.
Treatment of Normal and High Emitters ("Toxic-TOG Curves") - An issue that received
considerable discussion at the beginning of this project was how to implement an
approach that treated normal and high emitters separately. The issue here is that normal
emitters and high emitters may have different characteristics in terms of their response to
fuel parameters (and corresponding toxics fractions) and therefore need to be treated
separately. This becomes difficult when different I/M scenarios are considered that
impact the distribution of normals and highs in the fleet. A methodology to account for
normal and high emitters within the T2ATTOX code was suggested by EPA. A summary
of this method is presented below, and the original write-up provided by EPA is included
in Appendix B.
Although the approach suggested by EPA was presented in algebraic terms, it is useful to
start with a simple example and work backward from there. Assume that the TOG
emission rates, benzene emission rates, and benzene fractions for normal and high
emitters corresponding to a baseline fuel and a target fuel are as listed in Table 4-2.
Using the values presented in Table 4-2, if T2ATTOX calculated a fleet-average emission
rate of 1.0 g/mi TOG for the baseline fuel, the fraction of normals and highs making up
the 1.0 g/mi emission rate could be calculated as follows:
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Figure 4-1
Unconsolidated Complex Model Run
Chicago
Fuel Prameters
1990
Summertime
Based on
Fuel Parameters
CAA Base Target Fuel
OXYGEN (wt%)
SULFUR (ppm)
RVP (psi)
E200 (%)
E300 (%)
AROMATICS (vol%)
OLEFINS (vol%)
BENZENE (vol%)
Percent Change
Exh
TG1
TG2
TG3
TG4
TG5
TG6
TG7
TG8
TG9
High Emitters
Baseline mg/mi
Exh
TG1
TG2
TG3
TG4
TG5
TG6
TG7
TG8
TG9
High Emitters
Target Fuel mg/mi
Exh
TG1
TG2
TG3
TG4
TG5
TG6
TG7
TG8
TG9
High Emitters
voc
8.91
6.63
10.85
19.67
18.25
5.37
11.10
11.10
-2.75
VOC
493
404
408
771
317
354
689
457
3075
VOC
537
431
452
923
375
373
765
508
2990
0
339
8.7
41
83
32
9.2
1.53
Exh ben
0.21
-6.16
4.90
-6.16
-12.66
-6.16
-6.16
-36.76
-6.62
Exh ben
27.30
22.39
22.59
42.72
17.58
19.64
38.20
25.33
190.65
Exh ben
27.35
21.01
23.69
40.09
15.35
18.43
35.85
16.02
178.02
0
512
8.67
47.2
78.6
28.8
8.6
1.35
Ace
12.32
12.32
12.32
11.63
12.32
12.32
12.32
12.32
12.32
Ace
2.42
1.99
2.01
3.79
1.56
1.74
3.39
2.25
15.01
Ace
2.72
2.23
2.25
4.23
1.75
1.96
3.81
2.53
16.85
Form
6.97
6.97
6.97
6.97
6.97
6.97
6.97
6.97
8.86
Form
5.91
4.85
4.89
9.25
3.81
4.25
8.27
5.49
29.58
Form
6.33
5.19
5.23
9.90
4.07
4.55
8.85
5.87
32.20
But
11.95
2.57
7.61
-4.38
2.57
11.18
2.57
2.57
-2.12
But
2.67
2.19
2.21
4.18
1.72
1.92
3.74
2.48
43.97
But
2.99
2.25
2.38
4.00
1.76
2.14
3.83
2.54
43.04
-------
Table 4-2
Hypothetical TOG and Benzene Emissions
Benzene (g/mi)
1.0g/mi=FN*TOGHBaseFuel + I
where FN is the fraction of normals and FH is the fraction of highs. The TOG emission
rates for normals and highs on base fuel (TOGN Base Fuel and TOG^ Base Fuel) can be obtained
from Table 4-2, and the fraction of highs is just (1-FN). Substituting these into the
equation above gives:
1.0 g/mi = FN*0.5 + (1-FN)*2.0
Solving the above for FN results in the fraction of normals being 0.667 and the fraction of
highs being 0.333.
Using these fractions with the benzene emission rate for normals and highs, one can
obtain the mean benzene emission rate for the target fuel presented in this example, i.e.,
BZntjarge,
R
where BZnt Target is the fleet-average benzene emission rate for the target fuel, BZNTarget is
the average benzene emissions from normal emitters operating on the target fuel, and
BZjjjargg, is the average benzene emissions from high emitters operating on the target fuel.
Substituting the fraction of normals and highs calculated above and the benzene emission
rates from Table 4-2, the following is obtained:
BZntTarget = 0.667*0.016 + 0.333*0.133 = 0.055 g/mi (or 55 mg/mi)
Note that this approach used the benzene emission rate for the target fuel directly without
first adjusting the base fuel TOG levels for the target fuel.
As outlined in Appendix B, the emissions data presented in Table 4-2 can also be thought
of in graphical terms, as illustrated in Figure 4-2. Using this presentation, the target fuel
benzene emission level (in g/mi or mg/mi) can be thought of as a linear function of the
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140
Hypothetical Benzene-TOG Curve
0.5
1 1.5
Baseline Fuel TOG (g/mi)
2.5
-------
Figure 4-2
Benzene-TOG curve
baseline fuel TOG emission rate. The baseline fuel normal emitter TOG emission rate
defines the lower end of the curve, while the baseline fuel high emitter TOG emission
rate defines the upper end of the curve. Thus, the points plotted in Figure 4-2 are simply
the values outlined in Table 4-2.
Based on the relationships presented in Appendix B, these "toxic-TOG curves" can be
defined by an intercept (A) and a slope (B), according to the following:
j^ Base Fuel BZN Target - TOGN Base Fuel BZ^ Target)/
( A OGj^ Base Fue[ - 1 OGN Base Fue[)
^Target ~~ U^H, Target " ^^N, Target)' ( ^ OGj^ Base Fue[ - 1 OGN Base Fuei)
where the TOG and BZ variables are those defined previously.
Using baseline fuel normal and high emitter TOG emission rates (in g/mi) and the target
fuel normal and high emitter benzene emission rates (in mg/mi) defined in Table 4-2 as
an example, the values of A and B are calculated as:
ATarget = (2.0* 16 - 0.5* 133)7(2.0 - 0.5) = -23.0
BTarge, = (133 - 16)7(2.0 - 0.5) = 78.0
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Using the above example of a fleet-average TOG emission rate of 1.0 g/mi on the base
fuel, the fleet-average benzene emission rate (in mg/mi) is calculated as:
BZHt Target ATarget + BTarget TOGHt Base Fuel
BZHtjTarget = -23.0 + 78.0*1 = 55.0 mg/mi
which matches the calculation performed above.
An issue related to the above methodology is whether the linear assumption is valid for
baseline TOG values above the high emitter point and below the normal emitter point.
This is particularly relevant in cases where A and B values are determined from Tier 0
vehicles (e.g., the Complex model), but the results are applied to Tier 1 and LEV-
category vehicles. For the simple example presented above, negative benzene emissions
are estimated for the target fuel when the baseline fleet-average TOG emission rate falls
below 0.295 g/mi. Thus, for fleet-average emission rates below (and above) the normal
(and high) emitter values, a different methodology was needed. In those cases, it was
assumed that the toxic emission rate was the same on a fractional basis. For the example
above, the benzene emission rate for a baseline TOG value of 0.1 g/mi would be
calculated as follows:
BZ(TOG=0 j g/mi) = 0.1 g/mi * (16 mg/mi BZ / 0.5 g/mi TOG) = 3.2 mg/mi
This has the effect of forcing the toxic-TOG curve from the normal-emitter point back
through the origin. The same approach is used in cases where the fleet-average baseline
TOG emission rate is above the high emitter point.
The above approach was used to estimate toxic emissions as a function of baseline fuel
TOG emission rates for all categories of vehicles. (For this analysis, industry average
fuel defined in the 1990 Clean Air Act Amendments was considered the baseline fuel.)
Rather than generating the A and B terms outside of the model, an input file was created
with the normal and high emitter TOG emission rates (in g/mi) and the corresponding
normal and high toxic emission rates (in mg/mi). This approach made the QC process
much easier and only required a few lines of code to implement.
Toxic-TOG Curves: Pre-Complex Model Vehicles - For pre-complex model light-duty
gasoline cars and trucks, heavy-duty gasoline vehicles, and Diesel vehicles, there are
insufficient data with which to establish toxic emission rates as a function of normal and
high emitters. As such, the toxic-TOG curves were generated by establishing the normal
emitter point at the origin and the high emitter baseline TOG emission rate at 10 g/mi.
The toxic emission rates corresponding to the 10 g/mi TOG value were then calculated
from equations developed by EPA, many of which were updated from those developed
for the 1993 MVRATS. A summary of these relationships is given in Appendix C.
As an example of the methodology used in this analysis, consider benzene emissions
from a non-catalyst FtDGV using a fuel with 1.2 vol% benzene and 31 vol% aromatics.
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The equation relating the fuel parameters to the benzene level (as a percentage of TOG
emissions) for non-catalyst HDGVs (from Appendix C) is as follows:
BZ %TOG= 0.8551 * vol% BZ + 0.12198 * vol% ARO - 1.1626
BZ%TOG= 0.8551 * 1.2 + 0.12198*31 - 1.1626 = 3.64%
Thus, if the high-emitter TOG emission rate is assumed to be 10 g/mi, the resulting
benzene emission rate would be:
BZKghEmitter = 10 g/mi * 0.0364 = 0.364 g/mi (or 364 mg/mi)
For cases in which the target fuel contained an oxygenate or an RVP level below the
baseline fuel assumption (i.e., 8.7 psi),* the TOG emission rate was decreased to account
for that effect prior to generating the toxic pollutant emission point. The corrections used
to model those impacts were provided by EPA and are summarized in Table 4-3.
Table 4-3
TOG Oxygenate and RVP Adjustments for Non-Complex Model Vehicles
Fuel Parameter
Oxygen, per 1 wt%
RVP, per 1 psi decrease
Non-Catalyst Vehicles
- 1.6%
- 1.8%
Oxidation Catalyst Vehicles
- 4.46%
- 1.7%
The methodology described above was applied to all technology groups and vehicle
classes that were not evaluated with the Complex model. Open-loop three-way catalyst
technologies, which are not evaluated by the Complex model, were treated as open-loop
oxidation catalyst vehicles for this analysis. (Note that this technology was used only
during the early 1980s, and it never accounted for more than 20% of the light-duty
vehicle fleet in any model year.) Technology-specific toxic emission rates were
developed based on a 10 g/mi TOG emission rate, and model-year-specific technology
fractions (described later in this section of the report) were used to compile model-year-
specific toxic-TOG curves.
Toxic-TOG Curves: Tier 0 Vehicles - The toxic-TOG curves developed for closed-loop
Tier 0 vehicles made use of the unconsolidated Complex model provided to Sierra by
Note that the RVP effect was applied only during the spring and summer evaluation periods. That is
because the impact of RVP on exhaust emissions is generally thought to be a result of canister purge.
Thus, under cold temperature conditions, this effect would be mitigated.
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EPA. (All open-loop technologies were analyzed as described above.) The Complex
model provides emissions estimates for eight different technology groups plus high
emitters. For this study, the Complex model technology groups were collapsed to be
consistent with available data on the fleet make-up (based on MOBILESa definitions).
The mapping between the Complex model technology groups and the technology groups
utilized in this analysis was suggested by EPA (see Appendix D) and is summarized in
Table 4-4.
Table 4-4
MOBILESa and Complex Model Technology Group Mappings
MOBILESa Tech Group
Complex Model Tech Groups
Carbureted (3W and 3W+OX)
3WPFI
3WTBI
3W+OX PFI
3W+OX TBI
High Emitters (All Technologies)
9
Average of 1, 2, and 5
Average of 3 and 6
4
7
High Emitter
The first step in this part of the analysis was to develop baseline fuel TOG emission rates
for normal and high emitters in the Complex model. Because the Complex model
exhaust hydrocarbon emissions estimates are based on volatile organic carbon (VOC)
emissions (VOC = TOG - methane - ethane), a conversion to TOG was necessary. This
was based on conversion factors provided by EPA, which recommended that toxic
fractions based on VOC be scaled by a factor of 0.8079 for three-way catalyst vehicles
and a factor of 0.7166 for three way + oxidation catalyst vehicles. Alternatively, dividing
VOC emissions by these factors results in TOG emission estimates. Thus, after
combining the technology groups as described in Table 4-4, the resulting VOC emission
rates were converted to a TOG basis. These are shown in Table 4-5.
From this point, it is a simple matter of running the Complex model for the fuel
parameters being analyzed and compiling the resulting toxics emission rates for each
technology group. The model-year-specific emission rates (both TOG and toxics) for
normal emitters were then developed by weighting the technology-specific Complex
model results by the fraction of each technology in the fleet. A sample of this calculation
is shown for TOG and benzene in Table 4-6 for 1988 model year LDGVs evaluated with
1990 Chicago summertime fuel parameters. Note that the four values in the lower right
corner of the table shown in bold print would be used to establish the normal and high
emitter points on the benzene-TOG curve for this model year and vehicle class. The
same methodology was used for the remaining model years that had Tier 0 vehicles
equipped with closed-loop technology.
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Table 4-5
Mean Complex Model Base Fuel
VOC and TOG Emission Rates by Technology Group
MOBILES a Tech Group
Carbureted (3W and 3W+OX)a
3WPFI
3WTBI
3W+OX PFI
3W+OX TBI
High Emitters (All Technologies)13
Mean VOC (g/mi)
0.457
0.405
0.381
0.771
0.689
3.075
Mean TOG (g/mi)
0.638
0.501
0.472
1.076
0.961
4.034
a The VOC-to-TOG correction was based on 3 W+OX technology for this group.
The VOC-to-TOG correction was based on an average of 3 W and 3 W+OX technology groups for high
emitters.
Table 4-6
Sample Calculation Used to Develop the Toxic-TOG Curve for Benzene
1988 Model Year LDGV - 1990 Chicago Summertime Fuel
Tech Group
Carbureted
3WPFI
3WTBI
3W+OX PFI
3W+OX TBI
Normal Emitters
High Emitters
Fraction
0.101
0.444
0.327
0.048
0.080
TOG (g/mi)
0.638
0.501
0.472
1.076
0.961
0.570
4.034
Benzene (mg/mi)
16.02
21.24
21.06
40.09
35.85
22.73
178.02
Toxic-TOG Curves: Tier 1 Vehicles - For Tier 1 vehicles, the normal-emitter point
developed according to the methodology described above for closed-loop Tier 0 vehicles
was modified to reflect the fact that Tier 1 vehicles are certified to more stringent
hydrocarbon standards. Based on a review of information presented at the July 1992
MOBILESa workshop, Tier 0 vehicles (which are certified to a 0.41 g/mi total
hydrocarbon standard) have an effective NMHC standard of 0.377 g/mi. Tier 1 vehicles
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are certified to 0.25 g/mi NMHC. Thus, the lower point on the toxic-TOG curve
developed from the Complex model was adjusted by the ratio 0.25/0.377. This correction
was used for both cars and trucks, since the Complex model relationships were based on
data from cars and trucks, and similar fractional NMHC reductions occur between Tier 1
and Tier 0 vehicles. Because there is no information to suggest that Tier 1 high emitters
will be substantially different than Tier 0 high emitters (although there should be fewer of
them), the high-emitter point on the toxic-TOG curve was left unchanged.
Toxic-TOG Curves: LEV-Category Vehicles - As with Tier 1 vehicles, the high-emitter
point on the toxic-TOG curves remained the same for LEVs as that calculated for Tier 0
vehicles. (It is too early to determine if high-emitting LEVs will be significantly different
than high-emitting Tier 0 vehicles.) However, the normal-emitter point on the toxic-TOG
curve required an adjustment for gasoline sulfur level in addition to that made for the
standards differences.
The baseline fuel normal-emitter TOG point was corrected to account for LEV standards
by applying a ratio of standards to the Tier 0-based Complex model value for each
technology type. As described above, the Tier 0 "effective" NMHC standard is
0.377 g/mi. LEVs are certified to 0.075 g/mi nonmethane organic gas (NMOG), so an
approach to correct this to an equivalent NMHC basis was needed. This correction was
based on similar corrections developed by EPA and presented at the July 1992 MOBILES
workshop. Three corrections were applied to the 0.075 g/mi NMOG value: (1) a straight
NMOG to NMHC correction to remove "organic" gases (0.075 -> 0.0728); (2) a
correction to account for the fact that CARB-certified LEVs receive a reactivity
adjustment of 0.9410 (0.0728 KX0775); and (3) a correction to account for the difference
between California certification fuel and federal certification fuel (0.0775 >0.0880).
Using the TW PFI technology group as an example (0.501 g/mi TOG, from Table 4-5),
the resulting TOG normal emitter point was calculated to be:
TOGLEV.3WPn = 0.501 * (0.088/0.377) = 0.117 g/mi
Note that this reflects the LEV TOG emission rate on baseline fuel with 339 ppm S.
To generate toxics emission rates as a function of fuel parameters, several steps were
required. Because LEVs have been shown to have a stronger response to gasoline sulfur
levels than Tier 0 vehicles, the Complex model results could not be used directly in the
calculations. Instead, the Complex model was used to determine the non-sulfur fuel
corrections, while the sulfur equations provided by EPA (described in Section 3 of this
report) were used to determine the LEV-specific sulfur corrections. The specific
calculations in this analysis are illustrated with the example below.
Using the fuel parameters from the 1990 Chicago summer example above, the normal
emitter target fuel benzene emission rate for the 3W PFI technology group was calculated
as follows. (Although LEVs will not necessarily be operated on this fuel, it serves as a
good example.) First, it was assumed that the LEV sulfur effect would impact the TOG
mass and the toxics mass equally. Thus, the toxics mass fraction for the fuel being
analyzed was determined by simply taking the ratio of the target fuel toxic emission rate
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to the target fuel TOG rate calculated by the Complex model. In the case of benzene for
this example, this was 0.02124/0.5539 = 3.835%.
The next step of the analysis was to determine the impact that the fuel modifications
would have on the LEV TOG emission rate. This was estimated by determining the non-
sulfur TOG correction from the Complex model and the sulfur TOG correction from the
EPA equations. The non-sulfur Complex model correction was determined by
calculating the target fuel TOG emission rate with a sulfur level of 339 ppm. For this
example, the target fuel non-sulfur TOG emission rate was 0.505 g/mi (compared to a
baseline of 0.501 g/mi). Thus, the non-sulfur correction for this fuel was calculated as
follows:
TOGujv/N^s = 0.117 g/mi * (0.505/0.501) = 0.118 g/mi
The sulfur correction was applied next. In this example, the in-use sulfur level was
512 ppm. Thus a correction from 339 to 512 ppm was developed from the EPA
equations. This amounted to a multiplicative factor of 1.107. Applying this factor to the
non-sulfur TOG emission rate, the following is obtained:
TOGI£V/&^rected = 0.118g/mi * 1.107 = 0.131 g/mi
The benzene emission rate was then determined by applying the previously calculated
benzene fraction to the above TOG emission rate:
BZTarget = 0.131 g/mi * 0.03835 = 0.00502 g/mi (or 5.02 mg/mi)
Thus, for this fuel, the bottom point of the benzene-TOG curve would be 0.501 g/mi
TOG and 5.02 mg/mi benzene.
Technology Fractions - Because toxics emissions and toxics fractions are a function of
technology, the model-year-specific toxic-TOG curves developed for this study were
generated by weighting technology-specific emissions by the estimated sales mix of each
technology as a function of model year. For gasoline-fueled vehicles, the following
technology types were considered:
Open-loop, non-catalyst;
Open-loop, catalyst;
Closed-loop, carbureted;
Closed-loop, three-way catalyst, PFI;
Closed-loop, three-way + oxidation catalyst, PFI;
Closed-loop, three-way catalyst, TBI; and
Closed-loop, three-way + oxidation catalyst, TBI.
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For pre-1991 model year light-duty cars and trucks and all heavy-duty gasoline vehicles,
the technology fractions were based on those developed by EPA for MOBILESa.
Technology fractions for 1992 and later model year LDGV, LDGT1, and LDGT2
categories were derived from a recent report prepared in support of MOBILE6.11
However, because that study did not report PFI and TBI technologies separately for 1996
and later model year LDGTs, Sierra had to make assumptions regarding the phase-out of
TBI technology. In this analysis it was assumed that TBI technology on light-duty
gasoline trucks would be phased-out under the NLEV program (i.e., by the 2001 model
year for non-OTR states). The technology distribution for LDGTs for the 1996 to 2000
model years was estimated by interpolating between the 1995 and 2001 values. The final
model-year-specific technology fractions used in this study are summarized in Appendix
E.
Aggressive Driving Correction - The vast majority of data and models related to motor
vehicle air toxics is based on FTP testing. However, to be consistent with the approach
taken in the MOBILE modeling (i.e., T2AT) for the Tier 2 Study, EPA recommended that
an adjustment for aggressive driving behavior be applied to the toxics estimates
developed in this work assignment. This adjustment can be thought of as two discrete
steps: (1) an adjustment (i.e., increase) to the TOG mass to account for off-cycle
operation, and (2) an adjustment (increase or decrease) to account for the difference in
mass fraction of each toxic compound of interest between the FTP and the Unified Cycle
(UC). The UC, or LA92, is used here because that is the cycle upon which the TOG
aggressive driving corrections were developed for the T2AT model.
The methodology used to apply an aggressive driving correction to the toxics estimates
for this study is best illustrated with an example. Consider a case in which the Tier 1
vehicle FTP-based TOG emission rate is 0.5 g/mi and the benzene mass fraction is 5%.
Assume that the benzene mass fraction on the Unified Cycle is 7%. Using the off-cycle
correction factors developed by EPA for this effort, the TOG emission rate, corrected for
aggressive driving behavior, would be as follows:
TOGuc = OCCFAgg*TOGFTP
TOGUC = 1.29 * 0.5 g/mi = 0.645 g/mi
where 1.29 is the aggressive driving correction for Tier 1 vehicles that have not been
certified to the SFTP regulations. (See Table 3-3 earlier in this report.)
In this example, the benzene emission rates over the two cycles would be:
BNZFTP = 0.5 g/mi * 0.05 = 0.025 g/mi
BNZUC = 0.645 g/mi * 0.07 = 0.045 g/mi
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where BNZUC reflects the "in-use" benzene emission rate corrected for aggressive driving
behavior.
Continuing with this example, an off-cycle toxics adjustment factor can be developed
from the ratio of the benzene fraction over the UC to the benzene fraction over the FTP:
A-UJBNZ,uc/FTP ~~ "BNZ,UC'-"-BNZ,FTP
ADJBNZUC/FTP = 0.07/0.05 = 1.4.
Based on the Toxic-TOG curve approach described above (in which the FTP-based TOG
emission rate is used to establish the FTP-based toxic emission rate), determining the
FTP-based toxic emission rate is the first step in the overall calculation of in-use toxic
emission rates. Thus, in the example presented here, the starting point would be BNZFTP
= 0.025 g/mi. This value would then need to be corrected for aggressive driving behavior
(both for the TOG mass increase and the differential mass fraction between the FTP and
the UC), as shown below.
BNZUC BNZpj-p ADJAggressiveDriving ADJBNZjUC/Frp
BNZUC = 0.025 g/mi * 1.29 * 1.4
BNZUC = 0.045 g/mi
which corresponds with the "in-use" benzene emission rate in the example presented
above.
Using data collected by CARB in which vehicles were tested on both the FTP and the
UC, off-cycle toxics adjustment factors were developed for benzene, acetaldehyde,
formaldehyde, 1,3-butadiene, and MTBE based on the ratio of the toxic mass fraction
over the UC to the toxic mass fraction over the FTP. A complete description of the
database provided by CARB and the analysis performed for this study is contained in
Appendix F, and a summary of the results follows.
Summary of Analysis of CARB Off-Cycle Data - CARB provided speciated data for 18
FTP and UC test "pairs." The 18 test pairs reflect test results for a total of 13 vehicles
while operating on one or more of 3 test fuels (Indolene, commercial unleaded gasoline,
and California Phase 2 reformulated gasoline). Test results for one vehicle were
eliminated from all off-cycle toxics analyses because the FTP and UC test fuels were not
the same. Furthermore, to ensure that analysis results were not unduly biased by any one
particular vehicle, all test pairs applicable to a single vehicle were collapsed into a single
test pair by arithmetically averaging individual FTP and UC test results. With one
exception, test fuel sensitivities were not considered in the off-cycle analysis (i.e., all test
fuels were treated as a group) due to insufficient data. However, since analysis results are
expressed in a normalized form as the ratio of UC data to FTP data, most fuel-related
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distinctions should be controlled. A single exception was made for MTBE emissions,
where test results for zero MTBE content fuels (i.e., Indolene and one commercial
unleaded gasoline) were excluded from the estimation of UC to FTP ratios (for MTBE
only). Following this approach, the CARB database was collapsed into eight normal
THC emitter test pairs (seven for MTBE) and four high THC emitter test pairs.
Basic statistical regression analysis was performed on the CARB test data, primarily as a
quality assurance tool. The size of the normal and high emitter databases was sufficiently
small to prohibit the development of robust UC/FTP relationships through detailed
statistical analysis. Nevertheless, regression analysis was undertaken to check for data
consistency and the likelihood of an additive component (i.e., an emissions offset) in
UC/FTP relationships. For all species subjected to regression analysis (TOG, benzene,
1,3-butadiene, MTBE, formaldehyde, and acetaldehyde), the intercept terms in
regressions of UC emissions versus FTP emissions were not significant at the 95 percent
confidence level. Moreover, regression of the UC toxics fraction of TOG versus the FTP
toxics fraction of TOG for all five toxics species yielded similar results (i.e., insignificant
intercepts). Based on these results, it is unlikely that an additive component exists, and
the ratio of average UC test results to average FTP test results should provide a
reasonable estimation of UC/FTP emissions relationships. Therefore, the required
UC/FTP off-cycle toxics adjustment factors (ADJuc/Frp, as described above) were
calculated as the ratio of the mean of the toxics fractions over the UC to the mean of the
toxics fractions over the FTP. Appendix F provides additional detail on the basis for the
use of means, but in general calculated mean ratios were consistent with zero-intercept
regression coefficients to within an error of ±5 percent. Table 4-7 presents the specific
normal and high emitter off-cycle adjustment factors used for the toxics emissions
analysis.
Table 4-7
Ratio of UC Toxics Fraction to FTP Toxics Fraction
Toxic Species
Benzene
1,3 -Butadiene
MTBE
Formaldehyde
Acetaldehyde
Normal THC Emitters
1.315
1.037
0.825
1.163
1.020
High THC Emitters
1.126
0.708
0.965
0.894
0.919
Off-cycle adjustment factor development was obviously hampered by the limited amount
of data available for analysis. Ideally, separate adjustment factors would be developed for
the different vehicle technologies and classes represented in the fleet as well as the
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different fuels encountered in-use. However, independent adjustment factor development
was not possible given that only eight normal emitter test pairs (six LDVs and two LDTs
covering the 1984 through 1996 model years) and four high emitter test pairs (three
LDVs and one LDT covering the 1982 through 1987 model years) were available for
analysis. As a result, there was little alternative but to treat the database in the aggregate,
and develop a single set of adjustment factors for normal and high emitters which could
subsequently be weighted to develop unique model-year- and vehicle-class-specific
adjustments. Before this aggregate treatment, however, a basic regression analysis was
conducted on the 12 test pairs to determine whether a significant age-based relationship
was evident in the test data. The resulting regression coefficients were not significant for
any of the five emissions species examined; therefore, the aggregate treatment was
deemed acceptable and the normal and high emitter adjustment factors presented in
Table 4-7 were used without change for all 1981 and later gasoline-powered vehicles.
Because no data were available with which to generate factors for pre-1981 vehicles, two
different approaches were considered. First, because most of the pre-1981 model year
vehicles in the emissions analyses performed for this study would be high emitters based
on their HC emission rates, one possibility is to simply assign pre-1981 vehicles the high-
emitter factor. Alternatively, because no data exist on pre-1981 vehicles, it can also be
argued that a factor of 1.0 is appropriate. Because of the uncertainty involved in this
analysis, pre-1981 model year vehicles were assigned a value of 1.0 for the off-cycle
toxics factor.
For 1995 and later model year vehicles, the HC emission factors are such that few high
emitters are assumed to exist in the fleet, particularly for the I/M cases. Because of that,
the off-cycle toxics factor for these vehicles was assumed to be equal to the normal
emitter factor in Table 4-7.
For 1981 to 1994 model year vehicles, the normal and high emitter adjustment factors in
Table 4-7 were weighted according to the anticipated contribution of normals and highs
to the FTP-based HC emission rate. Because this is dependent on the calendar year of
analysis and whether an I/M program is in effect, a series of different factors were
developed. This was accomplished by forecasting the HC base emission rate equations
provided by EPA using the odometer level expected in 1990, 1996, and 2007. (The BERs
are discussed in detail in Section 3 of this report.) The methodology used to perform this
analysis is similar to that described in Section 3 for the implementation of normal and
high emitter CO oxygenate impacts; an example of the calculation follows.
The mean HC emission rate of the normal and high emitters in the FTP/UC sample was
0.23 g/mi and 1.77 g/mi, respectively. A 1984 model year vehicle, evaluated in 1996,
would have an average emission rate of 1.4 g/mi. Thus, the fraction of normals (using the
FTP/UC sample definition) can be calculated from the equation shown below.
1.4 g/mi = 0.23*N+1.77*(1-N)
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Solving for N, one arrives at 24% normals and 76% highs, with normals contributing
3.9% to the 1.4 g/mi emission rate (i.e., (0.23*0.24)71.4). Thus, for this case, the
weighted UC/FTP factor for benzene would be:
ADJBNZUC/FTP = 0.039*1.315 + 0.961*1.126= 1.133
This methodology was used to develop the UC/FTP toxics factors for 1981 to 1994 model
year light-duty vehicles for 1990, 1996, and 2007 non-I/M cases, and for 1990 and 1996
I/M cases. (The 1996 I/M case was used for the 2007 and 2020 runs, consistent with the
approach that EPA used to develop the off-cycle correction factors.) The results are
summarized in Appendix A with the TOG off-cycle corrections.
Air Conditioning Usage - For the quarters in which air conditioning is likely to be used
(i.e., spring and summer), an additional correction to the in-use toxic emission rates was
applied. Because air conditioning usage results in a relatively constant load on the
engine, it was assumed in this analysis that the FTP-based toxic fractions will apply to the
increased TOG mass as a result of air conditioning usage. Under this assumption, the
FTP-based toxic emission rate can be used directly in the calculation. Thus, the increase
in toxic emissions as a result of air conditioner usage was calculated as the difference
between the toxic emission rate with the full off-cycle correction applied (i.e., aggressive
driving + A/C) and the toxic emission rate with only an aggressive driving component
included. For the example above (i.e., a Tier 1 vehicle not certified to the SFTP
regulations), the two correction factors are calculated as follows.
ADJAggDn,= 1.29
ADJAggDrv + A/c= 1.29* 1.04 =1.342
Using the example above, the increase in benzene emissions as a result of air
conditioning usage would be calculated as shown below.
p * (1.342 - 1.29)
= 0.025 g/mi * (1.342 - 1.29) = 0.0013 g/mi
This result is then added to the BNZUC value calculated above for an overall in-use
benzene emission rate. At this point, the MOBILE model takes over and completes the
calculations (e.g., temperature corrections, travel fraction weighting, etc.).
Code Changes Required to Implement the Revised Exhaust Emissions Methodology -
The original T2ATTOX code provided by EPA was modified to implement the
methodologies described above. The original code structure ran the model for one toxic
emission factor at a time. We modified the structure so that all toxic emission factors
could be generated within the same run. This change was made to the subroutine
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HCCALX. In addition, the original code required that a multiplicative factor be input for
each toxic so that the ratio reflected the toxic emission rate per TOG exhaust emission
rate (i.e., it was structured to perform estimates by applying the toxic fraction to the
calculated TOG emission rates). This factor was used for all emission levels for a
particular model year and vehicle type. In the version of the model developed in this
study, the toxic-TOG relationship was described separately for low and high emitters in
terms of mg/mi toxic versus g/mi TOG. The TOG emission factor developed for a
particular run was then used to interpolate between the two relationships. This change
was implemented in the TOXADJ subroutine.
Other code changes were made to the GETTX2 routine to read in the toxic-TOG curves,
the aggressive driving factors, and the air conditioning factors. The OFFCYC subroutine
was modified to perform the aggressive driving and air conditioning corrections described
above. The BEF subroutine was modified to add calls to the TOXADJ and OFFCYC
subroutines. Two output routines (OUTDT3 and OUTDT4) were modified so that all the
toxic emission factors could be printed for each run. Subroutines SAVER and ADJUST
were modified so that the new toxic emission factors could be saved and corrected for
cases in which July runs were requested. For July runs the model is run twice, once with
the preceding Calendar year and then with the succeeding year. The two runs need to
saved and averaged for the July output. A listing of the subroutines modified for this
effort is presented in Appendix G, along with a description of how the model is run.
For acetaldehyde, formaldehyde, and 1,3-butadiene, crankcase emissions from tampered
vehicles are included in the exhaust emissions. For benzene and MTBE, the crankcase
emissions are calculated with hot-soak and diurnal emissions. Crankcase emissions from
correctly operating vehicles are zero, but for vehicles with inoperable PCV valves,
emissions need to be estimated. These emissions are calculated for all toxic compounds
and occur as combustion gases blow by the piston into the engine crankcase, so these
emissions are similar to exhaust emissions. The exhaust toxic fractions are applied for
estimating the toxic emission factors from crankcase emissions.
Evaporative Emissions
The only toxics included in the evaporative emissions estimates were benzene and
MTBE. For this analysis, the methodology originally developed for the T2ATTOX
model to estimate evaporative toxics estimates was used directly. In that method, the
mass fraction of benzene and MTBE (as a percent of total TOG emissions) is applied to
the evaporative TOG emissions estimates calculated by the MOBILE model.
The toxics fractions used in this analysis were based on the fuel property data specific to
each area and control scenario and the toxic-to-evaporative emissions relationships
provided by EPA (which came from the Complex model). A summary of the equations
relating fuel parameters to evaporative toxics fractions is given in Table 4-8 for each of
the evaporative processes modeled by MOBILE. Since the Complex model does not
calculate resting loss emissions, it was assumed that the benzene and MTBE fractions
were equal to those of diurnal emissions. Note that two sets of equations are given for
-47-
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MTBE. That is because a "high" and "low" evaporative MTBE estimate is included in
the MTBE model developed by EPA. Based on direction from EPA, the "high" MTBE
fractions were used in this analysis.
Table 4-8
Evaporative Benzene and MTBE Fraction Equations
from the Complex Model and EPA's MTBE Model
Pollutant
Benzene
MTBE
(High)
MTBE
(Low)
Process
Hot Soak
Diurnal
Running
Resting
Refueling
Hot Soak
Diurnal
Running
Resting
Refueling
Hot Soak
Diurnal
Running
Resting
Refueling
Toxic Fraction Equation (% of TOG)
(-0.03420*OXY - 0.080274*RVP + 1.4448)*BNZ
(-0.02895*OXY - 0.080274*RVP + 1.3758)*BNZ
(-0.03420*OXY - 0.080274*RVP + 1.4448)*BNZ
(-0.02895*OXY - 0.080274*RVP + 1.3758)*BNZ
(-0.02955*OXY - 0.081507*RVP + 1.3972)*BNZ
(24.205 - 1.746*RVP)*MTBE/10
(22.198 - 1.746*RVP)*MTBE/10
(17.8538 - 1.6622*RVP)*MTBE/10
(22.198 - 1.746*RVP)*MTBE/10
1.743*MTBE*(-0.02955*OXY - 0.081507*RVP + 1.3972)
((31.442 - 1.746*RVP)/1.8029)*MTBE/10
((31.442 - 1.746*RVP)/2.3191)*MTBE/10
((31.412 - 1.6622*RVP)/4.9963)*MTBE/10
((31.442 - 1.746*RVP)/2.3191)*MTBE/10
1.743*MTBE*(-0.02955*OXY - 0.081507*RVP + 1.3972)
Note: OXY = wt% oxygen
RVP = Reid vapor pressure in psi
BNZ = vol% benzene
MTBE = vol% MTBE
As with the exhaust emission factors, evaporative emission factors developed above were
read into the modified T2ATTOX model through subroutine GETTX2. The evaporative
fractions were developed for Benzene and MTBE for each of the evaporative components
described above. These fractions were then used to develop the evaporative toxic
emission factors in the subroutine EVPADJ. EVPADJ is called from the subroutine
HCCALX for each of the evaporative processes and for each toxic. The primary change
in the new model is that the evaporative emission factors for both the toxics are
calculated in the same run, rather than in separate runs.
Diesel Particulate Emissions
-48-
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Estimating Diesel particulate matter (PM) emission rates proved to be a much more
straightforward process than for the other toxic compounds considered in this study. For
this analysis, EPA's PARTS model was used directly. PARTS is similar in structure and
function to the MOBILE series of models, calculating exhaust and non-exhaust (e.g., road
dust) particulate emissions for each vehicle class included in the MOBILE models. Only
exhaust PM emission rates from Diesel vehicles were included in this analysis, and a
particle size cut-off of 10 jim was specified in the model inputs.
###
-49-
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5. DEVELOPMENT OF AREA-SPECIFIC MODEL INPUTS
The next step in estimating toxic exposure and risk estimates was to run the modified
T2ATTOX model. This required the development of input files specific to each area,
calendar year, season, and control scenario. As outlined above, nine urban areas and four
calendar years were evaluated in this study. For two of those calendar years (1990 and
1996), four seasons and a baseline control scenario were modeled. For the two forecast
years (2007 and 2020), four seasons and four control scenarios were modeled. For each
of these 360 modeling runs, it was necessary to determine the inputs needed and develop
input files for the revised T2ATTOX model. Because of the large number of modeling
runs, it was necessary to automate the process of constructing the input files as much as
possible to minimize potential errors in developing those inputs.
The input files for the revised T2ATTOX model include the same information required in
a standard MOBILESb run. Some of the inputs that were important to determine for each
urban area included in this study were the registration distributions, inspection and
maintenance program parameters (start year, stringency level, program type and
frequency, and vehicles tested), fuel RVP levels, and temperatures.
To determine all of the necessary input parameters for each city, several sources were
used. The first source of information was a group of input files developed by E. H.
Pechan (called the Trends input files12) which were provided to Radian and Sierra by
EPA. The Trends MOBILESb input files were developed for 13 selected areas, which
include the nine areas considered for this study. There were several Trends files for each
of the nine areas that represent different counties within that area. However, for this
analysis, only one file per area was desired. Therefore, it was necessary to choose one
county from each of the Trends files that best represented the city considered for the
study. Table 5-1 shows the cities considered in this study and the counties that were
selected from the Trends input files for each of these cities.
Specific MOBILE Inputs for This Study
Radian used the Trends input files and other information provided by EPA to determine
the area-specific input parameters. These parameters included registration fractions,
VMT mix, alternate basic emission rates (discussed in Section 3), inspection and
maintenance program parameters, Stage n refueling controls, and local area parameter
record inputs (fuel RVP and calendar year of evaluation). Summarized below are the
specific inputs used in this analysis.
-50-
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Table 5-1
Trend Files and Counties Selected for Each Modeled Urban Area
Urban
Area
Chicago
Denver
Houston
Minneapolis
New York
City
Philadelphia
Phoenix
Spokane
St. Louis
Counties
Cook, DuPage, and Lake Counties
Adams, Arapahoe, Boulder, Denver, and Jefferson
Counties
Harris County
Anoka, Carver, Dakota, Hennepin, Ramsey, Scott,
and Washington Counties
Bronx, Kings, Nassau, New York, Queens,
Richmond, Rockland, Suffolk, and Westchester
Counties
Bucks, Chester, Delaware, Montgomery, and
Philadelphia Counties
Maricopa County
Spokane County
Jefferson, St. Charles, St. Louis Counties, and St.
Louis City
Name of Selected
Trends File
M96 17031. IN
M9608001.IN
M9648201.IN
M9627003.IN
M9636005.IN
M9642017.IN
M9604013.IN
M9653063.IN
M9629099.IN
Registration Fractions - The registration fractions were determined for each city from two
sources. For the 1990 and 1996 modeling runs, the information provided for each city in
the Trends input files was used. For the 2007 and 2020 modeling runs, the registration
fractions included with the T2AT model were used. These registration fractions were
determined during the Tier II study.
VMT Mix - For the 1990 calendar year runs, the MOBILESb default VMT mix was used.
For the 1996 runs, EPA provided alternate VMT fractions for light-duty gas vehicles
(LDGVs), light-duty gas trucks 1 (LDGTls), and light-duty gas trucks 2 (LDGT2s) based
on the Tier 2 study. These 1996 VMTs for LDGVs, LDGTls, and LDGT2s were
combined with the default 1996 VMT mix from MOBILESb for the other five vehicle
classes to determine the VMT mix for 1996.
The VMT mixes for the baseline runs in 2007 and 2020 were calculated in a similar way.
The VMT split for the LDGVs, LDGTls, and LDGT2s were previously developed by
EPA for the Tier 2 Study. These numbers were combined with the MOBILESb defaults
for 2007 and 2020 to determine the baseline VMT mixes for 2007 and 2020.
For the increased light-duty Diesel truck penetration scenario in 2007 and 2020, the VMT
fractions for LDGTls, LDGT2s, and LDDTs were provided by EPA. These fractions
simply replaced those calculated for the baseline 2007 and 2020 runs. Table 5-2 shows
the VMT fractions each of the calendar years and scenarios.
-51-
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Table 5-2
VMT Fractions Used for the Toxics Analysis
Year
1996
2007
2020
2007
2020
Scenario
Baseline
Baseline
Baseline
Increased
Diesel
Increased
Diesel
LDGV
0.550
0.435
0.391
0.435
0.391
LDGT1
0.225
0.303
0.333
0.230
0.185
LDGT2
0.107
0.144
0.158
0.110
0.087
HDGV
0.035
0.032
0.031
0.032
0.031
LDDV
0.003
0.002
0.002
0.002
0.002
LDDT
0.002
0.002
0.004
0.109
0.223
HDDV
0.070
0.077
0.077
0.077
0.077
MC
0.008
0.005
0.004
0.005
0.004
Alternate TOG BERs - As discussed in Section 3, alternate BER were provided by EPA
for these modeling runs. Depending on the control scenario being modeled, these
alternate BERs were included in the input file. Table 5-3 shows the alternate BER files
which were used for each city, year, and scenario. Print-outs of these files are shown in
Appendix A.
Inspection and Maintenance (I/M) Program Parameters - The I/M program parameters
were determined from several sources. The first source was the Trends input files
developed by E.H. Pechan. Several pieces of information were also provided by EPA,
including the following:
Alternate credit files for 1981 and newer vehicles;13
An internal document listing I/M test type for each city and calendar year;14 and
A table outlining primary modeling elements for operating I/M programs
throughout the U.S.15
These four sources of information were used to determine the I/M program parameters for
this study. The I/M program parameters included the start year of the program, test type,
model years tested, vehicles tested, test frequency, test facility, waiver rates, and
compliance rate. In addition, the tampering rates calculated by MOBILESb were zeroed
out for I/M areas evaluated in 2007 and 2020. This is consistent with the approach taken
in the Tier 2 Study.
-52-
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Table 5-3
BER Input Files Used for Each Study Areas
City
Chicago
Denver
Houston
Minn.
New
York
Philly
Phoenix
Spokane
St. Louis
Scenario
Baseline
SC#1
SC#2,#3
Baseline
SC#1
SC#2,#3
Baseline
SC#1
SC#2,#3
Baseline
SC#1
SC#2,#3
Baseline
SC#1
SC#2,#3
Baseline
SC#1
SC#2,#3
Baseline
SC#1
SC#2,#3
Baseline
SC#1
SC#2,#3
Baseline
SC#1
SC#2,#3
1990
NTR_IM_B.BER
DNV_IM_B.BER
NTR_NO_B.BER
NTR_IM_B.BER
OTR_IM_B.BER
OTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_B.BER
1996
NTR_IM_B.BER
DNV_IM_B.BER
NTR_NO_B.BER
NTR_IM_B.BER
OTR_IM_B.BER
OTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_B.BER
2007
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_C.BER
DNV_IM_B.BER
DNV_IM_B.BER
DNV_IM_C.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_C.BER
NTR_NO_B.BER
NTR_NO_B.BER
NTR_NO_C.BER
OTR_IM_B.BER
OTR_IM_B.BER
OTR_IM_C.BER
OTR_IM_B.BER
OTR_IM_B.BER
OTR_IM_C.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_C.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_C.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR IM C.BER
2020
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_C.BER
DNV_IM_B.BER
DNV_IM_B.BER
DNV_IM_C.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_C.BER
NTR_NO_B.BER
NTR_NO_B.BER
NTR_NO_C.BER
OTR_IM_B.BER
OTR_IM_B.BER
OTR_IM_C.BER
OTR_IM_B.BER
OTR_IM_B.BER
OTR_IM_C.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_C.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR_IM_C.BER
NTR_IM_B.BER
NTR_IM_B.BER
NTR IM C.BER
Start year - The Trends input files for the original I/M program start year were used to
determine the I/M program start year. The only exception was for Minnesota's I/M
program. According to the Trends input files, the program started in 1990; however, it
was determined, based on information from the Minnesota DEQ, that the program
actually started in July 1991. For each city, the same I/M program start year was used for
all four calendar years of evaluation.
-53-
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Test type - For test type, information provided by EPA was used. Table 5-4 shows the
I/M test types that were provided by EPA. The only change to this information is in
Minneapolis for the calendar year 1990. According to information receive from EPA,
there was an I/M program 1990. However, as noted above, the I/M program did not start
until July 1991. Thus, the 1990 runs performed for this analysis did not include an I/M
program.
Table 5-4
I/M Test Type Information
City
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
1990
Idle
Idle
No I/M
No I/M
Idle
Idle
Idle
Idle
Idle
1996
Idle
Phase-in IM240
No I/M
Idle
Idle
Idle
Phase-in IM240
Idle
Idle
2007
Final IM240
Final IM240
Idle
No I/M
Phase-in IM240
Phase-in IM240
Final IM240
Phase-in IM240
Final IM240
2020
Final IM240
Final IM240
Final IM240
No I/M
Final IM240
Final IM240
Final IM240
Final IM240
Final IM240
Model years tested - For the model years covered in each I/M program, the information
provided in the Trends files was used. However, for LDGVs newer than 1994 and
LDGTs newer than 1996, the I/M program benefit was included in the alternate BERs.
Therefore, the I/M program in these input files was modeled to test only 1994 and older
LDGVs and 1996 and older LDGTs.
Test facility, test frequency, and vehicles tested- For these three parameters, two sources
of information were used. For the older calendar years (1990 and sometimes 1996), the
information was determined from the Trends input files. For 2007 and 2020, information
received from EPA was used instead.
Stringency, waiver rates, and compliance rates - The Trends input files were the only
source of information that contained any specific information about these three input
parameters.
Table 5-5 summarizes the source of information that determined each of the I/M program
parameters for this study.
-54-
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Table 5-5
I/M Program Parameters Information Sources by Calendar Year
Parameter
Model Years
Covered
Test type
Start Year,
Stringency,
Waiver Rates,
and Compliance
Rate
Test Facility,
Test Frequency,
and Vehicles
Tested
Calendar
Years
1990, 1996,
2007, and
2020
1990, 1996,
2007, and
2020
1990, 1996,
2007, and
2020
1990
1996
2007 and
2020
Source
Trends input files and information from EPA memo
concerning alternate credit files and alternate BERs.13
Information provided by Dave Sosnowski.14
Trends input files.
Trends input files.
Trends input files and information provided by Buddy
Polovick (for Denver, Minneapolis, and Phoenix only).15
Information provided by Buddy Polovick15
Evaporative System Functional Checks - One aspect of I/M that has been evolving over
the last several years is related to evaporative system functional checks. The practical
implementation of pressure and purge functional checks has had mixed success, and
many areas of the country are now considering a functional check of only the gas cap,
instead of the entire evaporative system.
For this study, evaporative control system functional checks in each area were modeled as
shown in Table 5-6. That table shows a breakdown of pressure, purge, and gas cap tests
for each city and calendar year used in this modeling. Two model year distinctions are
made in the table. That is because 1997 and newer model year vehicles are equipped with
enhanced evaporative control systems and onboard diagnostic (OBD) systems. (The
phase-in of these requirements actually spans several model years - 1997 was chosen as a
midpoint.) For this analysis, it was assumed that OBD would result in the identification
and repair of malfunctioning evaporative control systems that would be on par with the
pressure and purge test. At this point, however, this assumption is very subjective and
may overstate the benefits of the OBD system. Currently, very few data exist on the in-
use performance of OBD systems and the response of consumers to malfunction
identification. In addition, it is likely that the failure rates of vehicles certified to the
enhanced evaporative emission standards will decrease relative to the default values in
MOBILESb. Again, however, no data exist on the in-use performance of these systems.
For areas without an I/M program in the future (i.e., Minneapolis) it was assumed that
there is no benefit conferred by OBD.
-55-
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Table 5-6
Evaporative Checks by Calendar Year and Modeled Urban Area
Area
Chicago
Denver
Houston
Minneapolis
New York City
Philadelphia
Phoenix
Spokane
St. Louis
Model
Year
Pre-97
1997+
Pre-97
1997+
Pre-97
1997+
Pre-97
1997+
Pre-97
1997+
Pre-97
1997+
Pre-97
1997+
Pre-97
1997+
Pre-97
1997+
Functional Evap Checks by Calendar Year
1990
None
None
None
None
None
None
None
None
None
None
None
None
None
None
None
None
None
None
1996
None
None
None
None
None
None
None
None
None
None
None
None
None
None
None
None
None
None
2007
Cap
Pressure/Purge
Cap
Pressure/Purge
Cap
Pressure/Purge
None
None
Cap
Pressure/Purge
Pressure
Pressure/Purge
Pressure
Pressure/Purge
Cap
Pressure/Purge
Cap
Pressure/Purge
2020
Cap
Pressure/Purge
Cap
Pressure/Purge
Cap
Pressure/Purge
None
None
Cap
Pressure/Purge
Pressure
Pressure/Purge
Pressure
Pressure/Purge
Cap
Pressure/Purge
Cap
Pressure/Purge
For pre-1997 vehicles, a gas cap only or pressure test is specified in Table 5-6, which is
based on information received from EPA.15 A gas cap test was modeled as a 40% benefit
of a full pressure test. The test frequency for both the pressure and purge tests was
modeled as annual or biennial, depending on the inspection frequency of the I/M program
modeled for the area.
Stage II Refueling Controls - Consistent with the MOBILESb model, T2ATTOX requires
the user to input efficiency levels for areas that have Sage II refueling controls. Although
on-board refueling vapor recovery systems will be in place on the majority of vehicles in
the 2007 and 2020 runs, it is important to properly characterize Stage II efficiency in the
1990 and 1996 runs, as that is the only means of refueling control in those calendar years.
Information on Stage II programs and effectiveness was provided by Sierra based on a
study performed for the American Automobile Manufacturers Association in 1993.16
Table 5-7 summarizes the Stage II program efficiencies for each city and calendar year
that were used in the input files for this study.
-56-
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Table 5-7
Stage II Efficiencies by City and Calendar Year
Estimated Stage II Vapor Recovery Efficiency (%)
City
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Estimated Stage II Vapor Recovery Efficiency (%)
1990
0.0
0.0
0.0
0.0
82.6
0.0
0.0
0.0
85.5
1996
85.5
0.0
76.7
0.0
85.5
80.2
80.2
0.0
85.5
2007
85.5
0.0
85.5
0.0
85.5
80.2
80.2
0.0
85.5
2020
85.5
0.0
85.5
0.0
85.5
80.2
80.2
0.0
85.5
Local Area Parameter Record and Scenario Record Inputs - The information for the
parameters in the LAP record and the scenario record in each input file came from several
sources. The minimum and maximum daily temperatures were taken from the Trends
input files for 1990 and 1996. The 1996 temperatures were used for 2007 and 2020 as
well as for 1996. Based on correspondence with EPA, it was determined that the
temperatures for Winter, Spring, Summer, and Fall came from the Trends runs for
January, April, July, and October for each year, respectively. The spring and summer
months were evaluated for the current calendar year (e.g., 1990 for 1990, 1996 for 1996)
using a July-based run; the winter evaluation was performed for the current calendar year
based on a January evaluation date; and the fall evaluation was performed for the next
calendar year (e.g., 1991 for 1990, 1997 for 1996) using a January evaluation date.
The RVP levels were determined from the fuel properties provided to Sierra by EPA.
These RVP levels were provided for each city and year. The average speed of 19.6 mph
was determined through correspondence with EPA. Finally, the operating mode fractions
for VMT accumulated by non-catalyst vehicles in cold start mode, catalyst-equipped
vehicles in hot-start mode, and catalyst-equipped vehicles in cold-start mode were
determined from the Trends input files.
Area-Specific Toxic-TOG Curves
In addition to the standard MOBILE inputs described above, the toxic-TOG curves
described in Section 4 of this report had to be generated for each fuel scenario. In total,
there were 72 different fuel scenarios analyzed in this effort based on the following
parameters:
-57-
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Baseline fuel for 1990, 1996, and 2007/2020;
40 ppm sulfur fuel for 2007/2020;
Summer vs. winter; and
Nine modeled urban areas.
As described in Section 4, the toxic-TOG curves for each fuel were based on
relationships developed by EPA and on results from the Complex model. The fuel
parameters used in this analysis were provided by EPA and are summarized in Table 5-8.
(Note that the 2007 fuel properties listed in the table were also used for 2020.) From
these fuel specifications, TOG and toxic emission rates were developed for normal- and
high-emitting vehicles as a function of technology type, and a FORTRAN routine was
written to compile the technology-based results into model-year-specific factors for use in
the T2ATTOX model. A sample output from that routine is given in Appendix H for the
1990 Phoenix summertime fuel scenario.
EPA compiled the fuel parameters in Table 5-8 from a number of different sources. For
the 1990 and 1996 calendar years, the fuel properties for Chicago, Denver, Minneapolis,
New York, Philadelphia, Phoenix, and St. Louis came from fuel surveys conducted by the
American Automobile Manufacturers Association (AAMA). The Houston fuel properties
were from surveys conducted by the National Institute for Petroleum and Energy
Research (NIPER). For Spokane, AAMA survey results from Billings, Montana, were
used as a surrogate, and it was assumed that the Spokane oxygenated fuel requirement in
1996 was met by splash blending with ethanol.
Projections for future years were based on refinery modeling performed by EPA using the
1996 fuel properties in each area as a basis. If no new fuel programs were implemented,
the baseline 2007 and 2020 fuels were assumed to be the same as 1996. For RFG areas,
adjustments for the more stringent Phase n requirements (which begin in calendar year
2000) were made. To meet the Phase n RFG oxygen requirements (2.1 percent by
weight), ethanol was assumed to be blended into gasoline at 6.1 volume percent, MTBE
at 11.8 volume percent, or ETBE at 13.7 volume percent. Note that for older technology
vehicles, ETBE-specific equations were not available, and equations developed for
ethanol were used instead. This occurs only in the 2007 and 2020 summertime Chicago
runs, and the impact is very slight, since older technology vehicles have been removed
from the fleet by that time (except for the heavy-duty gasoline vehicle class).
-58-
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Table 5-8
Fuel Parameters Used in Toxics Emissions Analysis
(Continued)
Area
Chicago
Chicago
Chicago
Chicago
Chicago
Chicago
Chicago
Chicago
Denver
Denver
Denver
Denver
Denver
Denver
Denver
Denver
Houston
Houston
Houston
Houston
Houston
Houston
Houston
Houston
Minneapolis
Minneapolis
Minneapolis
Minneapolis
Minneapolis
Minneapolis
Minneapolis
Minneapolis
New York
New York
New York
New York
New York
New York
New York
New York
Kl-tj Meaf
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
No
No
No
No
No
No
No
No
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
No
No
No
No
No
No
No
No
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Year
1990
1990
1996
1996
2007
2007
2007
2007
1990
1990
1996
1996
2007
2007
2007
2007
1990
1990
1996
1996
2007
2007
2007
2007
1990
1990
1996
1996
2007
2007
2007
2007
1990
1990
1996
1996
2007
2007
2007
2007
Season
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Scenario
Baseline
Baseline
Baseline
Baseline
Baseline
Baseline
40 ppm
40 ppm
Baseline
Baseline
Baseline
Baseline
Baseline
Baseline
40 ppm
40 ppm
Baseline
Baseline
Baseline
Baseline
Baseline
Baseline
40 ppm
40 ppm
Baseline
Baseline
Baseline
Baseline
Baseline
Baseline
40 ppm
40 ppm
Baseline
Baseline
Baseline
Baseline
Baseline
Baseline
40 ppm
40 ppm
KVK, psi
8.7
13.7
7.9
14.0
6.6
14.0
6.6
14.0
8.3
12.1
8.8
13.6
8.8
13.6
8.8
13.8
8.3
12.8
7.1
12.8
6.8
12.8
6.4
12.8
9.5
13.2
9.6
14.9
9.6
14.9
9.6
13.8
8.3
13.3
8.0
13.2
6.8
13.2
6.6
13.2
Aromatics
28.8
23.0
26.0
22.4
25.6
21.4
26.9
19.7
24.8
19.3
27.1
21.9
27.1
21.9
26.9
21.8
30.2
23.0
27.4
21.1
27.0
20.2
28.4
18.6
29.8
24.9
28.2
23.4
28.2
23.4
28.0
23.2
31.9
26.4
28.6
23.3
28.1
22.3
29.6
20.5
Uletms
8.6
9.1
9.7
7.8
7.4
6.4
4.4
3.1
12.2
12.8
8.8
9.2
8.8
9.2
4.6
4.7
10.9
14.4
13.0
12.8
9.8
10.5
5.9
5.1
8.3
9.3
7.3
5.3
7.3
5.3
3.9
2.7
13.9
16.7
17.1
16.6
11.3
13.7
7.8
6.7
benzene %
1.35
1.69
0.96
0.80
0.96
0.80
0.96
0.80
1.41
1.23
1.33
0.94
1.33
0.94
1.33
0.94
1.36
1.22
0.71
0.70
0.71
0.70
0.71
0.70
1.69
1.86
1.81
1.65
1.81
1.65
1.81
1.65
1.08
1.55
0.51
0.47
0.51
0.47
0.51
0.47
bultur
512
450
492
523
150
150
40
40
375
272
296
350
296
350
40
40
375
454
261
224
145
150
40
40
422
701
121
70
121
70
40
40
367
274
231
267
115
150
40
40
b^UU %
47.2
54.4
50.2
58.0
51.8
56.8
50.0
55.9
45.1
62.0
50.1
62.1
50.1
62.1
52.7
61.5
46.7
52.4
47.8
59.9
49.3
58.6
47.6
57.7
45.9
56.0
59.4
62.3
59.4
62.3
62.5
61.7
43.1
49.5
49.8
57.5
52.1
56.2
49.6
55.3
L3UU %
78.6
82.6
80.8
83.9
82.8
85.9
81.5
88.2
79.4
85.5
83.1
88.1
83.1
88.1
83.8
88.5
79.4
80.2
79.8
83.8
81.8
85.8
80.4
88.1
78.9
81.6
84.6
89.1
84.6
89.1
85.3
89.6
78.8
81.8
81.5
85.7
84.3
87.7
82.2
90.1
M I bb %
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
11.6
0.0
0.0
0.0
0.0
0.0
0.0
0.5
0.0
9.8
7.9
11.8
11.8
11.8
11.8
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
2.4
0.0
10.6
14.5
11.8
15.0
11.8
15.0
b I bb %
0.0
0.0
0.0
0.0
13.7
0.0
13.7
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
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
0.0
0.0
0.0
0.0
0.0
0.0
0.0
btUM %
0.0
0.0
9.0
9.0
0.0
9.0
0.0
9.0
0.0
0.0
0.0
8.4
0.0
8.4
1.5
8.4
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
9.4
8.0
9.4
8.0
9.3
8.1
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
uxygen wt
0.00
0.00
3.12
3.11
2.10
3.10
2.10
3.10
0.00
2.06
0.00
2.90
0.00
2.90
0.50
2.90
0.10
0.00
1.74
1.41
2.10
2.10
2.10
2.10
0.00
0.00
3.24
2.77
3.24
2.77
3.20
2.80
0.42
0.00
1.89
2.58
2.10
2.70
2.10
2.70
-------
Table 5-8
Fuel Parameters Used in Toxics Emissions Analysis
(Continued)
Area
Philadelphia
Philadelphia
Philadelphia
Philadelphia
Philadelphia
Philadelphia
Philadelphia
Philadelphia
Phoenix
Phoenix
Phoenix
Phoenix
Phoenix
Phoenix
Phoenix
Phoenix
Spokane
Spokane
Spokane
Spokane
Spokane
Spokane
Spokane
Spokane
St. Louis
St. Louis
St. Louis
St. Louis
St. Louis
St. Louis
St. Louis
St. Louis
Kl-tj Meaf
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
No
No
No
No
No
No
No
No
No
No
No
No
Yes
Yes
Yes
Yes
Year
1990
1990
1996
1996
2007
2007
2007
2007
1990
1990
1996
1996
2007
2007
2007
2007
1990
1990
1996
1996
2007
2007
2007
2007
1990
1990
1996
1996
2007
2007
2007
2007
Season
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Summer
Winter
Scenario
Baseline
Baseline
Baseline
Baseline
Baseline
Baseline
40 ppm
40 ppm
Baseline
Baseline
Baseline
Baseline
Baseline
Baseline
40 ppm
40 ppm
Baseline
Baseline
Baseline
Baseline
Baseline
Baseline
40 ppm
40 ppm
Baseline
Baseline
Baseline
Baseline
Baseline
Baseline
40 ppm
40 ppm
KVK, psi
8.4
13.9
7.9
13.5
6.7
13.5
6.6
13.5
8.1
10.9
6.8
8.7
7.0
8.7
7.0
8.7
8.6
13.1
8.7
14.8
8.7
14.8
8.7
14.8
8.8
13.2
6.8
13.6
6.4
13.6
6.4
13.8
Aromatics
29.2
23.5
29.0
25.4
28.6
24.3
30.1
22.4
33.0
26.4
36.1
34.3
21.9
21.9
21.9
21.9
21.0
19.2
28.5
18.6
28.5
18.5
28.3
18.4
28.9
22.0
29.9
23.8
29.4
22.4
29.7
23.6
Uletms
13.7
13.2
12.3
10.2
9.2
8.4
5.7
4.1
5.9
5.6
6.8
7.1
4.1
4.1
4.1
4.1
8.0
10.3
8.3
6.9
8.3
6.9
4.4
3.5
8.9
11.4
12.0
11.4
10.8
9.9
6.4
5.8
benzene %
0.86
1.63
0.80
0.63
0.80
0.63
0.80
0.62
2.15
1.88
1.07
1.40
0.55
0.69
0.55
0.69
1.36
1.58
1.32
0.97
1.32
0.96
1.32
1.00
1.11
1.71
0.70
0.89
0.69
0.89
0.69
0.89
bultur
371
206
367
337
135
150
40
40
123
157
118
216
20
20
20
20
739
698
412
350
412
346
40
40
372
319
492
535
145
150
40
40
b^UU %
43.6
50.5
51.2
59.3
52.9
58.0
51.0
57.1
41.1
56.5
45.7
50.2
49.8
55.1
49.8
55.1
46.6
51.1
45.0
59.8
45.0
60.2
47.3
59.6
45.2
54.0
39.0
52.7
44.2
52.5
43.2
52.2
L3UU %
79.0
82.9
81.8
85.9
83.9
88.0
82.5
90.4
78.5
82.9
76.2
82.6
84.7
84.7
84.7
84.7
82.6
84.9
81.4
87.1
81.4
87.2
82.0
87.6
78.9
82.7
78.8
82.6
83.5
84.7
83.5
83.0
M I bb %
0.0
0.0
11.3
8.8
11.8
11.8
11.8
11.8
0.0
11.4
0.8
0.0
11.8
15.0
11.8
15.0
0.0
0.0
0.0
0.0
0.0
0.0
2.8
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
b I bb %
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
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
0.0
0.0
13.7
0.0
13.7
0.0
btUM %
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
10.2
0.0
0.0
0.0
0.0
0.0
0.0
0.0
9.3
0.0
10.2
0.0
10.2
0.0
0.0
0.0
0.0
0.0
6.1
0.0
6.1
uxygen wt
0.00
0.00
2.01
1.58
2.10
2.10
2.10
2.10
0.00
2.04
0.14
3.53
2.10
2.70
2.10
2.70
0.00
0.00
0.00
3.20
0.00
3.50
0.50
3.50
0.00
0.00
0.00
0.00
2.10
2.10
2.10
2.10
-------
Area-Specific Evaporative Benzene and MTBE Fractions
The methodology described in Section 4 to determine benzene and MTBE evaporative
fractions was applied to the fuel data in Table 5-8. Because the same fractions are
applied to all technologies, the evaporative input file for the T2ATTOX runs consists of
only two lines of data - one reflecting benzene fractions and one reflecting MTBE
fractions. These fractions are applied to the TOG emissions from the appropriate
evaporative process (e.g., hot soak, diurnal, etc.). A sample evaporative fraction input
file for 1990 Phoenix summertime fuel is presented in Appendix I.
Input File Development
All of the area-specific inputs (the MOBILES flags, registration fractions, VMT mix, I/M
program parameters, etc.) were entered into a Microsoft Access database. Several
different tables were created in the database, one for each group of input parameters (e.g.,
one table for input flags, another for I/M parameters). Once all values had been entered,
each of the inputs was checked for accuracy.
Input File "Builder" Routine - In order to transfer the information from the Access table
to the ASCII T2ATTOX input files, Radian developed an input file "builder" routine in a
Visual Basic module in Access. This Visual Basic module read in the information from
each table, created an input file for each city, year, season, and control scenario, and
wrote the relevant information from the Access tables into the correct format in the input
file. The automated process of developing the input files reduced the number of times
that parameters needed to be typed into an ASCII file and significantly reduced the risk of
transcription errors. Appendix J shows an example input file (a selected file for Phoenix)
that was developed by the input file "builder" routine.
Modeling Runs - Once the input files were built for each city, year, season, and control
scenario, the modified T2ATTOX model was run for each file. An output file from the
model is contained in Appendix K, which shows the results based on the Phoenix input
file presented in Appendix J. A FORTRAN program was developed to process the output
files and condense the results into one large data file for later computation of toxics
exposure described in the next section of this report.
PARTS Input Files
The PARTS input files were developed using many of the same sources that were used
for the Toxics input files. The registration fractions used for the T2ATTOX model were
also used for the PARTS input files. The registration fractions for HDDVs were used for
each of the heavy-duty vehicle classes in PARTS.
The VMT mixes from the Toxics inputs were also used for the PARTS input files. The
HDDV VMT fraction was broken down into the five VMT fractions (2BHDDV,
-61-
-------
LHDDV, MHDDV, HHDDV, and buses) using the ratios that were included in the
examples in the PARTS User's Guide (i.e., standard model output). For example, the
1996 VMT fraction for HDDV was 0.070. This number was broken down into five VMT
fractions based on the ratios of 15.8%, 1.6%, 22.2%, 54.0%, and 6.4% for 2BHDDV,
LHDDV, MHDDV, HHDDV, and buses, respectively. The resulting VMT fractions were
0.01, 0.001, 0.014, 0.034, and 0.004 for each of these vehicle classes.
Other inputs for the PARTS files, such as percent of paved and unpaved silt, number of
precipitation days, and particle size cutoff, were taken from the Trends PARTS input
files.
Results from the PARTS runs were also summarized into a single output file for later use
in the exposure and risk analyses.
###
-62-
-------
6. MOTOR VEHICLE TOXICS EMISSIONS ESTIMATES
Using the methodologies and models described above, estimates of on-road motor vehicle
toxics emission rates were prepared for benzene, acetaldehyde, formaldehyde,
1,3-butadiene, MTBE, and Diesel PM. As described in the preceding section, emission
rates were generated for each quarter and for each vehicle class. In addition, annual
average estimates were prepared by taking the mean of the quarterly results. Consistent
with the requirements of this study, toxics emissions estimates were prepared for
(a) calendar years 1990, 1996, 2007, and 2020; (b) baseline emission factors and fuels
(for all calendar years); (c) three control scenarios (for 2007 and 2020); and (d) nine
urban areas.
Fleet-average emission results (i.e., all vehicle classes combined) are given in Tables 6-1
through 6-6 for benzene, acetaldehyde, formaldehyde, 1,3-butadiene, MTBE, and Diesel
PM, respectively. Because of the voluminous nature of these estimates, results are
presented only for Chicago and Phoenix; the complete set of toxics emission rates
calculated in this study is contained in Volume n of this report. Recall that the control
scenarios consisted of:
Scenario 1 - baseline emission factors (which include a national LEV program)
with a national 40 ppm gasoline sulfur limit;
Scenario 2 - Scenario 1 with more stringent NMHC standards for 2004 and later
model year light-duty cars and trucks; and
Scenario 3 - Scenario 2 with increased Diesel light-duty truck penetration
beginning in 2004, with 50% of new light-truck sales being Diesel in 2007.
Reviewing the fleet-average toxics emission factors in Tables 6-1 to 6-6, the following
observations can be made:
Significant reductions in fleet-average toxics emissions are observed between
1990 and 2020 with no further vehicle or fuel controls. This is a result of fleet-
turnover resulting in full implementation of the federal emission control
regulations currently on the books.
Toxic emissions in Chicago are typically at a minimum in summer. This is a
result of elevated exhaust hydrocarbon emissions (which are directly related to
most toxics emissions rates) in winter and fall due to cold temperature. However,
the
-63-
-------
Table 6-1
On-Road Motor Vehicle Benzene Emission Rates
for Chicago and Phoenix
(Units: mg/mi)
Area
Chicago
Phoenix
Quarter
Winter
Spring
Summer
Fall
Ann Ave
Winter
Spring
Summer
Fall
Ann Ave
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990 CO
Emissions
43.8
43.8
43.8
43.8
35.8
35.8
35.8
35.8
33.2
33.2
33.2
33.2
36.3
36.3
36.3
36.3
37.3
37.3
37.3
37.3
29.3
29.3
29.3
29.3
31.4
31.4
31.4
31.4
42.3
42.3
42.3
42.3
31.6
31.6
31.6
31.6
33.7
33.7
33.7
33.7
Calendar Year
1990
144.1
...
...
...
117.2
...
...
...
101.2
...
...
...
116.1
...
...
...
119.7
...
...
118.2
...
...
...
130.7
...
...
...
166.1
...
...
...
122.7
...
...
...
134.4
...
...
1996
74.6
...
...
...
49.9
...
...
...
40.7
...
...
...
48.1
...
...
...
53.3
...
...
76.6
...
...
...
63.2
...
...
...
78.0
...
...
...
67.2
...
...
...
71.2
...
...
2007
33.6
30.5
29.0
25.6
22.0
21.8
20.8
18.6
18.1
17.9
17.2
15.6
23.3
21.7
20.8
18.7
24.2
23.0
21.9
19.6
19.8
19.8
19.0
17.2
13.7
13.7
13.2
12.1
16.6
16.6
16.0
14.5
16.6
16.6
15.8
14.3
16.7
16.7
16.0
14.6
2020
20.2
18.1
13.1
10.1
13.5
12.9
9.6
7.7
11.0
10.6
8.1
6.7
15.0
13.8
10.9
8.8
14.9
13.8
10.4
8.3
11.6
11.6
8.7
7.0
8.4
8.4
6.5
5.4
10.0
10.0
7.8
6.4
10.5
10.5
7.9
6.5
10.1
10.1
7.7
6.4
-------
Table 6-2
On-Road Motor Vehicle Acetaldehyde Emission Rates
for Chicago and Phoenix
(Units: mg/mi)
Area
Chicago
Phoenix
Quarter
Winter
Spring
Summer
Fall
Ann Ave
Winter
Spring
Summer
Fall
Ann Ave
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990 CO
Emissions
43.8
43.8
43.8
43.8
35.8
35.8
35.8
35.8
33.2
33.2
33.2
33.2
36.3
36.3
36.3
36.3
37.3
37.3
37.3
37.3
29.3
29.3
29.3
29.3
31.4
31.4
31.4
31.4
42.3
42.3
42.3
42.3
31.6
31.6
31.6
31.6
33.7
33.7
33.7
33.7
Calendar Year
1990
21.5
...
...
...
18.1
...
...
...
15.7
...
...
...
16.2
...
...
...
17.9
...
...
17.9
...
...
...
15.2
...
...
...
16.9
...
...
...
15.3
...
...
...
16.3
...
...
1996
25.4
...
...
...
17.0
...
...
...
14.0
...
...
...
14.8
...
...
...
17.8
...
...
20.1
...
...
...
9.6
...
...
...
10.6
...
...
...
16.4
...
...
...
14.2
...
...
2007
11.1
10.7
10.3
9.5
6.6
6.5
6.3
6.1
5.5
5.4
5.3
5.2
6.3
6.1
5.9
5.7
7.4
7.2
6.9
6.6
4.2
4.2
4.2
4.3
3.6
3.6
3.5
3.7
3.8
3.8
3.7
3.9
3.5
3.5
3.4
3.5
3.8
3.8
3.7
3.9
2020
6.0
5.7
4.5
4.0
4.0
3.8
3.2
3.0
3.4
3.3
2.8
2.7
4.1
3.9
3.2
3.1
4.4
4.2
3.4
3.2
2.5
2.5
2.2
2.3
2.3
2.3
2.0
2.2
2.4
2.4
2.1
2.2
2.3
2.3
2.0
2.2
2.4
2.4
2.1
2.2
-------
Table 6-3
On-Road Motor Vehicle Formaldehyde Emission Rates
for Chicago and Phoenix
(Units: mg/mi)
Area
Chicago
Phoenix
Quarter
Winter
Spring
Summer
Fall
Ann Ave
Winter
Spring
Summer
Fall
Ann Ave
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990 CO
Emissions
43.8
43.8
43.8
43.8
35.8
35.8
35.8
35.8
33.2
33.2
33.2
33.2
36.3
36.3
36.3
36.3
37.3
37.3
37.3
37.3
29.3
29.3
29.3
29.3
31.4
31.4
31.4
31.4
42.3
42.3
42.3
42.3
31.6
31.6
31.6
31.6
33.7
33.7
33.7
33.7
Calendar Year
1990
66.8
...
...
...
55.4
...
...
...
48.4
...
...
...
50.1
...
...
...
55.2
...
...
71.1
...
...
...
49.3
...
...
...
54.8
...
...
...
60.1
...
...
...
58.9
...
...
1996
39.8
...
...
...
28.2
...
...
...
24.4
...
...
...
25.2
...
...
...
29.4
...
...
35.5
...
...
...
30.1
...
...
...
33.5
...
...
...
29.2
...
...
...
32.0
...
...
2007
18.1
18.0
17.5
17.2
12.4
12.4
12.0
12.4
10.7
10.7
10.5
.1
.3
.3
.0
.3
13.1
13.1
12.8
13.0
15.3
15.3
15.0
15.1
12.1
12.1
11.9
12.3
13.1
13.1
12.8
13.1
11.9
11.9
11.6
11.9
13.1
13.1
12.8
13.1
2020
10.1
10.1
8.3
8.1
7.6
7.6
6.5
6.7
6.7
6.7
5.9
6.3
7.5
7.4
6.4
6.7
8.0
8.0
6.8
6.9
8.2
8.2
7.1
7.3
7.2
7.2
6.3
6.7
7.7
7.7
6.6
6.9
7.6
7.6
6.6
6.9
7.7
7.7
6.7
6.9
-------
Table 6-4
On-Road Motor Vehicle 1,3-Butadiene Emission Rates
for Chicago and Phoenix
(Units: mg/mi)
Area
Chicago
Phoenix
Quarter
Winter
Spring
Summer
Fall
Ann Ave
Winter
Spring
Summer
Fall
Ann Ave
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990 CO
Emissions
43.8
43.8
43.8
43.8
35.8
35.8
35.8
35.8
33.2
33.2
33.2
33.2
36.3
36.3
36.3
36.3
37.3
37.3
37.3
37.3
29.3
29.3
29.3
29.3
31.4
31.4
31.4
31.4
42.3
42.3
42.3
42.3
31.6
31.6
31.6
31.6
33.7
33.7
33.7
33.7
Calendar Year
1990
20.4
...
...
...
16.9
...
...
...
14.0
...
...
...
14.5
...
...
...
16.5
...
...
14.3
...
...
...
13.6
...
...
...
15.4
...
...
...
11.6
...
...
...
13.7
...
...
1996
10.0
...
...
...
7.3
...
...
...
5.8
...
...
...
5.7
...
...
...
7.2
...
...
8.0
...
...
...
7.6
...
...
...
8.7
...
...
...
6.3
...
...
...
7.7
...
...
2007
4.2
3.8
3.7
3.6
2.9
2.7
2.6
2.6
2.3
2.2
2.1
2.2
2.4
2.2
2.1
2.2
3.0
2.7
2.6
2.6
2.5
2.5
2.4
2.5
2.1
2.1
2.0
2.1
2.3
2.3
2.3
2.3
2.0
2.0
1.9
2.0
2.2
2.2
2.2
2.2
2020
2.9
2.5
2.0
1.8
2.1
.9
.6
.4
.7
.6
.3
.2
.8
.6
.3
.3
2.1
.9
.6
.4
.7
.7
.4
.3
.5
.5
.3
.2
.7
.7
.4
.3
.5
.5
.2
.2
.6
.6
.3
.3
-------
Table 6-5
On-Road Motor Vehicle MTBE Emission Rates
for Chicago and Phoenix
(Units: mg/mi)
Area
Chicago
Phoenix
Quarter
Winter
Spring
Summer
Fall
Ann Ave
Winter
Spring
Summer
Fall
Ann Ave
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990 CO
Emissions
43.8
43.8
43.8
43.8
35.8
35.8
35.8
35.8
33.2
33.2
33.2
33.2
36.3
36.3
36.3
36.3
37.3
37.3
37.3
37.3
29.3
29.3
29.3
29.3
31.4
31.4
31.4
31.4
42.3
42.3
42.3
42.3
31.6
31.6
31.6
31.6
33.7
33.7
33.7
33.7
Calendar Year
1990
0.0
...
...
...
0.0
0.0
0.0
0.0
149.0
...
...
...
0.0
0.0
261.8
...
...
...
102.7
...
...
1996
0.0
...
...
...
0.0
0.0
0.0
0.0
0.0
5.9
...
...
...
10.1
0.0
4.0
...
...
2007
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
0.0
0.0
0.0
0.0
0.0
0.0
0.0
40.6
40.6
40.3
34.6
33.9
33.9
33.6
29.3
61.8
61.8
61.5
53.6
55.7
55.7
55.4
48.5
48.0
48.0
47.7
41.5
2020
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
0.0
0.0
0.0
0.0
0.0
0.0
0.0
23.4
23.4
22.0
16.6
19.3
19.3
18.3
14.2
33.7
33.7
32.7
25.1
32.6
32.6
31.4
24.5
27.3
27.3
26.1
20.1
-------
Table 6-6
On-Road Motor Vehicle Diesel PM Emission Rates
for Chicago and Phoenix
(Units: mg/mi)
Area
Chicago
Phoenix
Quarter
Winter
Spring
Summer
Fall
Ann Ave
Winter
Spring
Summer
Fall
Ann Ave
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990 CO
Emissions
43.8
43.8
43.8
43.8
35.8
35.8
35.8
35.8
33.2
33.2
33.2
33.2
36.3
36.3
36.3
36.3
37.3
37.3
37.3
37.3
29.3
29.3
29.3
29.3
31.4
31.4
31.4
31.4
42.3
42.3
42.3
42.3
31.6
31.6
31.6
31.6
33.7
33.7
33.7
33.7
Calendar Year
1990
93.6
...
...
...
94.6
...
...
...
94.6
...
...
...
91.3
...
...
...
93.5
...
...
92.7
...
...
...
94.0
...
...
...
94.0
...
...
...
90.6
...
...
...
92.9
...
...
1996
55.3
...
...
...
55.3
...
...
...
55.3
...
...
...
48.5
...
...
...
53.6
...
...
62.7
...
...
...
62.7
...
...
...
62.7
...
...
...
56.5
...
...
...
61.2
...
...
2007
23.8
23.8
23.8
39.7
23.8
23.8
23.8
39.7
23.8
23.8
23.8
39.7
22.0
22.0
22.0
35.8
23.4
23.4
23.4
38.7
23.8
23.8
23.8
39.7
23.8
23.8
23.8
39.7
23.8
23.8
23.8
39.7
22.0
22.0
22.0
35.8
23.4
23.4
23.4
38.7
2020
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
17.4
17.4
17.4
41.3
-------
opposite is true of the Phoenix runs. Because the fall and winter temperatures are
relatively mild in Phoenix, large increases in exhaust hydrocarbon emissions as a
result of cold temperature are not observed. In fact, the very high summer
temperatures result in both increased evaporative emissions (causing increases in
benzene and MTBE, when present) and increased exhaust emissions (as a result of
increased vapor from canister purge).
Implementation of Scenario 1 has no impact on the Phoenix runs. That is because
it was assumed that Phoenix would continue to use CARB "Cleaner Burning
Gasoline" (CBG), which already has sulfur levels below 40 ppm on average.
For the Chicago runs, Scenario 1 has the largest impact on benzene and
1,3-butadiene emissions. Aldehyde emissions are less affected under this
scenario.
Because it is assumed that gasoline dispensed in Chicago will use either ETBE or
ethanol as an oxygenate, MTBE emission rates are zero for all scenarios.
Moderate reductions are observed with Scenario 2 in 2007. However, by 2020
fleet-turnover impacts result in fleet-average toxic emission reductions on the
order of 15% to 25%.
Implementation of Scenario 3 results in reductions in benzene, acetaldehyde,
1,3-butadiene, and MTBE (where used). However, formaldehyde emissions show
a slight increase. Obviously, Diesel PM emissions increase substantially under
this scenario.
###
-70-
-------
7. TOXICS EXPOSURE ESTIMATES
Using the motor vehicle toxics emission rates described in the previous section of this
report, CO exposure estimates prepared with the HAPEM-MS model, and the 1990 CO
emission rates generated for each of the study areas, exposure estimates were calculated
for all study areas and scenarios evaluated in this effort. As described in Section 2, the
approach used to estimate toxics exposure was based on the following formula:
TOXExposure(tlg/m3) LCOExposure(tlg/m3)/COEF(g/mi)J1990 x TOXEF(g/mi)
where TOX reflects one of the six toxic pollutants considered in this study. Because some
of the toxic pollutants evaluated in this study (e.g., 1,3-butadiene) have a different
photochemical reactivity than CO, the exposure concentrations were adjusted to account
for atmospheric transformation. In addition, because the CO ratios are based on the 1990
calendar year, an adjustment was made to account for the increase in VMT relative to
1990.
Details of the calculations performed to generate exposure estimates for this study are
described below. Estimates were prepared for three specific demographic groups:
outdoor workers, children 0 to 17 years of age, and the total population. These groups
were selected because outdoor workers are generally the highest exposed demographic
group, children 0 to 17 represent a very sensitive demographic group, and the total
population gives an average exposure estimate.
1990 CO Exposure Estimates
The calendar year 1990 CO exposure estimates related to on-road motor vehicles were
provided to Sierra by EPA. Those estimates, which are summarized in Table 7-1, were
based on a recent study performed by Mantech Environmental Technology under contract
to EPA.17 That study used the Hazardous Air Pollutant Exposure Model (HAPEM) to
generate estimates of human exposure to ambient CO. The HAPEM model links human
activity patterns with ambient CO concentration to arrive at average exposure estimates
for 22 different demographic groups (e.g., outdoor workers, children 0 to 17, working
men 18 to 44, women 65+, etc.) and for the total population. The model simulates the
movement of individuals between home and work and through a number of different
microenviroments (37 in total). The CO concentration in each microenvironment is
determined by multiplying ambient concentration by a microenvironmental factor. For
example, a factor of 0.38 is used for time spent in an office building, while a factor of
2.11 is used for time spent in a shopping mall.
-71-
-------
Table 7-1
1990 On-Road Motor Vehicle CO Exposure Estimates (jig/m3)
Urban
Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Demo
Group
Outdoor Workers
Children 0-17
Total Population
Outdoor Workers
Children 0-17
Total Population
Outdoor Workers
Children 0-17
Total Population
Outdoor Workers
Children 0-17
Total Population
Outdoor Workers
Children 0-17
Total Population
Outdoor Workers
Children 0-17
Total Population
Outdoor Workers
Children 0-17
Total Population
Outdoor Workers
Children 0-17
Total Population
Outdoor Workers
Children 0-17
Total Population
Quarter
1
455
366
375
696
556
569
305
258
262
872
698
724
947
764
793
608
508
515
685
591
596
795
636
651
374
302
309
2
344
286
290
358
289
295
235
193
197
593
489
497
771
637
658
343
297
295
360
308
310
458
367
370
245
204
205
3
317
261
261
364
294
297
388
322
322
538
442
446
662
548
561
337
284
280
449
378
374
713
568
566
197
166
165
4
378
309
316
628
508
518
429
370
373
681
550
566
751
612
636
444
379
381
757
649
654
745
592
606
313
268
269
-72-
-------
With the CO exposure estimates generated by HAPEM model, EPA determined the
fraction of exposure that was a result of on-road motor vehicles. This was accomplished
by scaling the annual and quarterly exposure estimates prepared by Mantech (which
reflect exposure to total ambient CO) by the fraction of the 1990 CO emissions inventory
that was from on-road motor vehicles. The inventory estimates used for this purpose
were prepared by E.H. Pechan under contract to EPA.18 A spreadsheet with the exposure
results was provided to Sierra; the results were then summarized in an ASCII file that was
used as an input to a FORTRAN routine that compiled the exposure data, CO emissions
data, and the toxics emissions data to calculate toxics exposure and risk for each of the
urban areas and scenarios included in this study. The exposure estimates given in Table
7-1 reflect the adjustment to account only for on-road motor vehicles.
CO Emissions Estimates
As outlined above, the calendar year 1990 fleet-average CO emission rate is used in the
toxics exposure calculation. These CO estimates were prepared with a modified version
of the T2ATTOX model, which is described in Section 3 of this report. (Changes to the
current MOBILESb inputs were made to account for revised base emission rates, off-
cycle effects, and revised oxygenated fuels effects.) A summary of the calendar year
1990 fleet-average CO emission rates calculated for each area and quarter is given in
Table 7-2. Note that only baseline numbers were calculated, since no alternative control
programs were assumed in the 1990 runs.
Table 7-2
1990 On-Road Motor Vehicle CO Emissions Estimates
by Urban Area and Quarter (g/mi)
Urban
Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Quarter
1
43.8
55.4
46.6
61.8
43.1
54.6
29.3
45.2
44.1
2
35.8
55.4
36.3
47.8
35.1
44.7
31.4
38.8
36.2
3
33.2
50.0
44.8
41.5
33.4
43.4
42.3
33.5
36.6
4
36.3
46.4
40.8
47.3
36.0
45.4
31.6
40.4
37.9
-73-
-------
Several points can be made in reference to Table 7-2:
In general, CO emissions in the winter (i.e., quarter 1) are higher than in the other
seasons. This occurs because temperatures are lower, which results in elevated
CO emissions from gasoline-fueled vehicles (primarily due to cold-start
increases).
The one area where CO emissions are lower in winter than in the other seasons is
Phoenix. That is because Phoenix had a winter oxygenated fuels program in
1990, which resulted in CO emissions decreases. In addition, the winter ambient
temperatures in Phoenix are relatively mild (44° to 67 °F diurnal temperature
pattern), which mitigates the cold-start effects observed in some of the other
communities. Because Phoenix is very hot in the summer (83° to 105 °F diurnal
temperature pattern), the impact of air conditioning usage is maximized in the
summer run (quarter 3), resulting in elevated CO emission rates in the summer.
Denver also had an oxygenated fuels program in 1990, which results in the winter
CO emission rates being the same as in the spring (quarter 2) run, even though the
temperature was lower in the winter run.
Because the fall runs (quarter 4) were performed using a January 1991 evaluation
date in the MOBILE input files, those results reflect an additional year of fleet
turnover relative to the winter runs (which were based on a January 1990
evaluation date). The spring and summer runs assumed a July 1990 evaluation
date, reflecting six months of additional fleet turnover relative to the winter runs.
Reactivity and VMT Adjustments
As outlined previously, unadjusted toxic exposure estimates can be determined from the
following formula:
However, because some of the toxic pollutants evaluated in this study (i.e., formaldehyde,
acetaldehyde, and 1,3 -butadiene) have a different photochemical reactivity than CO, the
exposure concentrations must be adjusted to account for atmospheric transformation. In
addition, because the CO ratios are based on the 1990 calendar year, an adjustment must
be made to account for the increase in VMT relative to 1990, i.e.,
TOXExposure_Adj (ng^ = TOXExposure.Unadj (ng/ms) x ReactivityAdj x VMTAdj
The specific adjustments to account for reactivity and VMT are described below.
Reactivity Adjustments - The reactivity adjustments used in this effort were provided to
Sierra by EPA staff,19 and are summarized as follows:
-74-
-------
1,3-Butadiene - Seasonal reactivity adjustments were estimated by EPA. These
multiplicative factors are 0.44 for summer, 0.70 for spring and fall, and 0.96 for
winter.
Benzene, MTBE, and Diesel PM - These were assumed to be inert for the
modeling performed in this study.
Formaldehyde andAcetaldehyde - There is strong evidence to suggest that these
species undergo substantive atmospheric transformation, both in terms of decay of
primary (i.e., tailpipe) emissions and in the formation of secondary formaldehyde
and acetaldehyde. However, because of the complexities involved in quantifying
that effect, it was not addressed in this study. Thus, the calculations performed to
generate the exposure estimates presented below treat these species as if they were
inert. If the formaldehyde and acetaldehyde exposure estimates generated in this
study are used in ensuing risk assessments, some accounting for atmospheric
transformation would be warranted.
VMT Adjustments - As discussed in Section 6, future-year on-road motor vehicle toxics
emissions estimates are expected to decline significantly as a result of fleet turnover
effects (i.e., older, high-emitting vehicles are replaced by newer technology vehicles with
more durable emissions control systems), improved I/M program designs, and the use of
cleaner fuels. However, those reductions cannot be used directly to assess corresponding
reductions in ambient concentrations. That is because growth in VMT will partially
offset the gains made in per-vehicle (or per-mile) reductions. That being the case, the
toxics exposure estimates for future years need to be adjusted to account for VMT
increases relative to the 1990 base year used to estimate CO exposure.
The VMT projections for each of the urban areas evaluated in this study were based on an
evaluation of the "Trends" database performed by an EPA contractor.20 The results of
this analysis are presented in Table 7-3. Note that Sierra was provided VMT forecasts
only for 1990, 1996, 2007, and 2010. The 2020 values shown in Table 7-3 were
extrapolated from the 2010 numbers by applying the annualized growth rate observed
between 2007 and 2010. For example, the estimated Chicago VMT in 2007 is
74,646,000 miles and in 2010 it is 78,428,000 miles. Thus the annualized growth over
those three years is:
Annual VMT Growth = (78,428/74,646)% - 1.0 = 0.0166
or 1.66%. This value was used in conjunction with the 2010 VMT forecast to arrive at a
2020 estimate:
VMTCH.2020 = 78,428,000 x (1.0166)10 = 92.5 million miles
Using the VMT estimates shown in Table 7-3, VMT growth rate adjustment factors were
generated for each urban area. These results are given in Table 7-4.
-75-
-------
Table 7-3
VMT Forecasts by Urban Area
(1000s of Miles)
Urban Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
1990
49,032
14,289
24,400
17,798
92,323
36,612
18,762
3,447
18,037
1996
62,408
20,189
40,684
22,506
103,195
43,286
25,017
4,105
27,903
2007
74,646
26,636
52,550
28,350
117,422
52,169
33,295
5,146
32,383
2010
78,428
28,444
55,819
29,958
122,258
54,711
35,788
5,446
33,985
2020
92,474
35,406
68,256
36,008
139,863
64,114
45,531
6,581
39,919
Table 7-4
VMT Adjustment Factors by Urban Area Relative to 1990
Urban Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
1990
1.000
1.000
1.000
1.000
1.000
1.000
1.000
1.000
1.000
1996
1.273
1.413
1.667
1.265
1.118
1.182
1.333
1.191
1.547
2007
1.522
1.864
2.154
1.593
1.272
1.425
1.775
1.493
1.795
2020
1.886
2.478
2.797
2.023
1.515
1.751
2.427
1.909
2.213
-76-
-------
Modeled Urban Area Toxics Exposure Estimates
Using the methodology described above, toxics exposure estimates were prepared for
each of the nine urban areas included in this study. These estimates were generated for
calendar years 1990, 1996, 2007, and 2020, and estimates were prepared for each quarter
as well as on an annual average basis. Finally, separate estimates were calculated for the
three demographic groups discussed above, and the 2007 and 2020 runs include baseline
control assumptions and the three control scenarios. Obviously, presenting the entire set
of results within the text of this report is not viable. Only the highlights are discussed
below; complete results by urban area and vehicle class can be found in Volume n of this
report.
FORTRAN Model - Because of the large number of scenarios modeled in this effort, the
compilation of toxics emissions data, CO emissions data, and CO exposure estimates was
performed within a FORTRAN routine. As described later in this report, this also
facilitated the calculation of national exposure estimates as well as risk analysis (i.e.,
estimating the number of cancer incidences per million people and the overall number of
cancer cases as a result of the various scenarios modeled in this study).
As an example of the calculation, the baseline Chicago 1996 winter benzene exposure for
the total population demographic group was estimated as follows. Variables in the
calculation are listed below.
COExposure. win 90 =375 |ig/m3 (from Table 7-1)
COEmissions.win 90 =43.8 g/mi (from Table 7-2)
BenzeneEmissions.win96 = 67.76 mg/mi (See Section 6)
VMT Growth1996 =1.273 (from Table 7-4)
Using the equation described above, the winter 1996 Chicago benzene exposure in this
case was then calculated as:
BnzExposure.win96 = (375 ^g/m3 743.8 g/mi) x (67.76 mg/mi / 1000) x 1.273
BnzExposure.win96 = 0.739 |ig/m3
Note that no transformation term was included in this calculation as benzene was
assumed to be inert for the purposes of the exposure estimates. The same methodology
was used to calculate benzene exposure for the remaining seasons, resulting in the
following estimates:
BnzExposure.Spr96 = 0.512 |ig/m3
BnzExposure.Sum96 = 0.405 |ig/m3
BnzExposure.Fall96 = 0.491 |ig/m3
-77-
-------
An annual average exposure estimate was calculated as the arithmetic mean of the four
seasonal values. In this case, the annual average Chicago benzene exposure was
calculated to be 0.537 |ig/m3.
At the request of the work assignment manager, exposure estimates were also generated
by vehicle class. This was accomplished by multiplying the overall on-road motor
vehicle exposure (calculated above) by the fractional contribution of each vehicle class to
the fleet-average emission rate. For example, the LDGV (i.e., passenger car) benzene
emission rate in the winter 1996 run was 64.24 mg/mi, with that vehicle class
contributing 55.0% of overall VMT. Thus, this vehicle class contributed:
Bnz FractionLDQv = (64.24 mg/mi x 0.550)767.76 mg/mi = 0.521
where 67.76 mg/mi is the fleet-average emission rate. Using this value in conjunction
with the overall 1996 Chicago winter benzene on-road motor vehicle exposure, the
exposure as a result of the LDGV class was calculated as:
= 0.739 ,ig/m3 x 0.521 = 0.386 ,ig/m3
Consistent with the fleet-average calculations, annual-average exposure estimates for
each vehicle class were prepared by taking the arithmetic mean of the quarterly results for
each class.
Results - A detailed summary of the exposure estimates calculated as described above is
contained in Volume II for each urban area, calendar year, demographic group, scenario,
season, and vehicle class. The annual average exposure estimates for the total population
are summarized in Tables 7-5 to 7-10 for benzene, acetaldehyde, formaldehyde, 1,3-
butadiene, MTBE, and Diesel PM, respectively. Recall that the four control programs
were defined as follows:
0. Baseline fuels and emission rates, assuming the implementation of a National
Low-Emission Vehicle (NLEV) program;
1. Baseline emission factors with an assumed national gasoline regulation limiting
sulfur levels to 40 ppm;
2. Scenario 1 with more stringent tailpipe hydrocarbon emission standards for light-
duty cars and trucks (i.e., reflecting possible Tier 2 standards); and
3. Scenario 2 with an assumed increase in light-duty Diesel truck implementation
equivalent to 50% of total light-duty truck sales beginning in model year 2004.
-78-
-------
Table 7-5
Annual-Average Exposure Results for Benzene
Total Population - All On-Road Vehicles
(Units: ug/m3)
Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
8.1
8.1
8.1
8.1
6.9
6.9
6.9
6.9
11.3
11.3
11.3
11.3
18.0
18.0
18.0
18.0
7.8
7.8
7.8
7.8
14.4
14.4
14.4
14.4
13.6
13.6
13.6
13.6
6.0
6.0
6.0
6.0
Calendar Year
1990
0.997
0.922
0.787
1.923
2.106
1.071
1.923
1.492
0.690
1996
0.567
0.871
0.530
1.414
0.903
0.642
1.419
1.194
0.634
2007
0.308
0.292
0.279
0.249
0.526
0.470
0.452
0.403
0.328
0.314
0.303
0.272
1.055
1.035
0.995
0.859
0.527
0.503
0.482
0.430
0.290
0.273
0.261
0.232
0.456
0.456
0.437
0.397
0.682
0.600
0.577
0.511
0.302
0.289
0.276
0.246
2020
0.235
0.218
0.164
0.131
0.430
0.368
0.285
0.227
0.244
0.229
0.178
0.145
0.978
0.955
0.795
0.587
0.354
0.331
0.246
0.198
0.210
0.193
0.145
0.116
0.378
0.378
0.288
0.236
0.515
0.431
0.330
0.262
0.234
0.218
0.163
0.130
-------
Table 7-6
Annual-Average Exposure Results for Acetaldehydea
Total Population - All On-Road Vehicles
(Units: ug/m3)
Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
8.1
8.1
8.1
8.1
6.9
6.9
6.9
6.9
11.3
11.3
11.3
11.3
18.0
18.0
18.0
18.0
7.8
7.8
7.8
7.8
14.4
14.4
14.4
14.4
13.6
13.6
13.6
13.6
6.0
6.0
6.0
6.0
Calendar Year
1990
0.149
___
___
0.234
___
___
0.123
___
___
0.262
___
___
0.312
___
___
0.169
___
___
0.245
___
___
0.277
___
___
0.108
___
___
1996
0.189
___
___
0.288
___
___
0.112
___
___
0.366
___
___
0.194
___
___
0.118
___
___
0.312
___
___
0.322
___
___
0.103
___
___
2007
0.094
0.091
0.088
0.084
0.147
0.144
0.140
0.137
0.060
0.059
0.057
0.059
0.218
0.215
0.208
0.189
0.101
0.099
0.097
0.098
0.049
0.048
0.047
0.048
0.101
0.101
0.098
0.103
0.154
0.145
0.141
0.135
0.075
0.074
0.071
0.069
2020
0.069
0.066
0.054
0.050
0.123
0.117
0.103
0.099
0.048
0.047
0.041
0.043
0.182
0.178
0.151
0.128
0.071
0.069
0.060
0.063
0.037
0.036
0.031
0.032
0.086
0.086
0.076
0.080
0.115
0.105
0.087
0.082
0.056
0.054
0.045
0.042
' Results not corrected for atmospheric transformation.
-------
Table 7-7
Annual-Average Exposure Results for Formaldehyde"
Total Population - All On-Road Vehicles
(Units: ug/m3)
Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
8.1
8.1
8.1
8.1
6.9
6.9
6.9
6.9
11.3
11.3
11.3
11.3
18.0
18.0
18.0
18.0
7.8
7.8
7.8
7.8
14.4
14.4
14.4
14.4
13.6
13.6
13.6
13.6
6.0
6.0
6.0
6.0
Calendar Year
1990
0.459
0.847
0.387
0.828
0.991
0.534
0.915
0.874
0.338
1996
0.312
0.633
0.369
0.652
0.668
0.407
0.638
0.669
0.291
2007
0.167
0.166
0.162
0.165
0.313
0.313
0.308
0.314
0.200
0.201
0.197
0.199
0.348
0.355
0.345
0.332
0.348
0.352
0.343
0.340
0.169
0.170
0.166
0.165
0.352
0.352
0.344
0.350
0.290
0.296
0.288
0.291
0.145
0.146
0.142
0.145
2020
0.126
0.125
0.107
0.109
0.266
0.265
0.240
0.242
0.149
0.149
0.129
0.134
0.290
0.300
0.259
0.246
0.223
0.225
0.192
0.197
0.117
0.117
0.100
0.102
0.281
0.281
0.244
0.253
0.220
0.220
0.188
0.191
0.109
0.110
0.094
0.096
' Results not corrected for atmospheric transformation.
-------
Table 7-8
Annual-Average Exposure Results for 1,3-Butadiene
Total Population - All On-Road Vehicles
(Units: ug/m3)
Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
8.1
8.1
8.1
8.1
6.9
6.9
6.9
6.9
11.3
11.3
11.3
11.3
18.0
18.0
18.0
18.0
7.8
7.8
7.8
7.8
14.4
14.4
14.4
14.4
13.6
13.6
13.6
13.6
6.0
6.0
6.0
6.0
Calendar Year
1990
0.100
0.139
0.081
0.190
0.229
0.130
0.150
0.186
0.076
1996
0.057
0.104
0.060
0.122
0.123
0.073
0.112
0.126
0.071
2007
0.028
0.026
0.025
0.025
0.049
0.043
0.042
0.041
0.031
0.027
0.027
0.027
0.082
0.074
0.072
0.066
0.063
0.053
0.052
0.050
0.028
0.025
0.024
0.024
0.045
0.045
0.044
0.045
0.055
0.048
0.047
0.046
0.030
0.027
0.026
0.025
2020
0.025
0.022
0.018
0.016
0.045
0.039
0.033
0.030
0.027
0.023
0.019
0.018
0.089
0.079
0.069
0.055
0.048
0.039
0.032
0.029
0.023
0.020
0.016
0.015
0.044
0.044
0.036
0.034
0.046
0.039
0.032
0.028
0.028
0.024
0.019
0.017
-------
Table 7-9
Annual-Average Exposure Results for MTBE
Total Population - All On-Road Vehicles
(Units: ug/m3)
Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
8.1
8.1
8.1
8.1
6.9
6.9
6.9
6.9
11.3
11.3
11.3
11.3
18.0
18.0
18.0
18.0
7.8
7.8
7.8
7.8
14.4
14.4
14.4
14.4
13.6
13.6
13.6
13.6
6.0
6.0
6.0
6.0
Calendar Year
1990
0.000
0.902
0.023
0.000
0.181
0.000
2.109
0.000
0.000
1996
0.000
0.000
0.883
0.000
1.526
0.684
0.049
0.000
0.000
2007
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.958
0.971
0.966
0.846
0.000
0.000
0.000
0.000
1.052
1.060
1.051
0.907
0.423
0.421
0.417
0.362
1.267
1.267
1.260
1.095
0.000
0.086
0.086
0.074
0.000
0.079
0.079
0.070
2020
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.000
0.658
0.665
0.642
0.503
0.000
0.000
0.000
0.000
0.644
0.647
0.608
0.467
0.287
0.284
0.264
0.207
0.994
0.994
0.950
0.731
0.000
0.049
0.049
0.038
0.000
0.057
0.057
0.045
-------
Table 7-10
Annual-Average Exposure Results for Diesel PM
Total Population - All On-Road Vehicles
(Units: ug/m3)
Area
Chicago
Denver
Houston
Minneapolis
New York
Philadelphia
Phoenix
Spokane
St. Louis
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
8.1
8.1
8.1
8.1
6.9
6.9
6.9
6.9
11.3
11.3
11.3
11.3
18.0
18.0
18.0
18.0
7.8
7.8
7.8
7.8
14.4
14.4
14.4
14.4
13.6
13.6
13.6
13.6
6.0
6.0
6.0
6.0
Calendar Year
1990
0.776
___
___
0.756
___
___
0.628
___
___
1.040
___
___
1.660
___
___
0.715
___
___
1.379
___
___
1.296
___
___
0.574
___
___
1996
0.566
___
___
0.700
___
___
0.756
___
___
0.866
___
___
1.059
___
___
0.602
___
___
1.205
___
___
1.015
___
___
0.530
___
___
2007
0.295
0.295
0.295
0.488
0.354
0.354
0.354
0.584
0.342
0.342
0.342
0.566
0.417
0.417
0.417
0.690
0.533
0.533
0.533
0.882
0.257
0.257
0.257
0.425
0.614
0.614
0.614
1.015
0.486
0.486
0.486
0.805
0.254
0.254
0.254
0.420
2020
0.273
0.273
0.273
0.647
0.353
0.353
0.353
0.837
0.334
0.334
0.334
0.791
0.395
0.395
0.395
0.936
0.473
0.473
0.473
1.121
0.236
0.236
0.236
0.558
0.631
0.631
0.631
1.495
0.464
0.464
0.464
1.101
0.234
0.234
0.234
0.555
-------
It is interesting to note that the motor vehicle air toxics exposures are estimated to
decrease substantially between 1990 and 2020, even without additional controls on
vehicles and fuels. This is a result of fleet-turnover and the full implementation of federal
regulations that are currently in place. As one might expect, the benefits of Scenario 1, a
national gasoline rule limiting sulfur to 40 ppm, are greatest in areas that do not have a
pre-existing reformulated gasoline program such as Minneapolis. Areas with an RFG
program show more moderate decreases in motor vehicle toxics exposure, depending on
pollutant, as a result of a national gasoline sulfur limit. The more stringent light-duty
vehicle emission standards modeled in Scenario 2 in general show greater decreases in
toxics exposure than the other control scenarios modeled in this effort, particularly for the
2020 calendar year run. Finally, the increased light-duty Diesel penetration scenario
modeled in Scenario 3 results in substantial increases in Diesel paniculate exposure
levels, although benzene and 1,3-butadiene exposure is decreased. It should be kept in
mind that the exposure estimates for acetaldehyde and formaldehyde do not include any
adjustments to account for atmospheric transformation.
As discussed above, exposure estimates were also prepared for three different
demographic groups: total population, outdoor workers, and children 0-17 years of age.
(The estimates given in Tables 7-5 to 7-10 are for the total population.) As with the CO
exposure estimates shown in Table 7-1, the exposure to air toxics for outdoor workers is
generally about 20% higher than for the total population, while exposure for children is
typically slightly below the total population. This is observed in Table 7-11, which shows
the annual-average benzene exposure for the three demographic groups analyzed in this
study for Chicago under the control scenarios described above. As seen in the table,
benzene exposure is highest for outdoor workers (which is the highest exposed
demographic group), while children and the total population show similar results.
-85-
-------
Also Table 7-11
Table 1-3
Annual-Average Exposure Results for Benzene in Chicago
by Demographic Group for All On-Road Motor Vehicles
(Units: ug/m3)
Demographic
Group
Total
Population
Outdoor
Workers
Children
0-17 Years
Scenario
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
Base
Sc#l
Sc#2
Sc#3
1990
CO Ratio
8.4
8.4
8.4
8.4
10.1
10.1
10.1
10.1
8.2
8.2
8.2
8.2
Calendar Year
1990
0.997
1.200
0.980
1996
0.567
0.683
0.557
2007
0.308
0.292
0.279
0.249
0.371
0.351
0.336
0.300
0.303
0.287
0.274
0.245
2020
0.235
0.218
0.164
0.131
0.283
0.262
0.197
0.158
0.231
0.214
0.161
0.129
-------
8. RISK ASSESSMENT
Using the on-road motor vehicle toxic exposure estimates generated in Section 7,
estimates of individual cancer risk can be calculated from the following formula:
CANfcd = TOXExposure.Adj (wsta3) x (UR / YPL)
where TOXExposure_Adj (flg/m3) is the adjusted toxic exposure estimates generated in Section 7;
UR is the unit risk in cancer cases or deaths per person exposed in a lifetime to 1 |ig/m3
of the toxic compound of interest; and YPL is years per lifetime (typically assumed to be
70 years).
To calculate the total cancer cases for the population, the individual cancer risk defined
above is simply multiplied by the population subject to the toxic compound exposure, i.e.
CANPop = CANtod x Population
Because EPA has not yet finalized revised unit risk estimates, Sierra was directed to only
set up a methodology to calculate individual risk and cancer incidences. This was
accomplished within the FORTRAN routine developed to generate the exposure
estimates. That model was structured to allow a user to input two estimates of unit risk
for each pollutant (a lower bound and an upper bound), as well as alternative years per
lifetime estimates. Individual risk is reported in terms of cancer cases per million people,
and total cancer cases are calculated based on the population in each area. Estimates are
prepared for each of the nine modeled areas under the entire suite of forecast years and
control scenarios for which exposure is estimated.
A copy of the individual cancer risk output from the model is given in Table 8-1 for
benzene for the nine urban areas modeled in this effort (performed for the total population
and all vehicle classes). Note that the range of unit risk values used in this analysis was
chosen simply for calculational purposes. It is not necessarily reflective of the values
EPA may ultimately use in its analyses.
-87-
-------
Table 8-1
Sample Output from the Exposure Model
Benzene Cancer Incidences per Million People
DRAFT - DO NOT QUOTE OR CITE
Cancer Incidences Per Million People for Benzene
Demographic Group: All
Vehicle Class: All Veh
Low-Range Unit Risk (per million):
High-Range Unit Risk (per million):
Assumed Years Per Lifetime: 70.0
8.300
15.000
CY1990
Area
CHICAGO
CHICAGO
CHICAGO
CHICAGO
DENVER
DENVER
DENVER
DENVER
HOUSTON
HOUSTON
HOUSTON
HOUSTON
MINNEAPOLIS
MINNEAPOLIS
MINNEAPOLIS
MINNEAPOLIS
NEW YORK
NEW YORK
NEW YORK
NEW YORK
PHILADELPHIA
PHILADELPHIA
PHILADELPHIA
PHILADELPHIA
PHOENIX
PHOENIX
PHOENIX
PHOENIX
SPOKANE
SPOKANE
SPOKANE
SPOKANE
ST LOUIS
ST LOUIS
ST LOUIS
ST LOUIS
Seen
Base
Scttl
Sc#2
Sc#3
Base
Scttl
Sc#2
Sc#3
Base
Scttl
Sc#2
Sc#3
Base
Scttl
Sc#2
Sc#3
Base
Scttl
Sc#2
Sc#3
Base
Scttl
Sc#2
Sc#3
Base
Scttl
Sc#2
Sc#3
Base
Scttl
Sc#2
Sc#3
Base
Scttl
Sc#2
Sc#3
0.
0.
0.
0.
0.
0.
0.
0.
0.
Low
.1182
.1093
.0933
.2280
.2497
.1269
.2281
.1769
.0819
High
0.2136
0.1975
0.1686
0.4120
0.4512
0.2294
0.4122
0.3197
0.1479
CY1996
Low
0.0672
0.1033
0.0628
0.1676
0.1071
0.0761
0.1682
0.1416
0.0751
High
0.1215
0.1866
0.1135
0.3029
0.1936
0.1375
0.3040
0.2560
0.1358
CY2007
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
Low
.0366
.0346
.0330
.0295
.0624
.0558
.0536
.0478
.0389
.0372
.0359
.0322
.1251
.1227
.1180
.1018
.0625
.0597
.0571
.0509
.0344
.0323
.0309
.0275
.0540
.0540
.0518
.0470
.0809
.0711
.0684
.0605
.0358
.0343
.0327
.0292
High
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.0661
.0625
.0597
.0534
.1127
.1008
.0968
.0864
.0702
.0673
.0648
.0582
.2261
.2218
.2133
.1840
.1129
.1078
.1033
.0920
.0621
.0584
.0559
.0497
.0976
.0976
.0936
.0850
.1462
.1285
.1236
.1094
.0648
.0620
.0592
.0528
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
CY2020
Low
.0279
.0258
.0194
.0155
.0510
.0436
.0338
.0269
.0289
.0271
.0211
.0172
.1159
.1133
.0943
.0696
.0419
.0392
.0292
.0235
.0248
.0229
.0171
.0137
.0448
.0448
.0341
.0279
.0610
.0510
.0392
.0311
.0277
.0258
.0193
.0154
High
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.0504
.0467
.0351
.0280
.0922
.0789
.0610
.0486
.0523
.0491
.0382
.0311
.2095
.2047
.1704
.1257
.0758
.0709
.0527
.0424
.0449
.0414
.0310
.0248
.0810
.0810
.0617
.0505
.1103
.0923
.0708
.0562
.0501
.0466
.0349
.0278
-------
9. REFERENCES
1. "Mobile Vehicle-Related Air Toxics Study," U.S. Environmental Protection
Agency, April 1993.
2. "Regulations for Fuels and Fuel Additives; Standards for Reformulated and
Conventional Gasoline; Final Rule," U.S. Environmental Protection Agency,
Federal Register. Vol. 59, No. 32, February 16, 1994.
3. Koupal, J.W. and Rykowski, R.A., "Methodology for Modifying MOBILESb in
the Tier 2 Study," U.S. Environmental Protection Agency, EPA420-R-98-004,
April 1998.
4. Koupal, J.W., "Air Conditioning Activity Effects in MOBILE6 - DRAFT," U.S.
Environmental Protection Agency, M6.ACE.001, January 26, 1998.
5. "Effects of Fuel Oxygen Content on CO Emissions," Memorandum from Philip
Heirigs (Sierra Research) to David H. Lax (American Petroleum Institute),
February 13, 1998.
6. Rao, V., "Fuel Oxygen Effects on Exhaust CO Emissions - Recommendations for
MOBILE6 (Draft)," U.S. Environmental Protection Agency, Report No.
M6.FUL.002, March 16, 1998.
7. "Derivation of Technology Specific Effects of the Use of Oxygenated Fuel Blends
in Motor Vehicle Exhaust Emissions," U.S. Environmental Protection Agency,
October 1988.
8. "Final Regulatory Impact Analysis for Reformulated Gasoline," U.S.
Environmental Protection Agency, December 13, 1993.
9. Wyborny, L., "Methyl Tertiary Butyl Ether (MTBE) Emissions from Passenger
Cars," Draft Technical Report. U. S. Environmental Protection Agency, Office
of Mobile Sources, April 1998.
10. "California Exhaust Emission Standards and Test Procedures for 1988 and
Subsequent Model Passenger Cars, Light-Duty Trucks, and Medium-Duty
Vehicles," California Air Resources Board, June 24, 1996.
-91-
-------
11. "Emission Control Technology Distribution," Prepared by Energy and
Environmental Analysis for the U.S. Environmental Protection Agency, February
10, 1997.
12. "National Air Pollutant Emission Trends Report," Prepared by E.H. Pechan for
the U.S. Environmental Protection Agency, Work Assignment 1-02, Contract No.
68D70067, October 1, 1997.
13. Personal communication. John Koupal, U.S. Environmental Protection Agency,
June 1998.
14. Personal communication. Dave Sosnowski, U.S. Environmental Protection
Agency, June 1998.
15. Personal communication. Buddy Polovick, U.S. Environmental Protection
Agency, April 1998.
16. "A Comparative Study of the Effectiveness of Stage JJ Refueling Controls and
Onboard Refueling Vapor Recovery," Performed by Sierra Research for the
American Automobile Manufacturers Association, October 29, 1993.
17. Glen, G. and Shadwick, D., "Final Technical Report on the Analysis of Carbon
Monoxide Exposure for Fourteen Cities Using HAPEM-MS3," Prepared by
Mantech Environmental Technology, Inc. for the U.S. Environmental Protection
Agency, March 1998.
18. "Determination of Annual Average CO Inventories and the Mobile Source
Contribution in Selected Areas Using the 1990 OAQPS Trends Data Base,"
Prepared by E.H. Pechan for the U.S. Environmental Protection Agency,
September 1997.
19. Personal Communication. Pamela Brodowicz, U.S. Environmental Protection
Agency, September 1998.
20. Personal Communication. Maureen Mullen, E.H. Pechan to Pamela Brodowicz,
U.S. Environmental Protection Agency, September 1998.
-92-
-------
Appendix A
Revised TOG and CO Inputs Used in the
MOBILE Emissions Modeling
The following inputs and data are included in this appendix:
1. TOG/NMHC Ratios
2. Alternative TOG base emission rate equations for the following scenarios:
a. Non-OTR NLEV, I/M, baseline emission factors
b. Non-OTR NLEV, I/M, Tier 2 control
c. Non-OTR NLEV, Non-I/M, baseline emission factors
d. Non-OTR NLEV, Non-I/M, Tier 2 control
e. OTR NLEV, I/M, baseline emission factors
f. OTR NLEV, I/M, Tier 2 control
g. Denver - Non-OTR NLEV, I/M, baseline emission factors
h. Denver - Non-OTR NLEV, I/M, Tier 2 control
3. Off-cycle TOG correction factors
a. I/M, 1990
b. I/M, 1996 and later
c. Non-I/M, 1990
d. Non-I/M, 1996
e. Non-I/M, 2007 and later
4. Alternative CO base emission rate equations for the following:
a. Low-altitude
b. High-altitude (Denver)
5. Off-Cycle CO correction factors (I/M and non-I/M combined)
6. Air conditioning data for CO estimates (fraction equipped, malfunction rates)
7. Oxygenated fuels CO effects
-------
TOG/NMHC Correction Factors by Model Year and Vehicle Class
MY
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
LDGV
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.158
1.161
1.161
1.165
1.165
1.184
1.290
1.291
1.311
1.307
1.280
1.264
1.246
1.209
1.199
1.197
1.184
1.177
1.169
1.169
1.169
1.169
1.169
1.169
1.169
1.169
1.169
1.169
1.169
1.169
LDGT1
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.150
1.158
1.154
1.154
1.158
1.158
1.174
1.174
1.190
1.221
1.213
1.197
1.222
1.221
1.234
1.212
1.149
1.196
1.194
1.192
1.192
1.194
1.194
1.194
1.194
1.194
1.182
1.182
1.182
1.182
LDGT2
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.173
1.173
1.173
1.173
1.194
1.236
1.257
1.278
1.287
1.276
1.276
1.276
1.149
1.196
1.194
1.192
1.192
1.194
1.194
1.194
1.194
1.194
1.182
1.182
1.182
1.182
HDGV
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.252
1.271
1.271
1.271
1.271
1.271
1.367
1.406
1.406
1.610
1.610
1.610
1.610
1.610
1.610
1.618
1.618
1.618
1.618
1.629
1.629
1.629
1.629
1.637
LDDV
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
LDDT
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
1.1094
HDDV
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
1.1294
MC
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
1.099
-------
TOG BERs - I/M Non-OTR Baseline Case
File: NTR_IM_B.BER
LDGV
0099
111
111
111
111
111
111
111
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
65
68
70
72
75
76
78
80
81
83
84
85
86
87
88
89
90
91
92
93
95
01
04
65
68
70
72
75
76
77
79
81
83
84
85
86
87
88
89
90
91
92
94
95
01
04
65
70
74
79
81
83
84
85
86
87
88
89
67
69
71
74
75
77
79
80
82
83
84
85
86
87
88
89
90
91
92
94
00
03
50
67
69
71
74
75
76
78
80
82
83
84
85
86
87
88
89
90
91
93
94
00
03
50
69
73
78
80
82
83
84
85
86
87
88
89
7
4
3
3
1
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
7
4
3
3
1
1
1
0
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
9
6
6
0
1
1
0
0
0
0
0
0
ZM
.488
.576
.099
.491
.068
.071
.074
.371
.398
.258
.257
.251
.303
.299
.290
.288
.200
.198
.197
.195
.169
.094
.094
.488
.576
.099
.470
.802
.813
.807
.876
.140
.156
.486
.483
.477
.487
.486
.491
.323
.306
.318
.317
.214
.110
.110
.885
.486
.486
.887
.139
.159
.492
.500
.509
.513
.508
.508
DR1
0.186
0.258
0.382
0.165
0.282
0.283
0.284
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.
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.
.211
. 149
.051
.051
.050
.058
.057
.056
.055
.019
.018
.018
.018
.011
.009
.009
.186
.258
.382
.176
.270
.272
.271
.282
.044
.045
.022
.022
.022
.022
.022
.022
.018
.017
.017
.017
.012
.008
.008
.186
.258
.176
.286
.044
.045
.022
.023
.023
.023
.023
.023
DR2 Flex
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
0
0
0
0
0
0
0
0
.209
.140
.140
.137
.040
.040
.040
.040
.022
.015
.015
.143
.145
.108
.107
.106
.108
.108
.109
.047
. 044
.046
.046
.025
.016
.016
.143
.146
.109
.111
.113
.114
.113
.113
1
2
2
2
2
2
2
2
8
7
7
1
1
4
4
4
4
4
4
2
2
2
2
9
8
8
1
1
4
4
4
4
4
4
Pt
.53
.22
.22
.22
.13
.13
.13
.13
.90
.87
.87
.73
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.06
.29
.29
.73
.73
.41
.41
.41
.41
.41
.41
Includes LEV Sulfur Corr 1.36
Includes LEV Sulfur Corr 1.36
LDGT1
Includes LEV Sulfur Corr 1.23
Includes LEV Sulfur Corr 1.23
LDGT2
-------
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
4
4
5
5
5
5
5
5
5
5
5
5
6
6
6
6
6
6
6
6
6
6
7
7
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
90
91
92
94
96
97
01
04
94
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
94
04
90
91
93
95
96
00
03
50
94
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
03
50
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.340
.306
.318
.317
.318
.260
.258
.258
.586
.586
.589
.589
.589
.589
.593
.593
.593
.593
.453
.161
.161
.161
.161
.161
.161
.066
.066
.066
.066
.271
.271
.231
.231
.231
.231
.202
.202
.202
.202
.320
.290
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.019
.017
.017
.017
.017
.012
.012
.012
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.029
.011
.011
.011
.011
.011
.011
.006
.006
.006
.006
.015
.015
.011
.011
.011
.011
.010
.010
.010
.010
.000
.000
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.
0.
0.
.049
. 044
.046
.046
.046
.030
.030
.030
.021
.021
.021
.021
.021
.021
.011
.011
.011
.011
.038
.038
.027
.027
.027
.027
.024
.024
.024
.024
2
2
2
2
2
9
9
9
8
8
8
8
8
8
7
7
7
7
3
3
9
9
9
9
9
9
9
9
.13
.13
.13
.13
.13
.25
.25
.25
.90
.90
.90
.90
.90
.90
.87
.87
.87
.87
.87
.87
.21
.21
.21
.21
.01
.01
.01
.01
HDGV
LDDV
LDDT
Assumes 25% LDT1 and 75% LDT2
HDDV
-------
TOG BERs - I/M Non-OTR Control Case
File: NTR_IM_C.BER
LDGV
0099
111
111
111
111
111
111
111
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
65
68
70
72
75
76
78
80
81
83
84
85
86
87
88
89
90
91
92
93
95
01
04
65
68
70
72
75
76
77
79
81
83
84
85
86
87
88
89
90
91
92
94
95
01
04
65
70
74
79
81
83
84
85
86
87
88
89
67
69
71
74
75
77
79
80
82
83
84
85
86
87
88
89
90
91
92
94
00
03
50
67
69
71
74
75
76
78
80
82
83
84
85
86
87
88
89
90
91
93
94
00
03
50
69
73
78
80
82
83
84
85
86
87
88
89
7
4
3
3
1
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
7
4
3
3
1
1
1
0
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
9
6
6
0
1
1
0
0
0
0
0
0
ZM
.488
.576
.099
.491
.068
.071
.074
.371
.398
.258
.257
.251
.303
.299
.290
.288
.200
.198
.197
.195
.169
.094
.057
.488
.576
.099
.470
.802
.813
.807
.876
.140
.156
.486
.483
.477
.487
.486
.491
.323
.306
.318
.317
.214
.110
.058
.885
.486
.486
.887
.139
.159
.492
.500
.509
.513
.508
.508
DR1
0.186
0.258
0.382
0.165
0.282
0.283
0.284
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.
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.
.211
. 149
.051
.051
.050
.058
.057
.056
.055
.019
.018
.018
.018
.011
.009
.008
.186
.258
.382
.176
.270
.272
.271
.282
.044
.045
.022
.022
.022
.022
.022
.022
.018
.017
.017
.017
.012
.008
.008
.186
.258
.176
.286
.044
.045
.022
.023
.023
.023
.023
.023
DR2 Flex
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
0
0
0
0
0
0
0
0
.209
.140
.140
.137
.040
.040
.040
.040
.022
.015
.014
.143
.145
.108
.107
.106
.108
.108
.109
.047
. 044
.046
.046
.025
.016
. 014
.143
.146
.109
.111
.113
.114
.113
.113
1
2
2
2
2
2
2
2
8
7
8
1
1
4
4
4
4
4
4
2
2
2
2
9
8
8
1
1
4
4
4
4
4
4
Pt
.53
.22
.22
.22
.13
.13
.13
.13
.90
.87
.10
.73
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.06
.29
.10
.73
.73
.41
.41
.41
.41
.41
.41
Includes LEV Sulfur Corr 1.36
Includes LEV Sulfur Corr 1.36
LDGT1
Includes LEV Sulfur Corr 1.23
Includes LEV Sulfur Corr 1.36
LDGT2
-------
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
4
4
5
5
5
5
5
5
5
5
5
5
6
6
6
6
6
6
6
6
6
6
7
7
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
90
91
92
94
96
97
01
04
94
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
94
04
90
91
93
95
96
00
03
50
94
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
03
50
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.340
.306
.318
.317
.318
.260
.258
.058
.586
.586
.589
.589
.589
.589
.593
.593
.593
.593
.453
.161
.161
.161
.161
.161
.161
.066
.066
.066
.040
.271
.271
.231
.231
.231
.231
.202
.202
.202
.040
.320
.290
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.019
.017
.017
.017
.017
.012
.012
.008
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.029
.011
.011
.011
.011
.011
.011
.006
.006
.006
.006
.015
.015
.011
.011
.011
.011
.010
.010
.010
.006
.000
.000
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.
0.
0.
.049
. 044
.046
.046
.046
.030
.030
.014
.021
.021
.021
.021
.021
.021
.011
.011
.011
.010
.038
.038
.027
.027
.027
.027
.024
.024
.024
.010
2
2
2
2
2
9
9
8
8
8
8
8
8
8
7
7
7
8
3
3
9
9
9
9
9
9
9
8
.13
.13
.13
.13
.13
.25
.25
.10
.90
.90
.90
.90
.90
.90
.87
.87
.87
.10
.87
.87
.21
.21
.21
.21
.01
.01
.01
.10
Includes LEV Sulfur Corr
HDGV
1.36
LDDV
LDDT
Assumes 25% LDT1 and 75% LDT2
HDDV
-------
TOG BERs - Non-I/M Non-OTR Baseline Case
File: NTR_NO_B.BER
LDGV
0099
111
111
111
111
111
111
111
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
65
68
70
72
75
76
78
80
81
83
84
85
86
87
88
89
90
91
92
93
95
01
04
65
68
70
72
75
76
77
79
81
83
84
85
86
87
88
89
90
91
92
94
95
01
04
65
70
74
79
81
83
84
85
86
87
88
89
67
69
71
74
75
77
79
80
82
83
84
85
86
87
88
89
90
91
92
94
00
03
50
67
69
71
74
75
76
78
80
82
83
84
85
86
87
88
89
90
91
93
94
00
03
50
69
73
78
80
82
83
84
85
86
87
88
89
7
4
3
3
1
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
7
4
3
3
1
1
1
0
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
9
6
6
0
1
1
0
0
0
0
0
0
ZM
.488
.576
.099
.491
.068
.071
.074
.371
.398
.258
.257
.251
.303
.299
.290
.288
.200
.198
.197
.195
.169
.094
.094
.488
.576
.099
.470
.802
.813
.807
.876
.140
.156
.486
.483
.477
.487
.486
.491
.323
.306
.318
.317
.213
.110
.110
.885
.486
.486
.887
.139
.159
.492
.500
.509
.513
.508
.508
DR1
0.186
0.258
0.382
0.165
0.282
0.283
0.284
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.
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.
.211
. 149
.051
.051
.050
.058
.057
.056
.055
.019
.018
.018
.018
.016
.016
.016
.186
.258
.382
.176
.270
.272
.271
.282
.044
.045
.022
.022
.022
.022
.022
.022
.018
.017
.017
.017
.018
.017
.017
.186
.258
.176
.286
.044
.045
.022
.023
.023
.023
.023
.023
DR2 Flex
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
0
0
0
0
0
0
0
0
.209
.140
.140
.137
.040
.040
.040
.040
.038
.048
.048
.143
.145
.108
.107
.106
.108
.108
.109
.047
. 044
.046
.046
.039
. 044
. 044
.143
.146
.109
.111
.113
.114
.113
.113
1
2
2
2
2
2
2
2
6
6
6
1
1
4
4
4
4
4
4
2
2
2
2
7
3
3
1
1
4
4
4
4
4
4
Pt
.53
.22
.22
.22
.13
.13
.13
.13
.70
.77
.77
.73
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.27
.09
.09
.73
.73
.41
.41
.41
.41
.41
.41
Includes LEV Sulfur Corr 1.36
Includes LEV Sulfur Corr 1.36
LDGT1
Includes LEV Sulfur Corr 1.23
Includes LEV Sulfur Corr 1.23
LDGT2
-------
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
4
4
5
5
5
5
5
5
5
5
5
5
6
6
6
6
6
6
6
6
6
6
7
7
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
90
91
92
94
96
97
01
04
94
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
94
04
90
91
93
95
96
00
03
50
94
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
03
50
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.340
.306
.318
.317
.318
.260
.257
.257
.586
.586
.589
.589
.589
.589
.593
.593
.593
.593
.453
.161
.161
.161
.161
.161
.161
.066
.066
.066
.066
.271
.271
.231
.231
.231
.231
.202
.202
.202
.202
.320
.290
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.019
.017
.017
.017
.017
.018
.018
.018
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.029
.015
.015
.015
.015
.015
.015
.011
.011
.011
.011
.016
.016
.017
.017
.017
.017
.016
.016
.016
.016
.000
.000
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.
0.
0.
.049
. 044
.046
.046
.046
.039
.039
.039
.036
.036
.036
.036
.036
.036
.034
.034
.034
.034
.041
.041
.036
.036
.036
.036
.036
.036
.036
.036
2
2
2
2
2
7
7
7
6
6
6
6
6
6
6
6
6
6
3
3
7
7
7
7
6
6
6
6
.13
.13
.13
.13
.13
.49
.49
.49
.70
.70
.70
.70
.70
.70
.77
.77
.77
.77
.42
.42
.44
.44
.44
.44
.39
.39
.39
.39
HDGV
LDDV
LDDT
Assumes 25% LDT1 and 75% LDT2
HDDV
-------
TOG BERs - Non-I/M Non-OTR Control Case
File: NTR_NO_C.BER
LDGV
0099
111
111
111
111
111
111
111
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
65
68
70
72
75
76
78
80
81
83
84
85
86
87
88
89
90
91
92
93
95
01
04
65
68
70
72
75
76
77
79
81
83
84
85
86
87
88
89
90
91
92
94
95
01
04
65
70
74
79
81
83
84
85
86
87
88
89
67
69
71
74
75
77
79
80
82
83
84
85
86
87
88
89
90
91
92
94
00
03
50
67
69
71
74
75
76
78
80
82
83
84
85
86
87
88
89
90
91
93
94
00
03
50
69
73
78
80
82
83
84
85
86
87
88
89
7
4
3
3
1
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
7
4
3
3
1
1
1
0
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
9
6
6
0
1
1
0
0
0
0
0
0
ZM
.488
.576
.099
.491
.068
.071
.074
.371
.398
.258
.257
.251
.303
.299
.290
.288
.200
.198
.197
.195
.169
.094
.057
.488
.576
.099
.470
.802
.813
.807
.876
.140
.156
.486
.483
.477
.487
.486
.491
.323
.306
.318
.317
.213
.110
.058
.885
.486
.486
.887
.139
.159
.492
.500
.509
.513
.508
.508
DR1
0.186
0.258
0.382
0.165
0.282
0.283
0.284
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.
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.
.211
. 149
.051
.051
.050
.058
.057
.056
.055
.019
.018
.018
.018
.016
.016
.010
.186
.258
.382
.176
.270
.272
.271
.282
.044
.045
.022
.022
.022
.022
.022
.022
.018
.017
.017
.017
.018
.017
.010
.186
.258
.176
.286
.044
.045
.022
.023
.023
.023
.023
.023
DR2 Flex
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
0
0
0
0
0
0
0
0
.209
.140
.140
.137
.040
.040
.040
.040
.038
.048
.046
.143
.145
.108
.107
.106
.108
.108
.109
.047
. 044
.046
.046
.039
. 044
. 047
.143
.146
.109
.111
.113
.114
.113
.113
1
2
2
2
2
2
2
2
6
6
5
1
1
4
4
4
4
4
4
2
2
2
2
7
3
5
1
1
4
4
4
4
4
4
Pt
.53
.22
.22
.22
.13
.13
.13
.13
.70
.77
.77
.73
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.27
.09
.77
.73
.73
.41
.41
.41
.41
.41
.41
Includes LEV Sulfur Corr 1.36
Includes LEV Sulfur Corr 1.36
LDGT1
Includes LEV Sulfur Corr 1.23
Includes LEV Sulfur Corr 1.36
LDGT2
-------
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
4
4
5
5
5
5
5
5
5
5
5
5
6
6
6
6
6
6
6
6
6
6
7
7
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
90
91
92
94
96
97
01
04
94
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
94
04
90
91
93
95
96
00
03
50
94
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
03
50
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.340
.306
.318
.317
.318
.260
.257
.058
.586
.586
.589
.589
.589
.589
.593
.593
.593
.593
.453
.161
.161
.161
.161
.161
.161
.066
.066
.066
.040
.271
.271
.231
.231
.231
.231
.202
.202
.202
.040
.320
.290
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.019
.017
.017
.017
.017
.018
.018
.010
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.029
.015
.015
.015
.015
.015
.015
.011
.011
.011
.007
.016
.016
.017
.017
.017
.017
.016
.016
.016
.007
.000
.000
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.
0.
0.
.049
. 044
.046
.046
.046
.039
.039
.047
.036
.036
.036
.036
.036
.036
.034
.034
.034
.032
.041
.041
.036
.036
.036
.036
.036
.036
.036
.032
2
2
2
2
2
7
7
5
6
6
6
6
6
6
6
6
6
5
3
3
7
7
7
7
6
6
6
5
.13
.13
.13
.13
.13
.49
.49
.77
.70
.70
.70
.70
.70
.70
.77
.77
.77
.77
.42
.42
.44
.44
.44
.44
.39
.39
.39
.77
Includes LEV Sulfur Corr
HDGV
1.36
LDDV
LDDT
Assumes 25% LDT1 and 75% LDT2
HDDV
-------
TOG BERs - I/M OTR Baseline Case
File: OTR_IM_B.BER
LDGV
0099
111
111
111
111
111
111
111
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
65
68
70
72
75
76
78
80
81
83
84
85
86
87
88
89
90
91
92
93
95
00
04
65
68
70
72
75
76
77
79
81
83
84
85
86
87
88
89
90
91
92
94
95
00
04
65
70
74
79
81
83
84
85
86
87
88
89
67
69
71
74
75
77
79
80
82
83
84
85
86
87
88
89
90
91
92
94
99
03
50
67
69
71
74
75
76
78
80
82
83
84
85
86
87
88
89
90
91
93
94
99
03
50
69
73
78
80
82
83
84
85
86
87
88
89
7
4
3
3
1
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
7
4
3
3
1
1
1
0
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
9
6
6
0
1
1
0
0
0
0
0
0
ZM
.488
.576
.099
.491
.068
.071
.074
.371
.398
.258
.257
.251
.303
.299
.290
.288
.200
.198
.197
.195
.169
.094
.094
.488
.576
.099
.470
.802
.813
.807
.876
.140
.156
.486
.483
.477
.487
.486
.491
.323
.306
.318
.317
.214
.110
.110
.885
.486
.486
.887
.139
.159
.492
.500
.509
.513
.508
.508
DR1
0.186
0.258
0.382
0.165
0.282
0.283
0.284
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.
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.
.211
. 149
.051
.051
.050
.058
.057
.056
.055
.019
.018
.018
.018
.011
.009
.009
.186
.258
.382
.176
.270
.272
.271
.282
.044
.045
.022
.022
.022
.022
.022
.022
.018
.017
.017
.017
.012
.008
.008
.186
.258
.176
.286
.044
.045
.022
.023
.023
.023
.023
.023
DR2 Flex
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
0
0
0
0
0
0
0
0
.209
.140
.140
.137
.040
.040
.040
.040
.022
.015
.015
.143
.145
.108
.107
.106
.108
.108
.109
.047
. 044
.046
.046
.025
.016
.016
.143
.146
.109
.111
.113
.114
.113
.113
1
2
2
2
2
2
2
2
8
7
7
1
1
4
4
4
4
4
4
2
2
2
2
9
8
8
1
1
4
4
4
4
4
4
Pt
.53
.22
.22
.22
.13
.13
.13
.13
.90
.87
.87
.73
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.06
.29
.29
.73
.73
.41
.41
.41
.41
.41
.41
Includes LEV Sulfur Corr 1.36
Includes LEV Sulfur Corr 1.36
LDGT1
Includes LEV Sulfur Corr 1.23
Includes LEV Sulfur Corr 1.23
LDGT2
-------
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
4
4
5
5
5
5
5
5
5
5
5
5
6
6
6
6
6
6
6
6
6
6
7
7
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
90
91
92
94
96
97
01
04
94
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
94
04
90
91
93
95
96
00
03
50
94
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
03
50
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.340
.306
.318
.317
.318
.260
.258
.258
.586
.586
.589
.589
.589
.589
.593
.593
.593
.593
.453
.161
.161
.161
.161
.161
.066
.066
.066
.066
.066
.271
.271
.231
.231
.231
.202
.202
.202
.202
.202
.320
.290
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.019
.017
.017
.017
.017
.012
.012
.012
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.029
.011
.011
.011
.011
.011
.006
.006
.006
.006
.006
.015
.015
.011
.011
.011
.010
.010
.010
.010
.010
.000
.000
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.
0.
0.
.049
. 044
.046
.046
.046
.030
.030
.030
.021
.021
.021
.021
.021
.011
.011
.011
.011
.011
.038
.038
.027
.027
.027
.024
.024
.024
.024
.024
2
2
2
2
2
9
9
9
8
8
8
8
8
7
7
7
7
7
3
3
9
9
9
9
9
9
9
9
.13
.13
.13
.13
.13
.25
.25
.25
.90
.90
.90
.90
.90
.87
.87
.87
.87
.87
.87
.87
.21
.21
.21
.01
.01
.01
.01
.01
HDGV
LDDV
LDDT
Assumes 25% LDT1 and 75% LDT2
HDDV
-------
TOG BERs - I/M OTR Control Case
File: OTR_IM_C.BER
LDGV
0099
111
111
111
111
111
111
111
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
65
68
70
72
75
76
78
80
81
83
84
85
86
87
88
89
90
91
92
93
95
00
04
65
68
70
72
75
76
77
79
81
83
84
85
86
87
88
89
90
91
92
94
95
00
04
65
70
74
79
81
83
84
85
86
87
88
89
67
69
71
74
75
77
79
80
82
83
84
85
86
87
88
89
90
91
92
94
99
03
50
67
69
71
74
75
76
78
80
82
83
84
85
86
87
88
89
90
91
93
94
99
03
50
69
73
78
80
82
83
84
85
86
87
88
89
7
4
3
3
1
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
7
4
3
3
1
1
1
0
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
9
6
6
0
1
1
0
0
0
0
0
0
ZM
.488
.576
.099
.491
.068
.071
.074
.371
.398
.258
.257
.251
.303
.299
.290
.288
.200
.198
.197
.195
.169
.094
.057
.488
.576
.099
.470
.802
.813
.807
.876
.140
.156
.486
.483
.477
.487
.486
.491
.323
.306
.318
.317
.214
.110
.058
.885
.486
.486
.887
.139
.159
.492
.500
.509
.513
.508
.508
DR1
0.186
0.258
0.382
0.165
0.282
0.283
0.284
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.
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.
.211
. 149
.051
.051
.050
.058
.057
.056
.055
.019
.018
.018
.018
.011
.009
.008
.186
.258
.382
.176
.270
.272
.271
.282
.044
.045
.022
.022
.022
.022
.022
.022
.018
.017
.017
.017
.012
.008
.008
.186
.258
.176
.286
.044
.045
.022
.023
.023
.023
.023
.023
DR2 Flex
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
0
0
0
0
0
0
0
0
.209
.140
.140
.137
.040
.040
.040
.040
.022
.015
.014
.143
.145
.108
.107
.106
.108
.108
.109
.047
. 044
.046
.046
.025
.016
. 014
.143
.146
.109
.111
.113
.114
.113
.113
1
2
2
2
2
2
2
2
8
7
8
1
1
4
4
4
4
4
4
2
2
2
2
9
8
8
1
1
4
4
4
4
4
4
Pt
.53
.22
.22
.22
.13
.13
.13
.13
.90
.87
.10
.73
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.06
.29
.10
.73
.73
.41
.41
.41
.41
.41
.41
Includes LEV Sulfur Corr 1.36
Includes LEV Sulfur Corr 1.36
LDGT1
Includes LEV Sulfur Corr 1.23
Includes LEV Sulfur Corr 1.36
LDGT2
-------
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
4
4
5
5
5
5
5
5
5
5
5
5
6
6
6
6
6
6
6
6
6
6
7
7
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
90
91
92
94
96
97
01
04
94
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
94
04
90
91
93
95
96
00
03
50
94
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
03
50
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.340
.306
.318
.317
.318
.260
.258
.058
.586
.586
.589
.589
.589
.589
.593
.593
.593
.593
.453
.161
.161
.161
.161
.161
.066
.066
.066
.066
.040
.271
.271
.231
.231
.231
.202
.202
.202
.202
.040
.320
.290
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.019
.017
.017
.017
.017
.012
.012
.008
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.029
.011
.011
.011
.011
.011
.006
.006
.006
.006
.006
.015
.015
.011
.011
.011
.010
.010
.010
.010
.006
.000
.000
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.
0.
0.
.049
. 044
.046
.046
.046
.030
.030
.014
.021
.021
.021
.021
.021
.011
.011
.011
.011
.010
.038
.038
.027
.027
.027
.024
.024
.024
.024
.010
2
2
2
2
2
9
9
8
8
8
8
8
8
7
7
7
7
8
3
3
9
9
9
9
9
9
9
8
.13
.13
.13
.13
.13
.25
.25
.10
.90
.90
.90
.90
.90
.87
.87
.87
.87
.10
.87
.87
.21
.21
.21
.01
.01
.01
.01
.10
Includes LEV Sulfur Corr
HDGV
1.36
LDDV
LDDT
Assumes 25% LDT1 and 75% LDT2
HDDV
-------
TOG BERs - I/M Denver Baseline Case
File: DNV_IM_B.BER
LDGV
0099
211
211
211
211
211
211
211
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
65
68
70
72
75
76
78
80
81
83
84
85
86
87
88
89
90
91
92
93
95
01
04
65
68
70
72
75
76
77
79
81
83
84
85
86
87
88
89
90
91
92
94
95
01
04
65
70
74
79
81
83
84
85
86
87
88
89
67
69
71
74
75
77
79
80
82
83
84
85
86
87
88
89
90
91
92
94
00
03
50
67
69
71
74
75
76
78
80
82
83
84
85
86
87
88
89
90
91
93
94
00
03
50
69
73
78
80
82
83
84
85
86
87
88
89
9
5
4
4
2
2
2
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
9
5
4
4
3
3
3
1
2
1
0
0
0
0
0
0
0
0
0
0
0
0
0
12
8
8
1
1
1
0
0
0
0
0
0
ZM
.660
.765
.741
.783
.029
.035
.042
.704
.485
.258
.257
.251
.303
.299
.290
.288
.200
.198
.197
.195
.169
.094
.094
.660
.765
.741
.720
.423
.445
.434
.665
.166
.502
.729
.604
.596
.608
.608
.614
.403
.382
.398
.317
.214
.110
.110
.751
.822
.822
.686
.480
.507
.738
.626
.636
.641
.635
.635
DR1
0.186
0.258
0.382
0.165
0.282
0.283
0.284
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.
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.
.211
. 149
.051
.051
.050
.058
.057
.056
.055
.019
.018
.018
.018
.011
.009
.009
.186
.258
.382
.176
.270
.272
.271
.282
.044
.045
.022
.022
.022
.022
.022
.022
.018
.017
.017
.017
.012
.008
.008
.186
.258
.176
.286
.044
.045
.022
.023
.023
.023
.023
.023
DR2 Flex
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
0
0
0
0
0
0
0
0
.209
.140
.140
.137
.040
.040
.040
.040
.022
.015
.015
.143
.145
.108
.107
.106
.108
.108
.109
.047
. 044
.046
.046
.025
.016
.016
.143
.146
.109
.111
.113
.114
.113
.113
1
2
2
2
2
2
2
2
8
7
7
1
1
4
4
4
4
4
4
2
2
2
2
9
8
8
1
1
4
4
4
4
4
4
Pt
.53
.22
.22
.22
.13
.13
.13
.13
.90
.87
.87
.73
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.06
.29
.29
.73
.73
.41
.41
.41
.41
.41
.41
Includes LEV Sulfur Corr 1.36
Includes LEV Sulfur Corr 1.36
LDGT1
Includes LEV Sulfur Corr 1.23
Includes LEV Sulfur Corr 1.23
LDGT2
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
4
4
5
5
5
5
5
5
5
5
5
5
6
6
6
6
6
6
6
6
6
6
7
7
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
90
91
92
94
96
97
01
04
94
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
94
04
90
91
93
95
96
00
03
50
94
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
03
50
0
0
0
0
0
0
0
0
0
0
1
1
1
1
1
1
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.425
.382
.398
.317
.318
.260
.258
.258
.996
.996
.001
.001
.001
.001
.008
.008
.008
.008
.453
.161
.161
.161
.161
.161
.161
.066
.066
.066
.066
.342
.342
.291
.291
.291
.291
.255
.255
.255
.255
.735
.668
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.019
.017
.017
.017
.017
.012
.012
.012
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.029
.011
.011
.011
.011
.011
.011
.006
.006
.006
.006
.015
.015
.011
.011
.011
.011
.010
.010
.010
.010
.000
.000
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.
0.
0.
.049
. 044
.046
.046
.046
.030
.030
.030
.021
.021
.021
.021
.021
.021
.011
.011
.011
.011
.038
.038
.027
.027
.027
.027
.024
.024
.024
.024
2
2
2
2
2
9
9
9
8
8
8
8
8
8
7
7
7
7
3
3
9
9
9
9
9
9
9
9
.13
.13
.13
.13
.13
.25
.25
.25
.90
.90
.90
.90
.90
.90
.87
.87
.87
.87
.87
.87
.21
.21
.21
.21
.01
.01
.01
.01
HDGV
LDDV
LDDT Assumes 25% LDT1 and 75% LDT2
High Alt includes 1.26
correction to ZM
HDDV
-------
TOG BERs - I/M Denver Control Case
File: DNV_IM_C.BER
LDGV
0099
211
211
211
211
211
211
211
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
65
68
70
72
75
76
78
80
81
83
84
85
86
87
88
89
90
91
92
93
95
01
04
65
68
70
72
75
76
77
79
81
83
84
85
86
87
88
89
90
91
92
94
95
01
04
65
70
74
79
81
83
84
85
86
87
88
89
67
69
71
74
75
77
79
80
82
83
84
85
86
87
88
89
90
91
92
94
00
03
50
67
69
71
74
75
76
78
80
82
83
84
85
86
87
88
89
90
91
93
94
00
03
50
69
73
78
80
82
83
84
85
86
87
88
89
9
5
4
4
2
2
2
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
9
5
4
4
3
3
3
1
2
1
0
0
0
0
0
0
0
0
0
0
0
0
0
12
8
8
1
1
1
0
0
0
0
0
0
ZM
.660
.765
.741
.783
.029
.035
.042
.704
.485
.258
.257
.251
.303
.299
.290
.288
.200
.198
.197
.195
.169
.094
.057
.660
.765
.741
.720
.423
.445
.434
.665
.166
.502
.729
.604
.596
.608
.608
.614
.403
.382
.398
.317
.214
.110
.058
.751
.822
.822
.686
.480
.507
.738
.626
.636
.641
.635
.635
DR1
0.186
0.258
0.382
0.165
0.282
0.283
0.284
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.
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.
.211
. 149
.051
.051
.050
.058
.057
.056
.055
.019
.018
.018
.018
.011
.009
.008
.186
.258
.382
.176
.270
.272
.271
.282
.044
.045
.022
.022
.022
.022
.022
.022
.018
.017
.017
.017
.012
.008
.008
.186
.258
.176
.286
.044
.045
.022
.023
.023
.023
.023
.023
DR2 Flex
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
0
0
0
0
0
0
0
0
.209
.140
.140
.137
.040
.040
.040
.040
.022
.015
.014
.143
.145
.108
.107
.106
.108
.108
.109
.047
. 044
.046
.046
.025
.016
. 014
.143
.146
.109
.111
.113
.114
.113
.113
1
2
2
2
2
2
2
2
8
7
8
1
1
4
4
4
4
4
4
2
2
2
2
9
8
8
1
1
4
4
4
4
4
4
Pt
.53
.22
.22
.22
.13
.13
.13
.13
.90
.87
.10
.73
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.06
.29
.10
.73
.73
.41
.41
.41
.41
.41
.41
Includes LEV Sulfur Corr 1.36
Includes LEV Sulfur Corr 1.36
LDGT1
Includes LEV Sulfur Corr 1.23
Includes LEV Sulfur Corr 1.36
LDGT2
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
4
4
5
5
5
5
5
5
5
5
5
5
6
6
6
6
6
6
6
6
6
6
7
7
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
90
91
92
94
96
97
01
04
94
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
94
04
90
91
93
95
96
00
03
50
94
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
03
50
0
0
0
0
0
0
0
0
0
0
1
1
1
1
1
1
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.425
.382
.398
.317
.318
.260
.258
.058
.996
.996
.001
.001
.001
.001
.008
.008
.008
.008
.453
.161
.161
.161
.161
.161
.161
.066
.066
.066
.040
.342
.342
.291
.291
.291
.291
.255
.255
.255
.040
.735
.668
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.019
.017
.017
.017
.017
.012
.012
.008
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.029
.011
.011
.011
.011
.011
.011
.006
.006
.006
.006
.015
.015
.011
.011
.011
.011
.010
.010
.010
.006
.000
.000
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.
0.
0.
.049
. 044
.046
.046
.046
.030
.030
.014
.021
.021
.021
.021
.021
.021
.011
.011
.011
.010
.038
.038
.027
.027
.027
.027
.024
.024
.024
.010
2
2
2
2
2
9
9
8
8
8
8
8
8
8
7
7
7
8
3
3
9
9
9
9
9
9
9
8
.13
.13
.13
.13
.13
.25
.25
.10
.90
.90
.90
.90
.90
.90
.87
.87
.87
.10
.87
.87
.21
.21
.21
.21
.01
.01
.01
.10
Includes LEV Sulfur Corr
HDGV
1.36
LDDV
LDDT Assumes 25% LDT1 and 75% LDT2
High Alt includes 1.26
correction to ZM
for pre-2004 MY
HDDV
-------
Off-Cycle Corrections - I/M 1990
IV
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
MYA
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
MYB
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
AGG
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.079
.079
.078
.090
.089
.081
.081
.122
.120
.118
.137
.137
.136
.135
.135
.211
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.290
.290
.290
.290
.290
.290
.220
.150
.052
.010
.048
.048
.048
.055
.055
.050
.050
.074
. 074
.073
.078
.078
. 077
. 077
.091
.091
.258
.249
.238
.230
.230
.230
.230
A/C
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.016
.016
.015
.018
.017
.016
.016
.023
.023
.023
.026
.026
.026
.026
.025
.037
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.010
.010
.010
.010
.010
.010
.003
.995
.985
.980
.002
.002
.002
.003
.003
.003
.003
.004
.004
.004
.004
.004
.004
.004
.004
.004
.011
.011
.010
.010
.010
.010
.010
UC/FTP Toxics
BNZ
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.128
.156
.165
.175
.213
.228
.247
.273
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.128
.156
.167
. 177
.193
.211
ACET
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.920
.935
.940
.945
.966
.973
.983
.997
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.920
.935
.941
.946
.955
.965
Mass Fraction Ratios
FORM
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
1.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.897
.936
.949
.964
.018
.039
.066
.103
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.897
.936
.953
.967
.989
.015
13BD
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.712
.760
.776
.793
.860
.885
.918
.963
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.712
.760
.780
.797
.824
.856
MTBE
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.963
.943
.936
.929
.900
.890
.876
.856
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.963
.943
.934
.927
.915
.902
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
4
5
6
7
8
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1965
1965
1965
1965
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
2050
2050
2050
2050
2050
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.230
.230
.230
.230
.230
.230
.230
.290
.290
.290
.290
.290
.290
.223
.155
.061
.020
.044
. 044
. 044
.043
.042
.048
. 047
.047
.046
.052
.051
.050
.048
. 047
.090
.091
.264
.253
.241
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.290
.290
.290
.290
.290
.190
.090
.040
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
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.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.008
.005
.002
.000
.998
.998
.998
.998
.998
.998
.998
.998
.998
.997
.997
.997
.998
.998
.996
.996
.989
.989
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.216
.219
.284
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.128
.156
.166
.177
.193
.212
.216
.219
.284
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.967
.968
.003
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.920
.935
.940
.946
.955
.965
.967
.969
.003
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.022
.026
.118
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.897
.936
.951
.966
.990
.016
.022
.026
.118
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
0.
0.
0.
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.864
.869
.982
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.712
.760
.778
.796
.825
.857
.865
.869
.982
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
.899
.896
.848
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.963
.943
.935
.927
.915
.902
.898
.896
.848
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
-------
Off-Cycle Corrections - I/M 1996 a
IV MYA MYB AGG A/C
1 1965 1965 1.079 1.016
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.079
.079
.091
.091
.083
.083
.130
.129
.128
.140
.139
.139
.139
.138
.210
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.290
.290
.290
.290
.290
.290
.220
.150
.052
.010
.048
.048
.048
.056
.056
.051
.051
.078
.078
. 077
.079
.079
.079
.079
.089
.089
.299
.293
.288
.230
.230
.230
.230
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.016
.016
.018
.018
.016
.016
.025
.024
.024
.026
.026
.026
.026
.026
.037
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.010
.010
.010
.010
.010
.010
.003
.995
.985
.980
.002
.002
.002
.003
.003
.003
.003
.004
.004
.004
.004
.004
.004
.004
.004
.004
.012
.012
.012
.010
.010
.010
.010
UC/FTP Toxics
BNZ
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.138
.140
.142
.175
.178
.182
.189
.248
.262
.281
.306
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.138
.147
. 149
.151
.154
ACET
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.926
.926
.928
.945
.947
.949
.952
.984
.992
.002
.015
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.926
.930
.931
.932
.934
Mass Fraction Ratios
FORM
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.894
.911
.914
.917
.964
.969
.974
.983
.067
.088
.114
.150
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.894
.911
.923
.927
.930
.934
13BD
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.708
.729
.732
.737
.794
.799
.806
.817
.920
.945
.977
.022
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.708
.729
.744
.748
.752
.757
MTBE
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.956
.955
.953
.928
.926
.923
.919
.875
.864
.850
.832
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.956
.950
.948
.946
.944
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
4
5
6
7
8
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1965
1965
1965
1965
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
2050
2050
2050
2050
2050
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.230
.230
.230
.230
.230
.230
.230
.290
.290
.290
.290
.290
.290
.223
.155
.061
.020
.044
. 044
. 044
.044
.044
.050
.050
.050
.050
.058
.057
.056
.055
.054
.089
.089
.313
.306
.299
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.290
.290
.290
.290
.290
.190
.090
.040
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
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.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.008
.005
.002
.000
.998
.998
.998
.998
.998
.997
.997
.997
.997
.997
.997
.997
.997
.997
.996
.996
.987
.987
.988
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.157
.163
.207
.216
.227
.242
.261
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.138
.143
.146
. 148
.151
.155
.162
.206
.216
.228
.243
.263
.275
.284
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.936
.939
.962
.967
.973
.981
.991
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.926
.928
.929
.931
.933
.935
.938
.962
.967
.973
.982
.992
.999
.003
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.938
. 947
.010
.022
.038
.059
.087
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.894
.911
.918
.922
.925
.930
.935
.945
.008
.022
.039
.061
.089
.106
.118
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.762
.773
.850
.865
.884
.910
. 944
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.708
.729
.737
.742
.746
.752
.759
.770
.848
.865
.885
.912
. 947
.967
.982
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
.942
.937
.905
.898
.890
.879
.865
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.956
.952
.950
.949
.946
.943
.939
.905
.898
.890
.878
.863
.855
.848
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
-------
Off-Cycle Corrections - Non-I/M 1990 UC/FTP Toxics
IV
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
MYA
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
MYB
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
AGG
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.079
.079
.078
.090
.089
.081
.081
.122
.120
.118
.137
.137
.136
.135
.135
.211
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.287
.287
.287
.287
.287
.287
.218
. 149
.051
.010
.048
.048
.048
.055
.055
.050
.050
.074
. 074
.073
.078
.078
. 077
. 077
.091
.091
.258
.249
.238
.230
.230
.230
.230
A/C
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.016
.016
.015
.018
.017
.016
.016
.023
.023
.023
.026
.026
.026
.026
.025
.037
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.010
.010
.010
.010
.010
.010
.003
.995
.985
.980
.002
.002
.002
.003
.003
.003
.003
.004
.004
.004
.004
.004
.004
.004
.004
.004
.011
.011
.010
.010
.010
.010
.010
BNZ
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.151
.158
.169
.204
.219
.239
.270
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.151
.163
.173
. 187
.204
ACET
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.932
.936
.942
.961
.968
.979
.996
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.932
.939
. 944
.952
.961
Mass Fraction Ratios
FORM
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
1.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.895
.930
.940
.955
.005
.026
.055
.099
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.895
.930
.946
.961
.981
.005
13BD
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.709
.752
.764
.782
. 844
.869
.905
.959
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.709
.752
.772
.789
.815
.843
MTBE
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.946
.941
.933
.907
.896
.881
.858
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.946
.938
.930
.920
.907
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
4
5
6
7
8
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1965
1965
1965
1965
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
2050
2050
2050
2050
2050
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.230
.230
.230
.230
.230
.230
.230
.290
.290
.290
.290
.290
.290
.223
.155
.061
.020
.044
. 044
. 044
.043
.042
.048
. 047
.047
.046
.052
.051
.050
.048
. 047
.090
.091
.264
.253
.241
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.290
.290
.290
.290
.290
.190
.090
.040
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
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.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.008
.005
.002
.000
.998
.998
.998
.998
.998
.998
.998
.998
.998
.997
.997
.997
.998
.998
.996
.996
.989
.989
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.210
.217
.284
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.151
.162
.172
.188
.204
.210
.217
.284
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.964
.968
.003
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.932
.938
.944
.952
.961
.964
.968
.003
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.013
.023
.118
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.895
.930
.945
.960
.982
.005
.014
.024
.118
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
0.
0.
0.
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.854
.866
.982
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.709
.752
.771
.789
.816
. 844
.855
.867
.982
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
.903
.898
.848
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.946
.938
.931
.919
.907
.903
.897
.848
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
-------
Off-Cycle Corrections - Non-I/M 1996 UC/FTP Toxics
IV
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
MYA
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
MYB
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
AGG
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.079
.079
.079
.091
.091
.083
.083
.130
.129
.128
.140
.139
.139
.139
.138
.210
.212
.212
.212
.212
.212
.212
.212
.212
.212
.212
.212
.212
.212
.212
.267
.267
.267
.267
.267
.267
.202
.138
.048
.009
.048
.048
.048
.056
.056
.051
.051
.078
.078
. 077
.079
.079
.079
.079
.089
.089
.299
.293
.288
.216
.216
.216
.216
A/C
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.016
.016
.016
.018
.018
.016
.016
.025
.024
.024
.026
.026
.026
.026
.026
.037
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.010
.010
.010
.010
.010
.010
.003
.995
.985
.980
.002
.002
.002
.003
.003
.003
.003
.004
.004
.004
.004
.004
.004
.004
.004
.004
.012
.012
.012
.010
.010
.010
.010
BNZ
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.131
.133
.135
. 164
.168
.172
. 178
.231
.246
.266
.293
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.131
.137
. 140
.143
.146
ACET
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.922
.923
.924
.939
.941
.944
. 947
.975
.983
.994
.008
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.922
.925
.926
.928
.930
Mass Fraction Ratios
FORM
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.894
.901
.904
.907
.948
.954
.960
.968
. 044
.065
.093
.132
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.894
.901
.910
.914
.918
.922
13BD
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.708
.717
.720
.724
.774
.781
.789
.798
.891
.917
.951
.999
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.708
.717
.728
.732
.737
.743
MTBE
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.961
.960
.958
.937
.934
.931
.927
.887
.876
.861
.841
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.961
.957
.955
.953
.950
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
4
5
6
7
8
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1965
1965
1965
1965
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
2050
2050
2050
2050
2050
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.216
.216
.216
.216
.216
.216
.216
.273
.273
.273
.273
.273
.273
.209
. 146
.057
.019
.044
. 044
. 044
.044
.044
.050
.050
.050
.050
.058
.057
.056
.055
.054
.089
.089
.313
.306
.299
.212
.212
.212
.212
.212
.212
.212
.212
.212
.212
.212
.212
.212
.267
.267
.267
.267
.267
.175
.083
.037
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
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.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.008
.005
.002
.000
.998
.998
.998
.998
.998
.997
.997
.997
.997
.997
.997
.997
.997
.997
.996
.996
.987
.987
.988
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.150
.156
.195
.205
.217
.233
.256
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.131
.134
.137
. 140
. 144
.148
.154
.195
.204
.217
.234
.257
.275
.284
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.932
.935
.956
.961
.967
.976
.988
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.922
.924
.925
.927
.928
.931
.934
.956
.961
.968
.977
.989
.999
.003
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
0.
0.
0.
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.928
.936
.993
.006
.023
.046
.079
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.894
.901
.906
.910
.914
.919
.926
.934
.992
.006
.024
.048
.081
.106
.118
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.750
.760
.829
.845
.866
.894
.934
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.708
.717
.723
.727
.732
.739
.747
.757
.827
.845
.867
.896
.937
.967
.982
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
.947
.943
. 914
.907
.898
.886
.869
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.961
.959
.957
.955
.952
.948
.944
. 914
.907
.897
.885
.868
.855
.848
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
-------
Off-Cycle Corrections - Non-I/M 2007 UC/FTP Toxics
IV
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
MYA
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
MYB
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
AGG
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.079
.079
.079
.091
.091
.083
.083
.130
.129
.128
.140
.139
.139
.139
.138
.210
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.228
.287
.287
.287
.287
.287
.287
.218
. 149
.051
.010
.048
.048
.048
.056
.056
.051
.051
.078
.078
. 077
.079
.079
.079
.079
.089
.089
.299
.293
.288
.225
.225
.225
.225
A/C
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
0.
0.
0.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.016
.016
.016
.018
.018
.016
.016
.025
.024
.024
.026
.026
.026
.026
.026
.037
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.010
.010
.010
.010
.010
.010
.003
.995
.985
.980
.002
.002
.002
.003
.003
.003
.003
.004
.004
.004
.004
.004
.004
.004
.004
.004
.012
.012
.012
.010
.010
.010
.010
BNZ
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.126
.126
.126
. 144
.145
.149
.150
.172
.174
.177
.180
.183
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.126
.126
. 127
. 127
.128
ACET
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.919
.919
.919
.929
.929
.931
.932
. 944
.945
.946
.948
.950
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.919
.919
.919
.920
.920
Mass Fraction Ratios
FORM
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.894
.894
.894
.894
.920
.921
.926
.928
.959
.963
.966
. 971
.975
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.894
.894
.894
.895
.896
.897
13BD
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.708
.708
.708
.708
.739
.741
.747
.750
.788
.792
.797
.802
.808
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.708
.708
.708
.709
.710
.711
MTBE
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.965
.965
.965
.952
.951
.948
. 947
.931
.929
.927
.925
.923
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.965
.965
.965
.964
.964
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
4
5
6
7
8
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1965
1965
1965
1965
1965
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
2050
2050
2050
2050
2050
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.225
.225
.225
.225
.225
.225
.225
.284
.284
.284
.284
.284
.284
.218
.152
.059
.020
.044
. 044
. 044
.044
.044
.050
.050
.050
.050
.058
.057
.056
.055
.054
.089
.089
.313
.306
.299
.225
.225
.225
.225
.225
.225
.225
.225
.225
.225
.225
.225
.225
.284
.284
.284
.284
.284
.186
.088
.039
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
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.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.008
.005
.002
.000
.998
.998
.998
.998
.998
.997
.997
.997
.997
.997
.997
.997
.997
.997
.996
.996
.987
.987
.988
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.129
.130
.157
.159
.161
.163
.166
.315
.315
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.126
.126
.126
.126
.126
.126
.126
.126
.151
.152
.155
.157
.160
.163
.166
.315
.315
.315
.315
.315
.315
.315
.315
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.920
.921
.936
.937
.938
.939
.940
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.919
.919
.919
.919
.919
.919
.919
.919
.932
.933
.934
.935
.937
.939
.940
.020
.020
.020
.020
.020
.020
.020
.020
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.898
.899
.939
.941
.944
. 947
.950
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.894
.894
.894
.894
.894
.894
.894
.894
.894
.929
.932
.935
.938
.942
.946
.951
.163
.163
.163
.163
.163
.163
.163
.163
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
1 .
1 .
1.
1.
.713
.715
.763
.766
.769
.773
.777
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.708
.708
.708
.708
.708
.708
.708
.708
.751
.754
.758
.762
.766
.772
.778
.037
.037
.037
.037
.037
.037
.037
.037
.000
.000
.000
.000
.000
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
1.
1.
1.
1.
.963
.962
.942
.940
.939
.937
.936
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.965
.965
.965
.965
.965
.965
.965
.965
. 947
.945
.944
.942
.940
.938
.935
.825
.825
.825
.825
.825
.825
.825
.825
.000
.000
.000
.000
.000
-------
CO BERs - Non-I/M
0044
112
112
112
112
112
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
65
68
70
72
75
80
81
82
83
84
85
86
87
88
89
90
91
65
68
70
72
75
79
81
84
85
86
87
88
89
90
91
65
70
79
81
84
85
86
87
88
89
90
91
67
69
71
74
79
80
81
82
83
84
85
86
87
88
89
90
91
67
69
71
74
78
80
83
84
85
86
87
88
89
90
91
69
78
80
83
84
85
86
87
88
89
90
91
78
56
42
40
17
6
4
4
2
2
2
2
2
2
2
2
2
78
56
42
40
24
12
14
6
6
6
6
6
6
5
5
93
60
12
14
6
6
6
6
6
6
5
5
ZM
.270
.340
.170
.940
.720
.090
.301
.301
.813
.813
.813
.795
.795
.795
.795
.188
.188
.270
.340
.170
.780
.550
.280
.503
.045
.045
.045
.045
.045
.045
.382
.382
.980
.080
.280
.503
.045
.045
.045
.045
.045
.045
.382
.382
DR1
2.250
2.550
3.130
2.350
2.460
1
2
2
0
0
0
0
0
0
0
0
0
2
2
3
2
2
2
1
0
0
0
0
0
0
0
0
2
2
2
1
0
0
0
0
0
0
0
0
.958
.441
.441
.191
.191
.191
.696
.696
.696
.696
.076
.076
.250
.550
.130
.440
.590
.430
.929
.496
.496
.496
.496
.496
.496
.245
.245
.250
.550
.430
.929
.496
.496
.496
.496
.496
.496
.245
.245
DR2 Flex
3
3
1
1
1
0
0
1
1
1
1
1
1
0
0
1
1
1
1
1
1
0
0
.037
.037
.650
.650
.650
.556
.556
.094
.094
.094
.094
.094
.094
.717
.717
.094
.094
.094
.094
.094
.094
.717
.717
1
1
2
2
2
1
1
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
Pt
.50
.50
.16
.16
.16
.85
.85
.34
.34
.34
.34
.34
.34
.37
.37
.34
.34
.34
.34
.34
.34
.37
.37
File: BER_CO.PRN
LDGV
LDGT1
LDGT2
-------
Hi Alt CO BERs - Non-I/M
0033
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
81
82
83
84
85
86
87
88
89
90
91
81
82
83
84
85
86
87
88
89
90
91
81
82
83
84
85
86
87
88
89
90
91
81
82
83
84
85
86
87
88
89
90
91
81
82
83
84
85
86
87
88
89
90
91
81
82
83
84
85
86
87
88
89
90
91
16
11
2
2
2
2
2
2
2
2
2
51
34
34
14
8
8
8
8
8
7
7
51
34
34
14
8
8
8
8
8
7
7
ZM
.815
.455
.839
.813
.813
.795
.795
.795
.795
.188
.188
.014
.770
.770
.968
.462
.462
.463
.462
.461
.533
.532
.014
.770
.770
.968
.462
.462
.463
.462
.461
.533
.532
DR1
2
2
0
0
0
0
0
0
0
0
0
1
1
1
0
0
0
0
0
0
0
0
1
1
1
0
0
0
0
0
0
0
0
.441
.441
.191
.191
.191
.696
.696
.696
.696
.076
.076
.929
.929
.929
.496
.496
.496
.496
.496
.496
.245
.245
.929
.929
.929
.496
.496
.496
.496
.496
.496
.245
.245
DR2 Flex
3
3
1
1
1
0
0
1
1
1
1
1
1
0
0
1
1
1
1
1
1
0
0
.037
.037
.650
.650
.650
.556
.556
.094
.094
.094
.094
.094
.094
.717
.717
.094
.094
.094
.094
.094
.094
.717
.717
1
1
2
2
2
1
1
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
Pt
.50
.50
.16
.16
.16
.85
.85
.34
.34
.34
.34
.34
.34
.37
.37
.34
.34
.34
.34
.34
.34
.37
.37
File: DNV_CO.PRN
LDGV
LDGT1
LDGT2
-------
I/M IV
1 1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
MY Agg Drv
1965 1.328
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
.328
.324
.370
.365
.375
.371
.432
.426
.419
.574
.568
.560
.552
.543
.861
.611
.611
.611
.611
.611
.611
.611
.611
.611
.611
.611
.328
.328
.324
.370
.365
.375
.371
.432
.426
.419
.574
.568
.560
.552
.543
.292
.318
.316
.314
.617
.617
.617
A/C
1.217
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
.217
.215
.237
.235
.240
.238
.265
.263
.260
.321
.319
.316
.313
.310
.407
.326
.326
.326
.326
.326
.326
.326
.326
.326
.326
.326
.217
.217
.215
.237
.235
.240
.238
.265
.263
.260
.321
.319
.316
.313
.310
.158
.169
.168
.167
.267
.267
.267
Non-I/M Factors
-------
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1987
1988
1989
1990
1991
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
.617
.617
.617
.617
.617
.125
.125
.124
.123
.121
.152
.151
.149
.147
.148
.146
.144
.141
.138
.292
.292
.320
.317
.314
.617
.617
.617
.617
.617
.617
.617
.617
.328
.328
.324
.370
.365
.375
.371
.432
.426
.419
.574
.568
.560
.552
.543
.861
.630
.630
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
.267
.267
.267
.267
.267
.069
.069
.068
.068
.067
.082
.081
.081
.080
.080
.079
.078
.077
.075
.140
.140
.150
.150
.148
.238
.238
.238
.238
.238
.238
.238
.238
.217
.217
.215
.237
.235
.240
.238
.265
.263
.260
.321
.319
.316
.313
.310
.407
.340
.340
I/M Factors
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
1983
1984
1985
1986
1987
1988
1989
1990
1991
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
.630
.630
.630
.630
.630
.630
.630
.630
.630
.328
.328
.324
.370
.365
.375
.371
.432
.426
.419
.574
.568
.560
.552
.543
.292
.318
.316
.314
.630
.630
.630
.630
.630
.630
.630
.630
.125
.125
.124
.123
.121
.152
.151
.149
.147
.148
.146
.144
.141
.138
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
.340
.340
.340
.340
.340
.340
.340
.340
.340
.217
.217
.215
.237
.235
.240
.238
.265
.263
.260
.321
.319
.316
.313
.310
.158
.169
.168
.167
.270
.270
.270
.270
.270
.270
.270
.270
.069
.069
.068
.068
.067
.082
.081
.081
.080
.080
.079
.078
.077
.075
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1
1
1
1
1
1
1
1
1
1
1
1
1
.292
.292
.320
.317
.314
.630
.630
.630
.630
.630
.630
.630
.630
1
1
1
1
1
1
1
1
1
1
1
1
1
.140
.140
.150
.150
.148
.240
.240
.240
.240
.240
.240
.240
.240
-------
MY
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
LDGV
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
0
.60
.60
.60
.60
.60
.60
.60
.60
.65
.65
.65
.65
.65
.65
.65
.65
.67
.69
.72
.74
.76
.78
.80
.83
.85
.87
.87
LDGT
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
0
.29
.29
.29
.29
.29
.29
.29
.29
.29
.29
.29
.29
.35
.35
.35
.35
.39
.43
.48
.52
.56
.60
.64
.69
.73
.77
.77
Malf
Rate
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
0
.050
.050
.050
.050
.050
.050
.050
.050
.038
.038
.038
.038
.038
.025
.025
.025
.025
.025
.010
.009
.008
.006
.005
.000
.000
.000
.000
Functioning S;
LDGV LDGT
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
0
.570
.570
.570
.570
.570
.570
.570
.570
.626
.626
.626
.626
.626
.634
.634
.634
.655
.677
.709
.732
.754
.777
.800
.826
.848
.870
.870
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
0
.276
.276
.276
.276
.276
.276
.276
.276
.279
.279
.279
.279
.337
.341
.341
.341
.382
.423
.471
.513
.556
.598
.641
.686
.728
.770
.770
-------
Oxygenated Fuels Benefits (% Red per 1 wt % Oxygen)
Normals
IV MY
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
% Red
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.0552
.0576
.0532
.0431
.0441
.0535
.0532
.0375
.0375
.0336
.0336
.0310
.0310
.0186
.0062
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0913
.0918
.0854
.0793
.0667
.0668
.0589
.0575
.0574
.0570
.0570
.0310
Highs
g/mi
4
4
4
4
4
3
3
O
J
o
J
2
2
2
2
2
1
1
1
1
1
1
0
0
0
0
0
0
0
0
0
0
4
4
4
4
4
O
J
O
J
3
3
O
J
O
J
2
.9
.9
.9
.9
.9
.2
.2
.0
.0
.8
.8
.8
.8
.2
.7
.4
.4
.4
.4
.4
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.2
.2
.2
.2
.2
.2
.8
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
% Red g/mi
.0645
.0663
.0630
.0554
.0561
.0540
.0537
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0920
.0924
.0874
.0828
.0733
.0638
.0551
.0536
.0535
.0530
.0530
.0530
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
-------
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
O
O
3
3
O
O
3
3
O
O
3
3
O
O
3
3
O
O
3
3
O
O
3
3
O
O
3
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.0310
.0186
.0062
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0913
.0918
.0854
.0793
.0667
.0668
.0589
.0575
.0574
.0570
.0570
.0310
.0310
.0310
.0310
.0186
.0062
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
.0000
2
2
1
1
1
1
1
1
0
0
0
0
0
0
0
0
0
0
4
4
4
4
4
O
O
3
3
O
O
2
2
2
2
2
1
1
1
1
1
1
1
1
1
1
1
1
.8
.2
.7
.4
.4
.4
.4
.4
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.2
.2
.2
.2
.2
.2
.8
.8
.8
.8
.2
.7
.4
.4
.4
.4
.4
.4
.4
.4
.4
.4
.4
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0920
.0924
.0874
.0828
.0733
.0638
.0551
.0536
.0535
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
.0530
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
20.
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
-------
2009
2010
0.0000
0.0000
1.4 0.0530
1.4 0.0530
20.5
20.5
-------
Appendix B
Methodology to Account for
Normal/High Emitter Distributions in T2ATTOX
(Development of Toxic-TOG Curves)
-------
Modeling Toxics to Account for Normal/High Emitter Distributions in T2ATTOX
1) Complex Model gives benzene emission rate at normal and high emission levels
2) Figure below relates benzene gram per mile to TOG gram per mile
3) Case: MY cohort fleet with FTP TOGBase&el = X (X is calculated within MOBILE)
300
250
Benzene 200
150
100
50
0
Fleet X High
TOG Emission Rate Basefuel
4) Assume: This fleet is a mix of
X - FTP TOGM m , ,
TLT _ Normalaasejuel
H FTP TOG
HighBasefuel NormalBasefuel
X 100 %
-------
J7TP TOf J^TP
rir J-U^J r ir
5) Question: What is the fleet's benzene on fuel Fl?
Answer:
r y D_ , AT y D_
// ^ DZHishFuelFl 7VTV ^ DZNormal FuelFl
X - FTP TOG,, FTP TOGrr - X
X (BzH .) + ( - ^ - ) X (BzN
Hm N
FTP TOGH - FTP TOGN FTP TOGH - FTP TOGN
FTP TOG,, X BzM . - FTP TOGM X Bzn ff, Bzn - BzM
_ / n TV rl TV ri rl / ri TV \
FTP TOG,, - FTP TOG,, FTP TOG^ - FTP TOG,,
n N n N
Techl + "Fl Techl *
(Mass emission rate of benzene on Fuel Fl, including the effect of fuel Fl on TOG)
-------
Bz % =
X
6) Inside MOBILESb:
No fleet ought to be cleaner than TOG FTPN or dirtier than TOG FTPH
If base fuel is not indolene, need to be sure commercial fuel adjustment is applied
before X is used with A and B
I/M adjustment happens before toxic number calculated
Other adjustments (non-FTP speed, temp, etc.) have to come after A and B are
applied
7) For non-complex model technology types:
A = 0
B = (* ) * (
voc
Fuel Baseline
-------
Appendix C
Equations Used to Generate Toxics Fractions
for Non-Complex Model Vehicles
Non-Catalyst and Oxidation Catalyst LDGVs, LDGT1, LDGT2s
All Heavy-Duty Gasoline Vehicles and Motorcycles
All Diesel Vehicles
-------
Exhaust Toxic Fraction Equations for LDGV with Oxidation Catalysts, Non-
Catalyst LDGV, HDGV, LDDV and HDDV
Table 1 presents equations for estimating exhaust toxic fractions for light-duty gasoline
vehicles with oxidation catalysts, light duty non-catalyst gasoline vehicles, heavy duty gasoline
vehicles, and heavy duty diesel vehicles. Exhaust benzene, 1,3-butadiene, formaldehyde, and
acetaldehyde fractions for light duty gasoline vehicles with three-way catalysts and three-way
plus oxidation catalysts, as well as evaporative benzene fractions for all catalyst technologies and
vehicle classes, will be estimated using the Complex Model.
Benzene
For LDGVs with no catalyst or an oxidation catalyst, and for HDGVs with no catalyst,
the equation used was:
Bz%THC = (0.8551*(volume % benzene) + 0.12198*(volume % aromatics) - 1.1626)
For FtDGVs with three-way catalysts, the equation used was:
Bz%THC = 1.077 + 0.7732*(volume % benzene) +
0.0987*(volume % aromatics - volume % benzene)
These equations were used in the "Motor Vehicle-Related Air Toxics Study" (EPA, 1993) and
were originally developed for the draft Regulatory Impact Analysis for RVP regulations (EPA,
1987). The benzene/TOG fractions for LDDVs, LDDTs, and HDDVs in Table 1 were based on
analysis of available speciation data (Springer, 1977; Springer, 1979; Bass andNewkirk, 1995;
CE-CERT, 1998).
Formaldehyde
Formaldehyde/TOG fractions for vehicles running on baseline gasoline and diesels were
based on analysis of available speciation data (see attachment). The TOG fraction for
LDGVs/LDGTs with oxidation catalysts, running on baseline fuel, was based on data from fifty
vehicles tested in eleven studies (Urban, 1980a; Springer, 1979; Sigsbyetal., 1987; Smith, 1981;
Stump et al., 1989, 1990, 1994, 1996; Auto/Oil, 1990; Boekhaus et al., 1991; Warner-Selph and
Smith, 1991; Colorado Department of Health, 1987). The TOG fraction for LDGVs/LDGTs
without catalysts, running on baseline fuel, was based on data from sixteen vehicles tested in five
studies (Urban, 1981, Urban 1980a, Sigsby et al., 1987, Warner-Selph and Smith, 1991, Stump
et. al, unpublished). The LDDV fraction was based on data from seven vehicles tested in two
studies (Springer, 1977; Springer, 1979). The FtDDV fraction were based on data from four
engines in three studies (Springer, 1979; Bass and Newkirk, 1995; CE-CERT, 1998). The
fraction for FtDGVs without catalysts was based on data from two engines in two studies
(Springer, 1979; Bass and Newkirk, 1995). The three-way fraction for FtDGVs was based on
data from one engine in one study (Bass and Newkirk, 1995).
-------
To calculate TOG fractions for vehicles running on MTBE blends and gasohol,
adjustment factors were applied to the baseline emission fractions for each vehicle class/catalyst
combination based on average percent change. The adjustment factors were obtained by
comparing data from vehicles running on baseline gasoline to data from the same vehicles
running on oxygenated gasoline. For MTBE, change was defined by solving the equation:
TOG frac @ 0% MTBE * (1 + (change/2.7) * Ox) = TOG frac @ 15% MTBE
For ethanol, change was defined by solving the equation:
TOG frac @ 0% EtOH * (1 + (change/3.5) * Ox) = TOG frac @ 10% EtOH
The data used to develop the change estimates are provided in the attachment.
Data from five vehicles in three studies were used to develop the MTBE change estimate
for LDGVs/LDGTs with oxidation catalysts (Auto/Oil, 1990; Boekhaus et al., 1991; Stump et al.,
1994). Data from two vehicles in two studies were used to develop the MTBE change estimate
for LDGVs/LDGTs without catalysts (Warner-Selph and Smith, 1991; Stump, 1997). Data from
one vehicle was used to develop the MTBE change estimate for non-catalyst HDGVs (Bass and
Newkirk, 1995). For catalyst-equipped HDGVs, the MTBE change estimate for LDGVs with
three-way catalysts from the EPA document, "Motor Vehicle-Related Air Toxics Study" was
used as a surrogate (EPA, 1993).
For ethanol, data from ten vehicles in three studies were used to develop the change
estimate for LDGVs/LDGTs with oxidation catalysts (Warner-Selph and Smith, 1991; Colorado
Department of Health, 1987; Stump et al., 1996). Data from five vehicles in two studies were
used to develop the ethanol change estimate for LDGVs/LDGTs/HDGVs without catalysts
(Warner-Selph and Smith, 1991; Colorado Department of Health, 1987). For catalyst-equipped
HDGVs, the ethanol change estimate for LDGVs with three-way catalysts from the EPA
document, "Motor Vehicle-Related Air Toxics Study" was used as a surrogate (EPA, 1993).
Acetaldehyde
Acetaldehyde/TOG fractions for vehicles running on baseline gasoline and diesels were
based on analysis of the same speciation data used for formaldehyde (see attachment). The
adjustment factors for MTBE blends and gasohol were also obtained using the same equations
and data that were used for formaldehyde.
1.3-Butadiene
1,3-butadiene/TOG fractions for vehicles running on baseline gasoline and diesels were
based on analysis of available speciation data (see attachment). The TOG fraction for
LDGVs/LDGTs with oxidation catalysts, running on baseline fuel, was based on data from fifty
-------
vehicles tested in ten studies (Urban, 1980a; Springer, 1979; Sigsby et al., 1987; Smith, 1981;
Stump et al., 1989, 1990, 1994, 1996; Auto/Oil, 1990; Boekhaus et al., 1991; Warner-Selph and
Smith, 1991; CARS, 1991). The TOG fraction for LDGVs/LDGTs without catalysts, running on
baseline fuel, was based on data from eighteen vehicles tested in three studies (CARB, 1991;
Stump, 1997; Warner-Selph and Smith, 1991). The LDDV fraction was based on data from two
vehicles tested in one study (CARB, 1991). The HDDV fraction was based on data from three
engines in three studies (CARB, 1991; Bass and Newkirk, 1995; CE-CERT, 1998). The fraction
for HDGVs without catalysts and HDGVs with catalysts were both based on data from one
engine in one study (Bass and Newkirk, 1995).
The adjustment factors were also obtained using the same equations and data that were
used for formaldehyde and acetaldehyde, with one exception. The adjustment factor for
formaldehyde and acetaldehyde with an MTBE blend uses a change estimate from LDGVs with
three-way catalysts as a surrogate. However, for 1,3-butadiene, the estimate is based on data
from one vehicle in one study (Bass and Newkirk, 1995).
MTBE
MTBE/TOG fractions were based on available speciation data. These data were from
vehicles running on fuels with varying levels of MTBE. To obtain an average 15% MTBE
fraction across studies for a given vehicle class/technology group, an assumption was made that
the relationship between MTBE in the fuel and exhaust was linear. MTBE/TOG fractions from
vehicles running on a blend with X percent MTBE were adjusted to represent the emission
fractions for a 15% by volume blend as follows:
TOG frac @ 15% MTBE = TOG frac @ X% MTBE * (2.7 / wt. % oxygen)
The resultant MTBE emission fractions for a 15% blend were used to develop the equations in
Table 1.
Data from five vehicles in three studies were used to develop the 15% MTBE emission
fraction for LDGVs/LDGTs with oxidation catalysts (Auto/Oil, 1990; Boekhaus et al., 1991;
Stump et al., 1994). Data from one vehicle was used to develop the fraction for LDGVs/LDGTs
without catalysts (Warner-Selph and Smith, 1991), the fraction for non-catalyst HDGVs (Bass
and Newkirk, 1995), and the fraction for HDGVs with catalysts (Bass and Newkirk, 1995).
-------
References
Auto/Oil Air Quality Improvement Research Program. 1990. Phase 1 Working Data Set
(published in electronic form). Prepared by Systems Applications International, San Rafael, CA.
Bass, E. A., and M. S. Newkirk. 1995. Reactivity Comparison of Exhaust Emissions from
Heavy-Duty Engines Operating on Gasoline, Diesel, and Alternative Fuels. Southwest Research
Institute, Report No. SwRI 9856, December, 1995.
Boekhaus, K. L., J. M. DeJovine, D. A. Paulsen, L. A. Rapp, J.S. Segal and D. J. Townsend.
1991. Clean Fuels Report 91-03: Fleet Test Emissions Data EC-Premium Emission Control
Gasoline. Arco Products Co., Anaheim, California.
CARB. 1991. Butadiene Emission Factors, memo from K. D. Drachand to Terry McGuire and
Peter Venturini, July 17, 1991.
College of Engineering - Center for Environmental Research and Technology. 1998. Evaluation
of Factor that Affect Diesel Exhaust Toxicity. Submitted to California Air Resources Board,
Contract No. 94-312.
Colorado Department of Health. 1987. Unpublished data from a motor vehicle emissions toxics
study of regulated and non-regulated pollutants. Aurora Emission Technical Center, Aurora,
Colorado.
EPA. 1987a. Draft Regulatory Impact Analysis: Control of Gasoline Volatility and Evaporative
Hydrocarbon Emissions from New Motor Vehicles. Ann Arbor, Michigan: Office of Mobile
Sources. July, 1987.
EPA. 1993. Motor Vehicle-Related Air Toxics Study. Office of Mobile Sources, Ann Arbor,
MI. Report No. EPA 420-R-93-005.
Sigsby, J. E., S. Tejeda, W. Ray, J. M. Lang, and J. W. Duncan. 1987. Volatile organic
compound emissions from 46 in-use passenger cars. Environ. Sci. Technol. 21:466-475.
Smith, L. R. 1981. Characterization of Exhaust Emissions from High Mileage Catalyst-
Equipped Automobiles. Ann Arbor, Michigan: U.S. Environmental Protection Agency, Office of
Mobile Sources. Publication no. EPA-460/3-81-024.
Springer, K. J. 1977. Investigation of Diesel-Powered Vehicle Emissions VII. Ann Arbor,
Michigan: U.S. Environmental Agency, Office of Mobile Sources. Publication no. EPA-460/3-
76-034.
-------
Springer, K. J. 1979. Characterization of Sulfates, Odor, Smoke, POM and Particulates from
Light and Heavy-Duty Engines Part IX. Ann Arbor, Michigan: U.S. Environmental Protection
Agency, Office of Mobile Sources. Publication no. EPA-460/3 -79-007.
Stump, F. D. 1997. Sun Fuels Alaska H Study. Unpublished data.
Stump, F. D., S. Tejada, W. Ray, D. Dropkin, F. Black, R. Snow, W. Crews, P. Siudak, C. O.
Davis, L. Baker and N. Perry. 1989. The influence of ambient temperature on tailpipe emissions
from 1984 to 1987 model year light-duty gasoline vehicles. Atmospheric Environment 23: 307-
320.
Stump, F. D., S. Tejeda, W. Ray, D. Dropkin, F. Black, R. Snow, W. Crews, P. Siudak, C. O.
Davis and P. Carter. 1990. The influence of ambient temperature on tailpipe emissions from
1985-1987 model year light-duty gasoline vehicles II. Atmospheric Environment 24A: 2105-
2112.
Stump, F. D., K. T. Knapp, W. D. Ray, P. D. Siudak, and R. F. Snow. 1994. Influence of
oxygenated fuels on the emissions from three pre-1985 light-duty passenger vehicles. J. Air &
Waste Manage. Assoc. 44:781-786.
Stump, F. D., K. T. Knapp, and W. D. Ray. 1996. Influence of ethanol-blended fuels on the
emissions from three pre-1985 light-duty passenger vehicles. J. Air & Waste Manage. Assoc. 46:
1149-1161.
Warner-Selph, M. A., and L. R. Smith. 1991. Assessment of Unregulated Emissions from
Gasoline Oxygenated Blends. Ann Arbor, Michigan: U.S. Environmental Protection Agency,
Office of Mobile Sources. Publication no. EPA-460/3-91-002.
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Vehicle Class/
Catalvst
Benzene
LDGV/oxcat
LDGV/noncat
HDGV/noncat
HDGV/cat
LDDV
Baseline Gasoline
Bz % TOG = 0.8551* (vol. % Bz) +
0.12198 * (vol. % Arom.) - 1.16261
Bz % TOG = 0.8551* (vol. % Bz) +
0.12198 * (vol. % Arom.) - 1.16262
Bz % TOG = 0.8551* (vol. % Bz) +
0.12198 * (vol. % Arom.) - 1.16263
Bz%TOG= 1.077 + 0.7732*(volume
% benzene) + 0.0987 * (volume %
aromatics - volume % benzene)4
Bz% TOG = 0.0200
MTBE Gasoline
Bz % TOG = 0.8551* (vol. % Bz) +
0.12198 * (vol. % Arom.) - 1.1626
Bz % TOG = 0.8551* (vol. % Bz) +
0.12198 * (vol. % Arom.) - 1.1626
Bz % TOG = 0.8551* (vol. % Bz) +
0.12198 * (vol. % Arom.) - 1.1626
Bz%TOG = 1.077 + 0.7732*(volume
% benzene) + 0.0987 * (volume %
aromatics - volume % benzene)
EtOH Gasoline
Bz % TOG = 0.8551* (vol. % Bz) +
0.12198 * (vol. % Arom.) - 1.1626
Bz % TOG = 0.8551* (vol. % Bz) +
0.12198 * (vol. % Arom.) - 1.1626
Bz % TOG = 0.8551* (vol. % Bz) +
0.12198 * (vol. % Arom.) - 1.1626
Bz%TOG= 1.077 + 0.7732*(volume
% benzene) + 0.0987 * (volume %
aromatics - volume % benzene)
1993 EPA Report, "Motor Vehicle-Related Air Toxics Study," EPA 420-R-93-005.
2From 1993 EPA Report, "Motor Vehicle-Related Air Toxics Study," EPA 420-R-93-005.
3From 1993 EPA Report, "Motor Vehicle-Related Air Toxics Study," EPA 420-R-93-005.
4From 1993 EPA Report, "Motor Vehicle-Related Air Toxics Study," EPA 420-R-93-005.
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Vehicle Class/
Catalvst
LDDT
HDDV
Formaldehyde
LDGV/oxcat
LDGV/noncat
HDGV/noncat
HDGV/cat
LDDV
LDDT
HDDV
Baseline Gasoline
Bz% TOG = 0.0200
Bz% TOG = 0.0105
Form % TOG = 0.0151
Form % TOG = 0.0224
Form % TOG = 0.0347
Form % TOG = 0.0054
Form % TOG =0.03 86
Form % TOG =0.03 86
Form % TOG = 0.0782
MTBE Gasoline
Form % TOG = 0.0151 + ((0.0151 *
1.2082)*(wt % MTBE/2.7))
Form % TOG = 0.0224 + ((0.0224 *
0.4336)*(wt % MTBE/2.7))
Form % TOG = 0.0347 + ((0.0347 *
0.1259)*(wt % MTBE/2.7))
Form % TOG = 0.0054 + ((0.0054 *
0.6746)*(wt % MTBE/2.7))5
EtOH Gasoline
Form % TOG = 0.0151 + ((0.0151 *
0.3350)*(wt % EtOH/3.5))
Form % TOG = 0.0224 + ((0.0224 *
0. 1034)*(wt % EtOH/3.5))
Form % TOG = 0.0347 + ((0.0347 *
0. 1034)*(wt % EtOH/3.5))
Form % TOG = 0.0054 + ((0.0054 *
0.4758)*(wt % EtOH/3.5))6
5Change with oxygenate estimate, 0.6746, from 3-way catalyst LDGV estimate in Appendix B4 of 1993 EPA Report, "Motor
Vehicle-Related Air Toxics Study," EPA 420-R-93-005.
6Change with oxygenate estimate, 0.4758, from 3-way catalyst LDGV estimate in Appendix B4 of 1993 EPA Report, "Motor
Vehicle-Related Air Toxics Study," EPA 420-R-93-005.
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Vehicle Class/
Catalvst
Acetaldehyde
LDGV/oxcat
LDGV/noncat
HDGV/noncat
HDGV/cat
LDDV
LDDT
HDDV
Baseline Gasoline
Acet% TOG = 0.0047
Acet% TOG = 0.0060
Acet% TOG = 0.0067
Acet % TOG = 0.0005
Acet% TOG =0.0123
Acet % TOG =0.0123
Acet % TOG = 0.0288
MTBE Gasoline
Acet % TOG = 0.0047 + ((0.0047 *
0.2556)*(wt % MTBE/2.7))
Acet % TOG = 0.0060 + ((0.0060 *
0.2303)*(wt % MTBE/2.7))
Acet % TOG = 0.0067
Acet % TOG = 0.0005 + ((0.0005 *
0.0826)*(wt % MTBE/2.7))7
EtOH Gasoline
Acet % TOG = 0.0047 + ((0.0047 *
2. 1074)*(wt % EtOH/3.5))
Acet % TOG = 0.0060 + ((0.0060 *
1.1445)*(wt%EtOH/3.5))
Acet % TOG = 0.0067 + ((0.0067 *
1.1445)*(wt%EtOH/3.5))
Acet % TOG = 0.0005 + ((0.0005 *
1.1369)*(wt%EtOH/3.5))8
7Change with oxygenate estimate, 0.0826, from 3-way catalyst LDGV estimate in Appendix B4 of 1993 EPA Report, "Motor
Vehicle-Related Air Toxics Study," EPA 420-R-93-005.
8Change with oxygenate estimate, 1.1369, from 3-way catalyst LDGV estimate in Appendix B4 of 1993 EPA Report, "Motor
Vehicle-Related Air Toxics Study," EPA 420-R-93-005.
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Vehicle Class/
Catalvst
1,3-Butadiene
LDGV/oxcat
LDGV/noncat
HDGV/noncat
HDGV/cat
LDDV
LDDT
HDDV
Baseline Gasoline
Buta% TOG = 0.0044
Buta% TOG = 0.0092
Buta% TOG = 0.0074
Buta% TOG = 0.0029
Buta% TOG =0.0090
Buta% TOG =0.0090
Buta% TOG = 0.0061
MTBE Gasoline
Buta % TOG = 0.0044 + ((0.0044 *
-0.2227)*(wt % MTBE/2.7))
Buta % TOG = 0.0092 + ((0.0092 *
0.1517)*(wt % MTBE/2.7))
Buta % TOG = 0.0074 + ((0.0074 *
-0.2172)*(wt % MTBE/2.7))
Buta % TOG = 0.0029 + ((0.0029 *
-0.3233)*(wt % MTBE/2.7))
EtOH Gasoline
Buta % TOG = 0.0044 + ((0.0044* -
0.2804)*(wt % EtOH/3.5))
Buta % TOG = 0.0092 + ((0.0092 *
0.1233)*(wt % EtOH/3.5))
Buta % TOG = 0.0074 + ((0.0074 *
0. 1233)*(wt % MTBE/2.7))
Buta % TOG = 0.0029 + ((0.0029 *
-0.1188)*(wt%EtOH/3.5))9
9Change with oxygenate estimate, -0.1188, from 3-way catalyst LDGV estimate in Appendix B4 of 1993 EPA Report, "Motor
Vehicle-Related Air Toxics Study," EPA 420-R-93-005.
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10
Vehicle Class/
Catalvst
MTBE
LDGV/oxcat
LDGV/noncat
HDGV/noncat
HDGV/cat
Baseline Gasoline
MTBE Gasoline
MTBE % TOG = 0.0464*(wt %
MTBE/2.7)
MTBE % TOG = 0.0333 *(wt %
MTBE/2.7)
MTBE % TOG = 0.0209*(wt %
MTBE/2.7)
MTBE % TOG = 0.0155*(wt %
MTBE/2.7)
EtOH Gasoline
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Appendix D
EPA's Suggested Methodology to Determine
Toxics Fuel Effects from the Complex Model
-------
(fuelsum6.wpd)
Toxics Fuel Effects Summary
I. Pre-1981 vehicles
A. Technology description: These vehicles include open-loop noncatalyst vehicles
(through 1974) and open-loop vehicles equipped with oxidation catalysts (1975-
1980 cars and trucks).
B. Fuel effect quantification
Baseline VOC emissions are derived from T2AT. The effects of fuel changes on
exhaust VOC emissions from these vehicles are taken from Greg Janssen's July
31, 1991 memo and are summarized below.
VOC Emission Effects
Fuel parameter
Oxygen, per 1 wt%
RVP, per 1 psi
Non-catalyst vehicles
- 1.6%
+ 1.8%
Oxidation catalyst vehicles
-4.46
+ 1.7%
To convert VOC FTP emissions to toxics emissions, Rich Cook has developed
mass fraction equations that describe toxics as a function of at most one or two
fuel properties.
Off-cycle VOC emissions are modeled in T2AT as an additive factor to FTP
emissions. These emissions may have different toxics fractions than on-cycle
emissions do. To model these emissions, the CARB database should be used to
develop off-cycle toxics fractions using one of two approaches: If available, data
from open-loop non-catalyst or oxidation catalyst cars should be used to develop
off-cycle toxics fractions. Otherwise, assume the same proportional change in
toxics fractions as was observed for more modern vehicles in the CARB database.
The CARB Predictive Model is not a viable option for these vehicles because
CARB has repudiated its earlier analysis of fuel effects on emissions from pre-
1981 cars.
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II. 1981-1983 Vehicles
A. Technology description: These vehicles fall into 3 classes: open-loop vehicles
equipped with oxidation catalysts, open-loop vehicles equipped with three-way
plus oxidation catalysts, and closed-loop vehicles. The latter class includes
vehicles with a range of fuel distribution systems and both three-way and three-
way plus oxidation catalysts. A small fraction of trucks have no controls.
B. Fuel effect quantification
1. Non-catalyst and open-loop oxidation catalyst vehicles: The equations
developed by Rich Cook can be used.
2. Open-loop vehicles with three-way + oxidation catalysts: These vehicles
will be modeled as open-loop vehicles with oxidation catalysts. The three-
way catalyst is primarily used to control NOx. Furthermore, in the
absence of closed-loop controls, the efficacy of the three-way catalyst on
older vehicles (all such vehicles will be at least 5 years old in 1990 and 11
years old in 1996) is questionable.
3. Closed-loop vehicles: The appropriate complex model technology types
can be used. The relationship between vehicle technologies and Complex
Model technology types is summarized below.
Technology Complex Model Tech Types
Carbureted (3-way and 3-way+oxcat) 9
3-way PFI Simple average of 1, 2, 5
3-way TBI Simple average of 3 & 6
3-way+oxcat PFI 4
3-way+oxcat TBI 7
Higher emitters (all technologies) Higher emitter
Off-cycle VOC emissions are modeled in T2AT as an additive factor to FTP
emissions. These emissions may have different toxics fractions than on-cycle
emissions do. To model these emissions, the CARB database should be used to
develop off-cycle toxics fractions using one of two approaches: If available, data
from cars with the corresponding vehicle technology should be used to develop
off-cycle toxics fractions. Otherwise, assume the same proportional change in
toxics fractions as was observed for more modern vehicles in the CARB database.
The CARB Predictive Model is not a viable option for these vehicles because the
CARB model does not distinguish between normal and higher emitters. It also is
-------
not designed to account for tech group to tech group variations, which can be
large (two-fold or even more).
C. Caveats
These vehicles are not equipped with adaptive learning, whereas the vehicles
tested for the Complex Model all had adaptive learning. Using Complex Model
fuel effects to represent the effect of fuel changes on emissions will tend to
underestimate the benefits of oxygenates in particular; it may also underestimate
the impact of RVP on exhaust emissions.
D. Additional work: Adjust tech group-specific emissions to account for tech group
to tech group variations in baseline VOC and toxics emissions, as described in
Appendix A.
-------
III. 1984-1985 cars, 1984-1987 trucks
A. Technology description: These vehicles are dominated by closed-loop
technologies without adaptive learning. They include a small percentage of open-
loop cars equipped with three-way plus oxidation catalysts and a few open-loop
trucks with oxidation catalysts, but they are dominated by closed-loop vehicles.
The latter class includes vehicles with a range of fuel distribution systems and
both three-way and three-way plus oxidation catalysts.
B. Fuel effect quantification
1. Open-loop vehicles: The same approach described for earlier open-loop
vehicles should be followed.
2. Closed-loop vehicles: The appropriate complex model technology types
can be used. The relationship between vehicle technologies and Complex
Model technology types is summarized below.
Technology Complex Model Tech Types
Carbureted (3-way and 3-way+oxcat) 9
3-way PFI Simple average of 1, 2, 5
3-wayTBI Simple average of 3 & 6
3-way+oxcat PFI 4
3-way+oxcat TBI 7
Higher emitters (all technologies) Higher emitter
The CARB Predictive Model is not a viable option for these vehicles because the
CARB model does not distinguish between normal and higher emitters. It also is
not designed to account for tech group to tech group variations, which can be
large (two-fold or even more).
3. Off-cycle adjustments: T2AT uses a multiplicative adjustment factor to
account for off-cycle adjustments for these and later vehicles. Toxics
fractions will have to be modified to account for the different toxics
fractions observed in off-cycle emissions.
Additional work: Adjust tech group-specific emissions to account for tech group
to tech group variations in baseline VOC and toxics emissions as discussed in
Appendix A.
-------
IV. 1986-1994 Tier 0 cars, 1988-1994 Tier 0 trucks
A. Technology description: These vehicles are dominated by closed-loop
technologies with adaptive learning. The mix of fuel distribution systems shifts
away from carbureted and TBI systems to PFI systems. Both three-way and three-
way plus oxidation catalyst designs are used.
B. Fuel effect quantification
The appropriate complex model technology types can be used. The relationship
between vehicle technologies and Complex Model technology types is
summarized below.
Technology Complex Model Tech Types
Carbureted (3-way and 3-way+oxcat) 9
3-way PFI Simple average of 1, 2, 5
3-way TBI Simple average of 3 & 6
3-way+oxcat PFI 4
3-way+oxcat TBI 7
Higher emitters (all technologies) Higher emitter
Off-cycle adjustments: T2AT uses a multiplicative adjustment factor to account
for off-cycle adjustments for these and later vehicles. Toxics fractions will have
to be modified to account for the different toxics fractions observed in off-cycle
emissions.
Additional work: Adjust tech group-specific emissions to account for tech group
to tech group variations in baseline VOC and toxics emissions, as described in
Appendix A.
-------
V. Tier 1 Vehicles
A. Technology description: These vehicles are dominated by closed-loop
technologies, PFI fuel metering systems, and adaptive learning. Both three-way
and three-way plus oxidation catalyst designs are used.
B. Fuel effect quantification: The appropriate complex model technology types can
be used. The relationship between vehicle technologies and Complex Model
technology types is summarized below.
Technology
3-way PFI
3-way TBI
3-way+oxcatPFI
3-way+oxcat TBI
Higher emitters (all technologies)
Complex Model Tech Types
Simple average of 1, 2, 5
Simple average of 3 & 6
4
7
Higher emitter
Off-cycle adjustments: T2AT uses a multiplicative adjustment factor to account
for off-cycle adjustments for these and later vehicles. Toxics fractions will have
to be modified to account for the different toxics fractions observed in off-cycle
emissions.
Additional work: Adjust tech group-specific emissions to account for tech group
to tech group variations in baseline VOC and toxics emissions, as per Appendix
A.
-------
VI. LEVs
A. Technology description: These vehicles are dominated by closed-loop
technologies, PFI fuel metering systems, adaptive learning, and advanced
catalysts. Three-way or three-way plus oxidation catalyst designs may be used.
B. Fuel effect quantification
2.
3.
Advanced catalyst designs show greater sulfur sensitivity than the
Complex Model suggests. The CRC sulfur study should be used to
develop the sulfur effect. The appropriate complex model technology
types can be used for the other fuel parameters to calculate percentage
changes in baseline toxics levels, which in turn can be calculated based on
the CRC sulfur study results.
A less desirable alternative would be to use Complex Model baseline
toxics emissions, adjusted to reflect lower VOC emissions from LEVs so
that average normal emitter emissions for LEVs do not fall below the
Complex Model normal level. The relationship between vehicle
technologies and Complex Model technology types that could be used is
summarized below.
Technology
3-way PFI
3-way+oxcat PFI
Higher emitters (all technologies)
Complex Model Tech Types
Simple average of 1, 2, 5
4
Higher emitter
It may be possible to further restrict the technology types used to evaluate
the impact of fuel changes on LEVs if information becomes available that
suggests EGR or supplementary air injection will become dominant.
Off-cycle adjustments: T2AT uses a multiplicative adjustment factor to
account for off-cycle adjustments for these vehicles. Toxics fractions will
have to be modified to account for the different toxics fractions observed
in off-cycle emissions.
Additional work
1. Option 1: Calculate baseline toxics using CRC data.
-------
2. Option 2: Adjust Complex Model baseline emissions to account for tech
group to tech group variations in VOC and toxics emissions.
-------
Appendix A: Adjusting Tech Group-Specific Emissions to Account for Tech Group
to Tech Group Variations in VOC and Toxics
The complex model normal emitter baseline numbers for VOC (482 mg/mi in summer
and 712 mg/mi in winter) and toxics are incorrectly assumed to be the same for all tech
groups. They need to be corrected by multiplying normal emitter baseline VOC and
toxics numbers by the following factors to reflect tech group to tech group variations in
VOC emissions:
Tech Correction New Summer baseline fuel emissions (mg/mi)
Group Factor
1 1.0223
2 0.8384
3 0.8458
4 1.5996
5 0.6582
6 0.7355
7 1.4305
9 0.9487
Winter VOC and toxics emissions would be 47.7% higher.
These emission factors should not be used to calculate in-use VOC or toxics emissions.
Rather, these factors should be used to determine the percent change in VOC and toxics
emissions due to fuel changes, which in turn should be applied to the VOC inputs to
T2ATTOX and to the toxics outputs from T2ATTOX.
The complex model database suggests that toxics fractions are not the same across tech
groups. However, no further correction will be made because the mix of test fuels differs
across tech groups, thereby limiting the usefulness of the complex model database in
correcting for tech group differences on baseline fuels. Furthermore, these differences are
smaller than they first appear due to averaging.
3. The complex model's percent change values for fuel changes are correct.
VOC
493
404
408
771
317
354
689
457
BZ
27.298
22.388
22.585
42.715
17.577
19.639
38.198
25.334
Form
5.913
4.849
4.892
9.252
3/807
4.254
8.274
5.488
Acet
2.424
1.988
2.006
3.793
1.561
1.744
3.392
2.250
Buta
2.671
2.190
2.210
4.179
1.720
1.921
3.737
2.479
-------
Appendix E
Model-Year-Specific Technology Fractions
-------
Open-Loop Closed-Loop
IV MYA MYB NCAT CAT Garb 3W PFI 3W TBI 3W+OX PF3W+OX TBI
1 65 74 100.00 0.00 0.00 0.00 0.00 0.00 0.00 100
1 75 75 20.00 80.00 0.00 0.00 0.00 0.00 0.00 100
1 76 77 15.00 85.00 0.00 0.00 0.00 0.00 0.00 100
1 78 79 10.00 90.00 0.00 0.00 0.00 0.00 0.00 100
1 80 80 5.00 95.00 0.00 0.00 0.00 0.00 0.00 100
1 81 81 0.00 28.10 62.90 6.00 0.00 0.10 2.90 100
1 82 82 0.00 32.50 50.60 6.20 6.70 0.00 4.00 100
1 83 83 0.00 24.40 48.60 8.50 11.50 0.20 6.80 100
1 84 84 0.00 5.80 55.00 10.50 15.90 0.50 12.30 100
1 85 85 0.00 7.60 40.80 29.20 5.80 1.60 15.00 100
1 86 86 0.00 2.40 31.90 32.90 13.30 6.40 13.10 100
1 87 87 0.00 1.70 24.90 34.70 21.70 2.40 14.60 100
1 88 88 0.00 0.00 10.10 44.40 32.70 4.80 8.00 100
1 89 89 0.00 0.30 12.50 54.60 23.90 5.10 3.60 100
1 90 90 0.00 0.10 1.80 71.80 19.40 4.30 2.60 100
1 91 91 0.00 0.00 0.30 77.50 18.90 2.10 1.20 100
1 92 92 0.00 0.29 0.00 86.47 9.56 3.68 0.00 100
1 93 93 0.00 0.00 0.00 89.06 10.94 0.00 0.00 100
1 94 94 0.00 0.00 0.00 96.12 3.88 0.00 0.00 100
1 95 95 0.00 0.00 0.00 98.80 1.20 0.00 0.00 100
1 96 99 0.00 0.00 0.00 100.00 0.00 0.00 0.00 100
1 00 00 0.00 0.00 0.00 100.00 0.00 0.00 0.00 100
1 01 03 0.00 0.00 0.00 100.00 0.00 0.00 0.00 100
1 04 50 0.00 0.00 0.00 100.00 0.00 0.00 0.00 100
2 65 74 100.00 0.00 0.00 0.00 0.00 0.00 0.00 100
2 75 75 30.00 70.00 0.00 0.00 0.00 0.00 0.00 100
2 76 76 20.00 80.00 0.00 0.00 0.00 0.00 0.00 100
2 77 78 25.00 75.00 0.00 0.00 0.00 0.00 0.00 100
2 79 80 20.00 80.00 0.00 0.00 0.00 0.00 0.00 100
2 81 81 3.00 95.20 1.80 0.00 0.00 0.00 0.00 100
2 82 82 0.00 96.10 3.90 0.00 0.00 0.00 0.00 100
2 83 83 2.60 84.10 13.10 0.20 0.00 0.00 0.00 100
2 84 84 0.00 72.80 25.00 2.20 0.00 0.00 0.00 100
2 85 85 0.00 62.90 25.80 6.60 4.70 0.00 0.00 100
2 86 86 0.00 49.50 13.10 23.80 9.10 0.00 4.50 100
2 87 87 0.00 26.40 12.80 20.40 22.30 12.30 5.80 100
2 88 88 0.00 5.00 9.20 28.00 37.00 13.60 7.20 100
2 89 89 0.00 1.40 7.70 33.10 30.70 20.90 6.20 100
2 90 90 0.10 1.20 2.00 41.20 32.50 18.70 4.30 100
2 91 91 0.00 0.10 1.50 43.50 36.20 14.20 4.50 100
2 92 92 0.48 0.87 0.76 54.15 31.82 11.86 0.06 100
2 93 93 0.00 0.00 1.10 58.00 30.08 10.82 0.00 100
2 94 94 0.00 0.00 0.00 62.13 27.21 10.66 0.00 100
2 95 95 0.00 0.00 0.00 63.92 25.36 10.72 0.00 100
2 96 96 0.00 0.00 0.00 63.00 25.00 12.00 0.00 100
2 97 97 0.00 0.00 0.00 69.08 20.00 10.92 0.00 100
2 98 98 0.00 0.00 0.00 75.16 15.00 9.84 0.00 100
2 99 99 0.00 0.00 0.00 81.24 10.00 8.76 0.00 100
2 00 00 0.00 0.00 0.00 87.32 5.00 7.68 0.00 100
2 01 03 0.00 0.00 0.00 93.40 0.00 6.60 0.00 100
2 04 50 0.00 0.00 0.00 93.40 0.00 6.60 0.00 100
3 65 78 100.00 0.00 0.00 0.00 0.00 0.00 0.00 100
3 79 80 0.00 100.00 0.00 0.00 0.00 0.00 0.00 100
3 81 81 3.00 95.20 1.80 0.00 0.00 0.00 0.00 100
3 82 82 0.00 96.10 3.90 0.00 0.00 0.00 0.00 100
3 83 83 2.60 84.10 13.10 0.20 0.00 0.00 0.00 100
3 84 84 0.00 72.80 25.00 2.20 0.00 0.00 0.00 100
3 85 85 0.00 62.90 25.80 6.60 4.70 0.00 0.00 100
-------
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
5
6
7
8
86
87
88
89
90
91
92
93
94
95
96
97
98
99
00
01
04
68
82
87
88
90
96
00
01
05
65
65
65
65
86
87
88
89
90
91
92
93
94
95
96
97
98
99
00
03
50
81
86
87
89
95
99
00
04
20
50
50
50
20
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
100
95
70
60
7
5
2
2
0
0
0
0
100
.00
.00
.00
.00
.10
.00
.48
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
49
26
5
1
1
0
0
0
0
0
0
0
0
0
0
0
0
0
5
30
40
93
95
98
98
100
0
0
0
0
.50
.40
.00
.40
.20
.10
.87
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
13
12
9
7
2
1
0
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.10
.80
.20
.70
.00
.50
.76
.10
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
23
20
28
33
41
43
54
58
62
63
63
69
75
81
87
93
93
0
0
0
0
0
0
0
0
0
0
0
0
0
.80
.40
.00
.10
.20
.50
.15
.00
.13
.92
.00
.08
.16
.24
.32
.40
.40
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
9
22
37
30
32
36
31
30
27
25
25
20
15
10
5
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.10
.30
.00
.70
.50
.20
.82
.08
.21
.36
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
0.
12.
13.
20.
18.
14.
11.
10.
10.
10.
12.
10.
9.
8.
7 .
6.
6.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.00
.30
.60
.90
.70
.20
.86
.82
.66
.72
.00
.92
.84
.76
.68
.60
.60
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
4.
5.
7 .
6.
4.
4 .
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.50
.80
.20
.20
.30
.50
.06
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
0.00
0.00
0.00
100
-------
Appendix F
Evaluation of CARB UC-FTP Database
-------
The Off-Cycle Toxics Adjustment Factor Analysis
Background: Work Assignment 0-07 involves the estimation of on-road motor vehicle air toxic
emissions, exposure, and cancer risk. The basic on-road emissions analysis requires an
assessment of both on- and off-cycle emissions performance. As a key component of their Tier
2 emission standards study, the U.S. Environmental Protection Agency (EPA) has previously
developed an approach for estimating off-cycle impacts on the criteria pollutants HC, CO, and
NOX.J Since that approach is carried over to the HC (as TOG) and CO components of Work
Assignment 0-07, a similar approach to the consideration of off-cycle impacts on toxic emissions
(which were not considered in the previous Tier 2 study) is required.
The EPA approach essentially involves the assumption that emissions measured over the Unified
Cycle (UC) accurately reflect the aggressive driving aspects of actual on-road performance and,
therefore, the relationship of UC measured emissions to Federal Test Procedure (FTP) measured
emissions provides the necessary adjustment factors to account for off-cycle (aggressive driving)
emission impacts. This appendix details the approach undertaken to derive the UC/FTP
relationship for five toxic species: benzene, 1,3-butadiene, MTBE, formaldehyde, and
acetaldehyde. The ultimate form of the derived relationships is expressed as, as described in
Section 4 of the main report, the ratio of the UC toxics fraction of TOG to the FTP toxics
fraction of TOG.
The EPA approach also involves the application of an additional set of adjustment factors to
account for on-road air conditioning usage not reflected in either the standard FTP or UC.
However, for HC (as TOG), the air conditioning adjustments are minor relative to the UC
off-cycle aggressive driving adjustments. Whereas the aggressive driving TOG adjustments can
be as high as 30 percent for some vehicle model years, air conditioning corrections are confined
to a range of -2 percent to +4 percent. In the absence of specific speciated test data on which to
base toxic air conditioning adjustment factors and because air conditioning represents a relatively
constant load (when activated), it was assumed that on-cycle (i.e., FTP) toxic fractions are
accurate over both on- and off-cycle air conditioning operation. Given the order-of-magnitude
difference in aggressive driving and air conditioning impacts on TOG emission rates, any error
associated with this assumption will be small.
Aggressive Driving Approach: A small database of toxic emissions measurements collected
over the REP05, US06, and FTP cycles was provided by EPA staff for use in determining
off-cycle aggressive driving toxics adjustment factors. Unfortunately, a basic review of the
database revealed several areas of concern limiting its utility. Table A-l provides an overview of
the database and illustrates most of the limiting factors. First, all vehicles with reported
1 "Tier 2 Study", Draft Report, EPA420-P-98-009, U.S. Environmental Protection Agency, April 23, 1998.
-1-
-------
Table A-l
Description of REP05/US06
Database
Vehicles Tested
Model Year
1995
1993
1993
1993
1994
1995
1995
1989
1989
1989
1989
not reported
not reported
not reported
Model
Caravan
Taurus
Spirit
Lumina
Dodge B250
Intrepid
Taurus
Camry
Grand Am
Taurus
Sundance
Chevrolet C-20 Pickup
Crown Victoria
Dodge B150 Ram Wagon
Type
Gasoline LDT
M-FFV
M-FFV
E-FFV
Gasoline LDT
Gasoline LDV
Gasoline LDV
Gasoline LDV
Gasoline LDV
Gasoline LDV
Gasoline LDV
CNG
CNG
CNG
Test Fuel(s)
2% MTBE
2% MTBE
2% MTBE
2% MTBE
not reported
not reported
not reported
Non-Oxy and 2% MTBE
Non-Oxy and 2% MTBE
Non-Oxy and 2% MTBE
Non-Oxy and 2% MTBE
CNG
CNG
CNG
Speciated Emissions Test Data Points
Species
Formaldehyde
Acetaldehyde
1,3 -Butadiene
Benzene
MTBE
TOG
REP05/FTP
18
18
17
18
7
4
US06/FTP
3
3
0
0
0
3
REP05/US06 Comments
0 a
0 a
0 a
0 a
0 b
0
Comments: a. REP05/FTP data points comprise 11 vehicles in total, 7 of which were tested on multiple fuels. 3
of 11 REP05/FTP vehicles and 6 of 18 data points are associated with CNG vehicle testing.
b. 3 of 7 REP05/FTP vehicles and data points are associated with CNG vehicle testing.
-2-
-------
model years fall within the very narrow range of 1989-1995. Second, three of the eleven vehicles
tested are CNG powered and, therefore, not reflective of typical on-road fleet impacts. Third,
there is no mechanism inherent in the database to adjust for differences in the REP05 and US06
cycles (i.e., no vehicles were tested over both cycles). Fourth, only a fraction of the data includes
simultaneous toxics species and TOG measurements. Finally, neither the REP05 or US06 test
cycles are reflective of emissions performance over the UC used for TOG off-cycle adjustment
factor development. Both REP05 and US06 incorporate much higher fractions of off-cycle
driving than the UC (and, theoretically, on-road operation which the UC was designed to reflect).
Therefore, while off-cycle to on-cycle toxics ratios can be developed from the data, a secondary
method of determining the fraction of on-road operation accumulated in each mode would be
required (as well as a method to equilibrate the two varying test cycles (i.e., the REP05 and the
US06) in the EPA database.
Based on the deficiencies noted, supplemental sources of off-cycle toxics data were investigated
and it was determined that the California Air Resources Board (CARB) had performed a
substantial number of speciated emissions tests over both the UC and FTP cycles. Since such
data alleviates several (but not all, as discussed below) of the deficiencies of the REP05/US06
database, the CARB UC/FTP database was obtained and utilized as the basis for the off-cycle
(aggressive driving) adjustment factors used in the performance of this work assignment.
The CARB FTP/UC Database: CARB provided results from 36 speciated emissions tests, 18
of which were performed over the FTP cycle and 18 of which were performed over the UC. A
total of 13 different test vehicles are represented. In all but one case, each of the 18 FTP tests can
be matched with a corresponding UC test, where both tests are conducted on the same vehicle,
using the same fuel, with only moderate mileage accumulation (in many cases, only the mileage
associated with the first test cycle) between tests. However, for a single test pair, the fuel
reported for the FTP test does not match the fuel reported for the UC test. Given the influence
test fuel can play on measured emissions, this single mismatched test pair was excluded from all
analysis under this work assignment. Table A-2 presents an overview of the CARB test data.
As indicated in Table A-2, of the 12 "matching fuel" vehicles in the database, 9 were tested once
over both the FTP and the UC while operating on one of two fuels, either commercial unleaded
gasoline (2 vehicles) or California Phase 2 Reformulated Gasoline (7 vehicles). Two of the
remaining three matching fuel vehicles were tested twice over the FTP and twice over the UC,
once while operating on indolene and once while operating on commercial unleaded gasoline.
One matching fuel vehicle was tested four times over the FTP and four times over the UC, once
each on California Phase 2 Reformulated Gasoline and indolene and twice on commercial
unleaded gasoline. The "mismatched fuel" vehicle (see arbitrarily labeled tests ISA and 18B in
Table A-2), which was excluded from all toxics adjustment factor analysis, was reported to have
been tested on commercial unleaded gasoline over the FTP and California Phase 2 Reformulated
Gasoline over the UC. Unfortunately CARB was unable to provide fuel specification data for
any of the test fuels so the specific variation in fuel properties is not available. However, test
dates indicate that some of the commercial unleaded gasoline testing was performed prior to the
requirement that all California gasoline meet Phase 2 Reformulated Gasoline specifications.
-3-
-------
Table A-2
Synopsis of the CARS FTP/UC Database
Test
lumber
1A
IB
2A
2B
3A
3B
4A
4B
5A
5B
6A
6B
7A
7B
8A
8B
9A
9B
10A
10B
11A
11B
12A
12B
13A
13B
14A
14B
ISA
15B
16A
16B
17A
17B
18A
18B
Model
Year
1996
1995
1994
1993
1993
1993
1993
1992
1989
1989
1989
1987
1984
1984
1983
1982
1982
1991
Vehicle
Make
FORD
TOTA
GM
FORD
FORD
FORD
FORD
CHRY
FORD
FORD
TOTA
MAZD
FORD
MITS
CHRY
GM
GM
FORD
Vehicle
Model
TAURUS GL
COROLLA DX
SUNBIRD LE4DR
TAURUS GL
TAURUS GL
TAURUS GL
TAURUS GL
WRANGLER 2DR
TRACER
TRACER
CAMRY
626LXi 2DR
P/U F-250
COLT
VAN RAM150
CORVETTE
CORVETTE
TAURUS
Engine
Family
STY1.8VJG1GA
R1G2.0V7GFEA
PFM3.8V5FAC8
PFM3.8V5FAC8
PFM3.8V5FAC8
PFM3.8V5FAC8
NCR242T5FEFX
KFM1.6V5FC9
KFM1.6V5FC9
KTY2.0V5FCC1
HTK2.0V5FAK3
EFM4.9T1HGG5
EMT1.6V2FCA5
DCR3.7T1AHS4
C1G5.7V5NBM2
C1G5.7V5NBM2
MFM3.0V5FX03
Odometer
Reading
43077
43088
12302
12313
53752
53774
7429
7964
7834
7798
8010
7850
7890
7901
65196
65255
104715
104497
104661
104613
129092
129115
223589
223628
36660
36671
122337
122337
114222
114247
131965
131974
132030
131910
69189
69134
Test
Type
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
Test
Fuel
RFG
UnL
RFG
Ind
UnL
UnL
RFG
RFG
Ind
UnL
UnL
RFG
RFG
RFG
RFG
Ind
UnL
UnL
RFG
High
Emitter?
No
No
No
No
No
No
No
No
No
No
No
Yes
No
Yes
Yes
Yes
Yes
Mn
THC
(g/mi)
0.1257
0.1309
0.1606
0.1301
0.1924
0.1344
0.0501
0.1164
0.1223
0.1239
0.0913
0.1181
0.0886
0.1005
0.2833
0.3644
0.1847
0.1844
0.2324
0.2730
0.2274
0.3742
1.7677
1.7501
0.3766
0.4903
1.4099
1.6163
2.2895
2.3424
1.7809
1.5220
1.4140
1.4043
0.4205
03703
TOG
(g/mi)
0.1311
0.1377
0.1662
0.1345
0.2045
0.1429
0.0536
0.1244
0.1272
0.1260
0.0923
0.1209
0.0920
0.1117
0.2941
0.3763
0.1888
0.1872
0.2531
0.2870
0.2318
0.3835
1.8764
1.8629
0.3841
0.4985
1.5309
1.7264
2.3704
2.4041
1.8317
1.5728
1.4803
1.4656
0.4328
03828
Benzene
(mg/mi)
3.8733
3.4630
4.6247
4.8528
4.6924
4.1695
1.7666
5.8468
6.2116
9.7737
3.9428
9.3815
3.1039
5.4411
8.2053
9.0569
6.0074
6.9607
6.3636
9.1525
7.9994
21.8217
72.7795
76.8858
12.1466
24.0186
35.7490
42.4803
59.8553
82.2424
69.9380
67.7398
58.0894
59.3127
13.2492
107827
1,3-Butad
(mg/mi)
0.4719
0.2598
0.8189
1.0670
0.9455
0.6358
0.1902
0.3080
0.7034
0.4274
0.4036
0.7331
0.4695
0.2481
1.3462
1.1907
0.8885
0.9538
0.6818
0.9992
1.2267
2.8594
17.5925
15.4418
0.7973
1.0149
14.6033
8.0979
4.4287
3.1607
5.3410
3.9056
6.0390
4.7875
1.4970
0 8301
MTBE
(mg/mi)
4.0072
3.4306
3.6832
2.3777
6.5115
3.6821
0.1345
0.0000
3.1396
2.6549
3.1161
2.1953
2.7508
2.9428
10.8351
17.9644
0.0000
0.0000
4.7496
2.4148
0.0000
0.0000
24.4603
16.0411
11.5648
9.2366
70.4496
80.0602
21.4863
12.3718
0.0000
1.2878
13.5599
20.4828
8.5297
80156
Formald
(mg/mi)
1.5937
3.9426
2.6499
1.8564
4.4394
4.0374
2.6240
6.3267
2.9638
0.4605
0.6365
0.9556
2.0666
9.6098
4.0166
4.4172
2.4745
0.8445
10.9043
10.4562
2.0930
2.8130
42.0528
43.7857
3.6149
3.6696
51.3210
43.8942
25.0328
25.0180
21.8404
24.6744
23.5275
12.9383
3.4716
34596
Acetald
(mg/mi)
0.5032
0.4645
0.5278
0.4098
1.0985
0.6821
0.2053
0.5020
0.4069
0.4898
0.1414
0.5244
0.3862
0.4014
1.2080
1.0991
0.4316
0.5624
0.7099
0.9512
0.7367
1.7792
11.3426
12.1923
0.9507
1.1920
11.6262
10.2241
7.7771
7.6806
8.8994
6.5080
7.8022
7.2346
1.2526
1 1353
Fuel type "RFG" indicates California Phase 2 Reformulated Gasoline, "Ind" indicates indolene, and "UnL" indicates commercial unleaded gasoline.
-4-
-------
"1,3-Butad" indicates 1,3-tmtadiene, "Formald" indicates formaldehyde, and "Acetald" indicates "acetaldehyde.'
-5-
-------
As mentioned above, most of the corresponding FTP and UC tests were performed with only
moderate mileage accumulation between tests. Of the 10 vehicles tested once (including the
mismatched fuel vehicle), the maximum reported mileage between FTP and UC test initiation is
believed to be 59 miles (the uncertainty derives from the fact that identical FTP and UC start
mileages are reported for one test vehicle). In all single test matched fuel cases, the FTP was
performed first. For vehicles tested multiple times on different fuels, greater mileage
accumulation is evident between tests on differing fuels to ensure that any emissions effects
associated with the preceding test fuel do not affect the following test performance.
Additionally, multiple fuel testing was not always performed sequentially (i.e., same-fuel FTP
and UC tests were not always performed consecutively), so that accumulations of one to two
hundred miles are observed between several corresponding multi-fuel tests, with a single test pair
separated by a maximum of 535 miles (due to the performance of 5 tests on other fuels between
the matching test pair).
The CARB database was subjected to a basic integrity check prior to off-cycle adjustment factor
analysis. This check detected two potential problem areas. First, test pair 4A/4B (see Table A-2)
was determined to be invalid. As evidenced by the emission measurements presented in Table
A-2, the FTP/UC relationship for this test pair is an outlier. Further review of the CARB test
data indicates that the CO2 emission rate over the FTP (test 4A) is reported to be only 168 grams
per mile, while that over the UC (test 4B) is a much more reasonable 439 grams per mile.
Clearly there is a quality problem with this test pair that appears to be traceable to a test 4A
dilution factor calculation error (given the apparent under-reporting of all test species). Since
sufficient information to confirm or correct such an error is not included in the data provided by
CARB, the test 4A/4B pair was dropped from the analysis database. The UC CO2/FTP CO2
relationship for all other test pairs varies from -2 percent to +13 percent (with both matching fuel
test pairs indicating a negative relationship being high emitters), so that no other obvious data
quality problems are apparent.
The second data integrity problem area was an apparent discrepancy in the treatment of THC,
CH4, and NMHC emission rates on all tests. Essentially, CARB appears to correct THC
measurements for FID CH4 "over-response," but does not apply this same correction to CH4
itself. Since NMHC is then determined as THC minus CH4, the reported CH4 emission rate
appears to be somewhat high (on the order of 5 percent or so depending on FID CH4 response)
and the reported NMHC emission rate appears to be correspondingly low. However, unlike the
previous under-measurement problem with test 4A, this problem is easily resolved. Since TOG
emissions are the basis for all off-cycle toxics fractions, only the THC (plus alcohol and
carbonyl) measurement need be precise. Moreover, all information necessary to correct both the
reported CH4 and NMHC measurements is available in the data provided by CARB. Therefore,
this potential problem area does not ultimately affect the off-cycle toxics analysis (but care was
taken to ensure that all data used in the analysis was consistent).
Determination of Off-Cycle Toxic Adjustment Factors: As described above (and as shown in
Table A-2), a total of 16 matched fuel UC/FTP speciated test pairs were available to support a
determination of the required off-cycle toxics adjustment factors (test pairs 4A/4B and 18A/18B
were excluded due to data integrity and fuel mismatch problems respectively). Ideally, off-cycle
-------
adjustment factor analysis would be conducted on a vehicle technology, vehicle class, and fuel
specific basis to ensure that all vehicle- and fuel-specific influences were properly accounted for
in the calculated adjustment factors. However, the size of the available database precludes such
disaggregated treatment. Nevertheless, several precautions were taken to minimize any
unaccounted for vehicle- and fuel-specific influences. First, all off-cycle adjustments are
calculated in normalized form as the ratio of the UC toxic fraction to the FTP toxics fraction.
Therefore, both vehicle- and fuel-specific influences will be controlled to the extent that such
influences are consistent across the FTP and UC. Second, in determining MTBE ratios, all zero
content MTBE fuels were excluded from analysis since exhaust MTBE emissions for such fuels
will be at or near zero. Third, the CARB test data was collapsed so that each test vehicle is
represented in the off-cycle adjustment database only once. Test results for vehicles that were
tested multiple times were consolidated into a single UC/FTP test pair by arithmetically
averaging individual test results. Finally, several statistical checks were applied to ensure no
obvious problems with the aggregated treatment of the CARB data. Table A-3 presents the
off-cycle toxics database after the application of the described quality control steps.
Following exclusion of suspect quality data, aggregation of multiple test vehicle results, and
elimination of the zero MTBE content fuel results for MTBE adjustment factor analysis, the
analysis database consists of:
8 normal emitter test pairs for benzene, 1,3-butadiene, formaldehyde, and acetaldehyde
analysis,
7 normal emitter test pairs for MTBE analysis, and
4 high emitter test pairs for benzene, 1,3-butadiene, MTBE, formaldehyde, and acetaldehyde
analysis.
Due to the small sample sizes available for adjustment factor development, an aggregated
approach based on the development of single adjustment factors for normal and high emitters
was employed. Such an approach allows for the development of model year specific adjustment
factors through the appropriate weighting of the normal and high emitter adjustments (as
described in Section 4), but explicitly discounts any inherent influences of vehicle technology,
class, or fuel. Given the limitations imposed by database size, it is difficult to be certain that
such overlooked influences are not significant, but basic analyses possible with the given data
imply that they are no more significant than seemingly random variations in the dataset. To some
extent, this is expected given the normalization approach employed in this analysis. While
technology and fuel may influence emissions, much of that influence should be consistent across
both the FTP and UC cycles and, therefore, "factored out" during the normalization process.
This does not imply any loss in fuel or technology significance in the overall toxics exposure
analysis, since the basic differences due to fuels and technology will be reflected in the basic
emission rates to which the off-cycle adjustments are applied.
-7-
-------
Table A-3
FTP/UC Database used for Off-Cycle Adjustment Analysis
Test
Mumber
1A
IB
2A
2B
3A
3B
5-7A
5-7B
8A
8B
9-10A
9-1 OB
10A
10B
11A
11B
13A
13B
12A
12B
14A
14B
ISA
15B
16-17A
16-17B
17A
17B
Model
Year
1996
1995
1994
1993
1992
1989
1989
1989
1984
1987
1984
1983
1982
1982
Vehicle
Make
FORD
TOTA
GM
FORD
CHRY
FORD
FORD
TOTA
FORD
MAZD
MITS
CHRY
GM
GM
Vehicle
Model
TAURUS GL
COROLLA DX
SUNBIRD LE4DR
TAURUS GL
WRANGLER 2DR
TRACER
TRACER
CAMRY
P/U F-250
626LXi 2DR
COLT
VANRAM150
CORVETTE
CORVETTE
Engine
Family
TFM3.0V8GKEK
STY1.8VJG1GA
R1G2.0V7GFEA
PFM3.8V5FAC8
NCR242T5FEFX
KFM1.6V5FC9
KFM1.6V5FC9
KTY2.0V5FCC1
EFM4.9T1HGG5
HTK2.0V5FAK3
EMT1.6V2FCA5
DCR3.7T1AHS4
C1G5.7V5NBM2
C1G5.7V5NBM2
Odometer
Reading
43077
43088
12302
12313
53752
53774
7911
7850
65196
65255
104688
104555
104661
104613
129092
129115
36660
36671
223589
223628
122337
122337
114222
114247
131998
131942
132030
131910
Test
Type
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
FTP
UC
Test
Fuel
RFG
UnL
RFG
UnL/RFG
RFG
Ind/UnL
UnL
UnL
RFG
RFG
RFG
RFG
Ind/UnL
UnL
High
Emitter?
No
No
No
No
No
No
No
No
No
Yes
Yes
Yes
Yes
Yes
THC
(g/mi)
0.1257
0.1309
0.1606
0.1301
0.1924
0.1344
0.1007
0.1142
0.2833
0.3644
0.2085
0.2287
0.2324
0.2730
0.2274
0.3742
0.3766
0.4903
1.7677
1.7501
1.4099
1.6163
2.2895
2.3424
1.5974
1.4631
1.4140
1 .4043
TOG
(g/mi)
0.1311
0.1377
0.1662
0.1345
0.2045
0.1429
0.1038
0.1196
0.2941
0.3763
0.2210
0.2371
0.2531
0.2870
0.2318
0.3835
0.3841
0.4985
1.8764
1.8629
1.5309
1.7264
2.3704
2.4041
1.6560
1.5192
1.4803
1 .4656
Benzene
(mg/mi)
3.8733
3.4630
4.6247
4.8528
4.6924
4.1695
4.4194
8.1988
8.2053
9.0569
6.1855
8.0566
7.9994
21.8217
12.1466
24.0186
72.7795
76.8858
35.7490
42.4803
59.8553
82.2424
64.0137
63.5262
1,3-Butad
(mg/mi)
0.4719
0.2598
0.8189
1.0670
0.9455
0.6358
0.5255
0.4695
1.3462
1.1907
0.7851
0.9765
1.2267
2.8594
0.7973
1.0149
17.5925
15.4418
14.6033
8.0979
4.4287
3.1607
5.6900
4.3466
MTBE
(mg/mi)
4.0072
3.4306
3.6832
2.3777
6.5115
3.6821
3.0021
2.5976
10.8351
17.9644
4.7496
2.4148
11.5648
9.2366
24.4603
16.0411
70.4496
80.0602
21.4863
12.3718
13.5599
20.4828
Form aid
(mg/mi)
1.5937
3.9426
2.6499
1.8564
4.4394
4.0374
1.8889
3.6753
4.0166
4.4172
6.6684
5.6504
2.0930
2.8130
3.6149
3.6696
42.0528
43.7857
51.3210
43.8942
25.0328
25.0180
22.6840
18.8063
Acetald
(mg/mi)
0.5032
0.4645
0.5278
0.4098
1.0985
0.6821
0.3115
0.4719
1.2080
1.0991
0.5708
0.7568
0.7367
1.7792
0.9507
1.1920
11.3426
12.1923
11.6262
10.2241
7.7771
7.6806
8.3508
6.8713
Fuel type "RFG" indicates California Phase 2 Reformulated Gasoline, "Ind" indicates indolene, and "UnL" indicates commercial unleaded gasoline.
"1,3-Butad" indicates 1,3-butadiene, "Formald" indicates formaldehyde, and "Acetald" indicates "acetaldehyde."
Test pairs 9-10A/9-10B, 11A/1 IB, and 16-17A/16-17B are excluded from MTBE adjustment factor development due to zero MTBE content fuel use.
Test pairs 10A/10B and 17A/17B are used only for MTBE adjustment factor development (both pairs exclude zero MTBE content fuel test results).
For multiple test pairs, the tabulated odometer readings are the arithmetic average of component test readings.
-------
Some degree of assessment of the potential significance of fuel effects can be attained by
examining the CARB data for the three vehicles that were tested multiple times on different
fuels. CARB tested a 1993 Ford Taurus once on indolene, once on California Phase 2
Reformulated Gasoline, and twice on commercial unleaded gasoline. Comparing the variation in
the ratio of the UC toxics fraction (of TOG) to the FTP toxics fraction (of TOG) when tested on
the two commercial unleaded gasolines to the overall variation indicates that the unleaded
variation comprises 58 percent of the overall variation for benzene, 81 percent of the overall
variation for 1,3-butadiene, 92 percent of the overall variation for MTBE, 27 percent of the
overall variation for formaldehyde, and 82 percent of the overall variation for acetaldehyde.
With the exception of formaldehyde, almost as much variability is observed between results for
the two commercial unleaded fuels as is observed over the entire four tests. While formaldehyde
appears to be an exception, nearly all the difference can be tied to a single UC test result that is
not supported by a similar difference in FTP results. Therefore, the source of the variation does
not appear to be fuel related.
CARB also tested two other vehicles on two fuels each. A 1989 Ford Tracer tested on both
indolene and commercial unleaded gasoline indicated total toxics fraction ratio variability across
the two fuels of only 9 percent for benzene, 19 percent for 1,3-butadiene, and 10 percent for
acetaldehyde. Once again, formaldehyde indicates significant variability, with a 146 percent
difference. Data for MTBE is only available for one fuel. A 1982 Chevrolet Corvette also tested
on both indolene and commercial unleaded gasoline indicates similar variabilities across fuels of
only 9 percent for benzene, 6 percent for 1,3-butadiene, and 10 percent for acetaldehyde.
Formaldehyde variability is again significant, but interestingly the variability is opposite in sign
to that for the Tracer and of virtually identical magnitude (-58 percent versus +146 percent
difference). As a result, it is not possible to identify any definitive fuel-specific influences within
the small sample available for analysis. Additional inferences may have been possible had
specific fuel specifications been available, but CARB did not respond to a request for such data.
Nevertheless, it does appear that fuel effects are not the predominant influence for a
normalization-based approach such as that employed in this analysis and the uncertainty
associated with treating all fuels in the aggregate is expected to be only a small component of
overall analysis uncertainty.
To assess the potential impacts of vehicle technology, a basic regression of the ratio of UC toxics
fraction (of TOG) to FTP toxics fraction (of TOG) by vehicle model year was conducted. The
results of this regression analysis are presented in the upper half of Table A-4. Notwithstanding
the very small sample sizes, not a single model year coefficient or intercept is significant at over
90 percent confidence. A case for a formaldehyde relationship can be made over the entire 8
normal emitter vehicle dataset as both coefficient and intercept are significant at 90 percent
confidence, but further examination indicates that this relationship is controlled by a single data
point for a 1996 Ford Taurus. When excluded, the confidence level of both the coefficient and
the intercept decline to just over 75 percent and "random" effects appear to dominate the model
year relationship. Based on this, albeit simplistic, analysis, it does not appear that vehicle
technology influences are a predominant factor, at least in the database available for this analysis.
One additional observation is, however, critical. The database available for analysis does not
include any pre-1981 model year vehicles. Therefore, potential
-9-
-------
Table A-4
Database Regression Analysis Results
Emitter
Category
Toxics
Species
Number
of
Data Points
r2
F
a
Confidence
Level
of a
b
Confidence
Level
ofb
Zero
Intercept
Slope
AvgUC
Fraction to
AvgFTP
Fraction
Slope/Avg
Delta
UC/FTP Toxic Fraction Ratio = a (Vehicle Model Year) + b
Normal
Emitters
High
Emitters
Benzene
1,3 -Butadiene
MTBE
Formaldehyde
Acetaldehyde
Benzene
1,3 -Butadiene
MTBE
Formaldehyde
Acetaldehyde
8
8
7
8
8
4
4
4
4
4
0.239
0.034
0.153
0.393
0.090
0.121
0.062
0.352
0.189
0.338
1.887
0.211
0.901
3.882
0.590
0.275
0.133
1.086
0.467
1.020
-0.038
-0.017
0.024
0.091
-0.019
-0.023
0.020
-0.134
0.025
0.034
78%
34%
61%
90%
53%
35%
25%
59%
44%
58%
77.181
34.870
-47.043
-179.436
39.523
47.337
-39.418
267.275
-49.168
-67.168
79%
35%
61%
90%
54%
36%
25%
59%
43%
58%
UC Toxics Fraction = a (FTP Toxics Fraction) + b
Normal
Emitters
High
Emitters
Benzene
1,3 -Butadiene
MTBE
Formaldehyde
Acetaldehyde
Benzene
1,3 -Butadiene
MTBE
Formaldehyde
Acetaldehyde
8
8
7
8
8
4
4
4
4
4
0.782
0.483
0.758
0.336
0.280
0.835
0.741
0.943
0.879
0.743
21.558
5.599
15.628
3.032
2.335
10.109
5.727
33.381
14.547
5.788
2.425
1.458
1.893
0.811
0.470
0.878
0.649
1.018
0.695
0.713
100%
94%
99%
87%
82%
91%
86%
97%
94%
86%
-0.034
-0.002
-0.031
0.006
0.002
0.008
0.000
-0.001
0.004
0.001
92%
47%
92%
49%
87%
53%
13%
16%
58%
43%
1.350
1.060
0.856
1.113
0.986
1.113
0.694
0.986
0.861
0.904
1.315
1.037
0.825
1.163
1.020
1.126
0.708
0.965
0.894
0.919
-3%
-2%
-4%
5%
3%
1%
2%
-2%
4%
2%
-10-
-------
influences associated with major catalyst technology differences cannot be ascertained. Too
some extent, this problem is alleviated through the predominance of 1981 and later vehicles in
the future year fleets addressed in the overall toxics exposure analysis. Nevertheless, a
significant fraction of such vehicles are present in the 1990 analysis fleet. Therefore, given the
complete absence of data for such vehicles, off-cycle adjustment factors have been set to unity
for pre-1981 LDV's and pre-1984 LDT's as described in Section 4 of the main report.
Based on the negative assessments of fuel and model year influences, an aggregate treatment of
the CARB test data appears to be justified. As outlined in Section 4 of the main report, the
desired application of the off-cycle adjustment is multiplicative in design. However, before such
application was accepted, a basic regression analysis of the CARB data was performed to ensure
that no absolute offsets were present in the UC/FTP relations. The bottom half of Table A-4
presents the results of a regression analysis of the UC toxics fraction (of TOG) versus the FTP
toxics fraction (of TOG). As indicated, significant intercepts were found in no cases at 95
percent confidence and only two cases at 90 percent confidence. Conversely, significant
coefficients were found at 95 percent or greater confidence in 3 of 10 relations (including both of
those where intercepts were significant at 90 percent confidence) and at 90 percent or greater
confidence in 6 of 10 relations. All four remaining relations showed significant coefficients only
between 80 and 90 percent confidence, but in all cases but one coefficient significance exceeded
intercept significance (in most cases by substantial margins). While the calculated relations are
not definitive in their confirmation of the superiority of a multiplicative approach in all cases,
they strongly suggest that such an approach is as or more reliable than an approach which
includes an emissions offset given available data.
The three rightmost columns of the bottom half of Table A-4 present results for two approaches
to the determination of multiplicative off-cycle adjustment factors. One approach relies on zero
intercept regression coefficients, while the second is simply the ratio of the arithmetic average of
UC toxic fractions to the arithmetic average of FTP fractions. By definition, these two estimates
must be similar and, as shown in Table 4, the observed variation is ±5 percent. Given this
similarity and the fact that the regression statistics are based on very small datasets, the estimates
derived through the arithmetic average approach were used for all subsequent toxics analysis.
Table A-5 presents a final summary of the off-cycle adjustment factors and includes the
minimum and maximum UC/FTP toxic fraction ratios for test data included in the arithmetic
average statistics. With the exception of MTBE, the range of ratios tends to be much smaller for
high emitters and, with the exception of 1,3-butadiene and acetaldehyde, closer to unity.
Clearly there is considerable uncertainty in the derived off-cycle adjustment factor estimates
given the quantity of available data. This uncertainty extends to the issue of whether vehicle
technology and fuel influences are, in fact, significant and just not identifiable given the relative
scatter of data over such a small database. Moreover, normal emitter adjustment factors for both
1,3-butadiene and acetaldehyde are sufficiently close to unity such that the collection of
additional data is required before even directional differences can be known with certainty.
While additional data should be collected to support more finely detailed analysis in the future,
the derived estimates appear reasonable, with the largest implied adjustment on the order of 30
percent.
-11-
-------
Table A-5
Summary of Off-Cycle Toxics Adjustment Factor Analysis
Toxic Species
Benzene
1,3 -Butadiene
MTBE
Formaldehyde
Acetaldehyde
Parameter
Ratio Estimate
Minimum
Maximum
Data Points
Ratio Estimate
Minimum
Maximum
Data Points
Ratio Estimate
Minimum
Maximum
Data Points
Ratio Estimate
Minimum
Maximum
Data Points
Ratio Estimate
Minimum
Maximum
Data Points
Normal Emitters
Regression
Coefficient
1.350
8
1.060
8
0.856
7
1.113
8
0.986
8
Arithmetic
Average
1.315
0.851
1.649
8
1.037
0.524
1.610
8
0.825
0.474
1.296
7
1.163
0.782
2.354
8
1.020
0.711
1.460
8
High Emitters
Regression
Coefficient
1.113
4
0.694
4
0.986
4
0.861
4
0.904
4
Arithmetic
Average
1.126
1.054
1.355
4
0.708
0.492
0.884
4
0.965
0.568
1.647
4
0.894
0.758
1.049
4
0.919
0.780
1.083
4
-12-
-------
Appendix G
Summary of T2ATTOX Code Changes to Implement
Revised Toxics Emissions Estimation Procedures
and Description of Model Function
-------
X6 I Added variables to store values for July Runs
BD38 FOR Added initializations for X6 Common Block
BD41 FOR Initializations for TOX variables
BEF FOR Added calls to TOXADJ and OFFCYC routines
CCEVRT FOR No Change
DAT01 I Contains Common block for TOX changes
DRIVER FOR Modified to automate Output file name
EVPADJ FOR Modified to do multiple Toxics
GETTX2 FOR Reads in Evap and Exhaust Tox factors and Offcycle
factors; Sets up TOX and Offcycle arrays.
HCCALX FOR Modified to handle multiple Toxic calculations
IM90 OFF Offcycle file used in Tox input file
LASTOUT FOR Writes out output header to the screen
NAMEOUT FOR Develops output file name
OFFCYC FOR Offcycle adjustments routine
ONESEC FOR Modified to run with only with NMHFLG=7 (File input]
OUTDT3 FOR Outputs multiple Toxic EFs
OUTDT4 FOR Outputs multiple toxic EFs
OUTTOX FOR Prints out Toxic/Off cycle factors used
PX90SB EVP Evap Toxic factor input file
PX96SB EXH Exhaust Toxic factor input file
SAVER FOR Saves output for Jul run
TOXADJ FOR Applies Toxic Emission corrections
VNAME I Header changes
ADJUST FOR Applies adjustments for JUL runs
-------
Appendix G
MOBTOXSb Usage and Description
MOBTOXSb Input file
MOBTOXSb input file should be similar to the standard MOBILESb input file with the
following exceptions:
1. The NMHFLG should be set to 7. In addition the LTXFLG on the same record should
always be 1. The format for the NMHFLG record should be : II, Ix, II. The input record
should look like:
7 1 NMHFLG=7 for Toxics output.
2. The Toxic-TOG curves, the evaporative toxic fractions and the off-cycle correction factors
are read in from three separate files. The input format of these files are described in
Appendix I for the evaporative fractions, Appendix H for the toxic-TOG curves, and
Appendix A for the off-cycle corrections. The input file needs to reference these files by
using the following three statements:
TX EVP FRACTIONS : EVAPFILE.EVP
TX EXH FRACTIONS : TX-TOGFILE.EXH
OFFCYCLE FACTORS : OFFCYCLEFILE.OFF
The format of these lines need to have the exact format and content as described above on the left
side of the colon. The colon should be in column 18. The file names on the right side of the
colon should name the input files describing the toxic factors.
An example input and an output file are included in Appendices J and K, respectively.
MOBTOXSb input prompts have been modified to ask the user for only the input file name. The
model output is written to a file with the same name with a '.out' suffix.
MOBTOXSb General Description
There are primarily three areas where the model code has been changed, they are input, toxic
factor calculations, and model output.
Model input:
The subroutine gettx2.for has been modified to read in the three files for evaporative, toxic-TOG
corrections and off-cycle factors. These factors are then stored in a common block for use in
other subroutines.
Toxic factor calculations:
The hccalx.for subroutine was modified to estimate emissions for each of the five toxic emission
factors. The subroutine calls the exhaust emission calculation routine, beffor, and evaporative
-------
emission calculation routines, ccevrt.for, rnglos.for, rstlos.for, and rlrate.for to calculate hot-soak
and diurnal emissions, running loss emissions, resting loss emissions and refueling emissions.
The subroutine bef.for calls the subroutine toxadj.for to apply the toxic-TOG curves and
offcyc.for to apply the offcycle corrections. The evaporative corrections are applied by a call to
the evpadj.for subroutine from hccalx.for for each of the evaporative components.
Model output:
Two output subroutines OUTDT3 and OUTDT4 have been modified to include the toxic
emission factors. A sample of the model output is attached. The output file contains all the toxic
factors included in the input. Emission factors for Benzene, Acetaldehyde, Formaldehyde, 1,3
Butadiene, and MTBE are contained in the model output. For Benzene and MTBE evaporative
and exhaust emission factors are included for each vehicle type.
-------
Appendix H
Sample Toxic-TOG "Curves" for
1990 Phoenix Summertime Fuel
-------
IV
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
MYA
1965
1975
1976
1978
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
2000
2001
2004
1965
1975
1976
1977
1979
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
MYB
1974
1975
1977
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1999
2000
2003
2050
1974
1975
1976
1978
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
TOG-N
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.000
.000
.000
.000
.000
.640
.628
.628
.639
.644
.641
.612
.570
.557
.535
.514
.519
.498
.500
.332
.332
.332
.117
.117
.000
.000
.000
.000
.000
.638
.638
.636
.627
.593
.572
.648
.620
.653
.623
.595
TOG-H
10.
10.
10.
10.
10.
4 .
4 .
4.
4.
4 .
4 .
4.
4.
4 .
4 .
4.
4.
4 .
4 .
4.
4.
4 .
4 .
4.
10.
10.
10.
10.
10.
4 .
4 .
4.
4.
4 .
4 .
4.
4.
4 .
4 .
4.
.00
.00
.00
.00
.00
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.00
.00
.00
.00
.00
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
BZ-N
0.
0.
0.
0.
0.
39.
36.
36.
37.
35.
34.
31.
27.
27.
24.
23.
23.
23.
23.
15.
15.
15.
4 .
4.
0.
0.
0.
0.
0.
29.
30.
31.
33.
31.
28.
31.
29.
30.
28.
26.
.00
.00
.00
.00
.00
.58
.99
.52
.86
.83
.12
.65
.37
.36
.71
.61
.91
.01
. 17
.40
.42
.42
.72
.72
.00
.00
.00
.00
.00
.95
.28
.63
.09
.57
.45
.38
.28
.44
.24
.95
BZ-H
464.
464 .
464 .
464.
464.
193.
192.
193.
195.
194 .
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
464.
464 .
464 .
464.
464.
187 .
187 .
188.
189.
190.
191.
193.
195.
195.
195.
195.
.70
.92
.94
.95
.97
.31
.96
.61
.09
.95
.36
.42
.55
.53
.55
.55
.53
.55
.55
.55
.55
.55
.55
.55
.70
.90
.92
.91
.92
.71
.88
.63
.74
.53
.60
.45
.16
.44
.45
.55
AC-N
0.
0.
0.
0.
0.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
1 .
1 .
1.
1.
1 .
0.
0.
0.
0.
0.
0.
0.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
.00
.00
.00
.00
.00
.46
.46
.41
.33
.38
.33
.26
.14
.10
.05
.00
.01
.96
.97
.31
.31
.31
.40
.40
.00
.00
.00
.00
.00
.98
.94
.88
.72
.53
.40
.49
.28
.33
.25
.18
AC-H
59
49
48
47
47
15
16
15
15
15
14
14
14
14
14
14
14
14
14
14
14
14
14
14
59
50
49
49
49
18
18
18
17
17
16
15
15
14
14
14
.34
.08
.43
.79
.15
.98
.15
.84
.12
.19
.98
.96
.89
.90
.89
.89
.90
.89
.89
.89
.89
.89
.89
.89
.34
.36
.08
.72
.08
.85
.61
.38
.71
.33
.81
.91
.08
.95
.95
.89
FR-N
0
0
0
0
0
6
6
6
6
6
6
5
5
5
5
5
5
5
5
3
3
3
1
1
0
0
0
0
0
9
9
9
8
7
7
7
6
6
6
5
.00
.00
.00
.00
.00
.84
.91
.64
.08
.25
.09
.85
.52
.43
.29
.13
.20
.02
.04
.35
.35
.35
.02
.02
.00
.00
.00
.00
.00
.60
.38
.12
.36
.60
.00
.06
.09
.25
.03
.76
FR-H
221
163
160
156
153
41
42
40
35
36
34
34
34
34
34
34
34
34
34
34
34
34
34
34
221
171
163
167
163
60
59
57
53
50
47
41
35
34
34
34
.52
.84
.24
.63
.02
.46
.61
.49
.62
.09
.73
.54
.10
.18
.13
.10
.18
.10
.10
.10
.10
.10
.10
.10
.52
.05
.84
.45
.84
.68
.26
.55
.16
.56
.06
.01
.41
.47
.47
.13
BD-N
0
0
0
0
0
2
2
2
2
2
2
2
2
2
2
2
2
2
2
1
1
1
0
0
0
0
0
0
0
2
2
2
2
2
2
2
2
2
2
2
.00
.00
.00
.00
.00
.54
.51
.49
.48
.53
.53
.41
.27
.24
.17
.09
.13
.03
.05
.36
.36
.36
.42
.42
.00
.00
.00
.00
.00
.86
.76
.80
.64
.47
.37
.65
.49
.64
.53
.40
BD-H
90
53
50
48
45
33
32
33
38
37
38
38
39
39
39
39
39
39
39
39
39
39
39
39
90
57
53
55
53
18
18
20
23
25
28
33
38
38
39
39
.98
.03
.66
.28
.91
.19
.23
.99
.04
.65
.78
.93
.30
.23
.28
.30
.23
.30
.30
.30
.30
.30
.30
.30
.98
.77
.03
.40
.03
.53
.41
.95
.48
.63
.54
.56
.21
.99
.03
.28
MT-N
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
MT-H
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
-------
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
4
4
4
4
4
4
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2004
1965
1979
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2004
1968
1982
1987
1988
1990
1996
1992
1993
1994
1995
1996
1997
1998
1999
2000
2003
2050
1978
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2003
2050
1981
1986
1987
1989
1995
1999
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.562
.556
.554
.368
.373
.370
.367
.364
.361
.126
.126
.000
.000
.638
.638
.636
.627
.593
.572
.648
.620
.653
.623
.595
.562
.556
.554
.555
.563
.370
.367
.364
.361
.357
.357
.000
.000
.000
.000
.000
.000
4.
4.
4 .
4 .
4.
4.
4 .
4 .
4.
4.
4 .
10.
10.
4.
4 .
4 .
4.
4.
4 .
4 .
4.
4.
4 .
4 .
4.
4.
4 .
4 .
4.
4.
4 .
4 .
4.
4.
4 .
10.
10.
10.
10.
10.
10.
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.00
.00
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.03
.00
.00
.00
.00
.00
.00
25.
25.
25.
16.
16.
16.
16.
16.
16.
5.
5.
0.
0.
29.
30.
31.
33.
31.
28.
31.
29.
30.
28.
26.
25.
25.
25.
25.
25.
16.
16.
16.
16.
16.
16.
0.
0.
0.
0.
0.
0.
.55
.37
.15
.72
.92
.83
.73
.64
.54
.38
.38
.00
.00
.95
.28
.63
.09
.57
.45
.38
.28
.44
.24
.95
.55
.37
.15
.21
.52
.83
.73
.64
.54
.45
.45
.00
.00
.00
.00
.00
.00
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
464 .
464.
187.
187 .
188.
189.
190.
191.
193.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
195.
464 .
470.
496.
507.
564.
566.
.45
.55
.55
.55
.55
.55
.55
.55
.55
.55
.55
.70
.98
.71
.88
.63
.74
.53
.60
.45
.16
.44
.45
.55
.45
.55
.55
.55
.55
.55
.55
.55
.55
.55
.55
.70
.08
.95
.70
.68
.83
2.
2.
2.
1 .
1.
1.
1 .
1 .
1.
0.
0.
0.
0.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
1.
1 .
1 .
1.
1.
1 .
0.
0.
0.
0.
0.
0.
.10
.08
.08
.38
.39
.39
.38
.38
.37
.45
.45
.00
.00
.98
.94
.88
.72
.53
.40
.49
.28
.33
.25
.18
.10
.08
.08
.08
.10
.39
.38
.38
.37
.37
.37
.00
.00
.00
.00
.00
.00
14
14
14
14
14
14
14
14
14
14
14
59
46
18
18
18
17
17
16
15
15
14
14
14
14
14
14
14
14
14
14
14
14
14
14
66
65
60
58
47
47
.97
.89
.89
.89
.89
.89
.89
.89
.89
.89
.89
.34
.51
.85
.61
.38
.71
.33
.81
.91
.08
.95
.95
.89
.97
.89
.89
.89
.89
.89
.89
.89
.89
.89
.89
.26
.27
.33
.36
.89
.50
5
5
5
3
3
3
3
3
3
1
1
0
0
9
9
9
8
7
7
7
6
6
6
5
5
5
5
5
5
3
3
3
3
3
3
0
0
0
0
0
0
.57
.46
.46
.62
.66
.64
.62
.59
.57
.16
.16
.00
.00
.60
.38
.12
.36
.60
.00
.06
.09
.25
.03
.76
.57
.46
.46
.46
.52
.64
.62
.59
.57
.55
.55
.00
.00
.00
.00
.00
.00
34
34
34
34
34
34
34
34
34
34
34
221
149
60
59
57
53
50
47
41
35
34
34
34
34
34
34
34
34
34
34
34
34
34
34
343
333
285
265
162
159
.59
.10
.10
.10
.10
.10
.10
.10
.10
.10
.10
.52
.42
.68
.26
.55
.16
.56
.06
.01
.41
.47
.47
.13
.59
.10
.10
.10
.10
.10
.10
.10
.10
.10
.10
.16
.47
.04
.66
.98
.11
2
2
2
1
1
1
1
1
1
0
0
0
0
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
1
1
1
1
1
1
0
0
0
0
0
0
.30
.26
.26
.50
.52
.51
.50
.49
.48
.48
.48
.00
.00
.86
.76
.80
.64
.47
.37
.65
.49
.64
.53
.40
.30
.26
.26
.26
.29
.51
.50
.49
.48
.47
.47
.00
.00
.00
.00
.00
.00
39
39
39
39
39
39
39
39
39
39
39
90
43
18
18
20
23
25
28
33
38
38
39
39
39
39
39
39
39
39
39
39
39
39
39
73
70
59
55
31
30
.10
.30
.30
.30
.30
.30
.30
.30
.30
.30
.30
.98
.54
.53
.41
.95
.48
.63
.54
.56
.21
.99
.03
.28
.10
.30
.30
.30
.30
.30
.30
.30
.30
.30
.30
.18
.96
.84
.39
.81
.92
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
-------
4
4
4
5
6
2000
2001
2005
1965
1965
2000
2004
2020
2050
2050
0.000
0.000
0.000
0.000
0.000
10.00
10.00
10.00
10.00
10.00
0.00
0.00
0.00
0.00
0.00
570.06
570.06
572.21
200.00
200.00
0.00
0.00
0.00
0.00
0.00
46.90
46.90
46.51
123.00
123.00
0.00
0.00
0.00
0.00
0.00
153.29
153.29
149.42
386.00
386.00
0.00
0.00
0.00
0.00
0.00
29.59
29.59
28.70
90.00
90.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
1965 2050 0.000 10.00 0.00 105.00 0.00 288.00 0.00 782.00 0.00 61.00 0.00 0.00
1965 2020 0.000 10.00 0.00 464.70 0.00 59.34 0.00 221.52 0.00 90.98 0.00 0.00
-------
Appendix I
Sample Evaporative Fraction Input File for
1990 Phoenix Summertime Fuel
-------
PX90SB.EVP - Phoenix 1990 Summer Baseline Evap Fractions
1
2050
0.0171 0.0156 0.0158 0.0171 0.0156 0.0171 0.0156 0.0158 0.0171 0.0156
0.0000 0.0000 0.0000 0.0000 0.0000 0.0000 0.0000 0.0000 0.0000 0.0000
-------
Appendix J
Sample T2ATTOX Input File For Phoenix
-------
Sample Input File
1 PROMPT - No prompting, vertical
MOBTOX5 -- PX90SB.INP
1 TAMFLG - Default tampering rates
1 SPDFLG - One speed per scenario
1 VMFLAG - Default VMT mix
3 MYMRFG - Input registration distributions
2 NEWFLG - Input new exhaust emission rates
3 IMFLAG - Two I/M programs
1 ALHFLG - No corrections
2 ATPFLG - ATP
1 RLFLAG - Refueling with onboard VRS
1 LOCFLG - One LAP record for each scenario
1 TEMFLG - Use default ambient exhaust temperatures
3 OUTFMT - 112-column descriptive
1 PRTFLG - Output HC only
1 IDLFLG - Do not output idle EFs
7 1 NMHFLG
2 HCFLAG - Component and total EFs printed
.048 .079 .083 .082 .084 .081 .078 .056 .050 .051
.050 .054 .047 .037 .024 .019 .018 .017 .013 .008
.007 .005 .004 .003 .002 Idgv
.057 .097 .099 .094 .098 .082 .070 .039 .033 .029
.026 .041 .030 .028 .024 .020 .026 .025 .021 .014
.012 .012 .009 .007 .007 Idgtl
.044 .074 .073 .058 .066 .060 .058 .051 .041 .039
.038 .079 .083 .065 .043 .031 .021 .020 .015 .010
.009 .008 .006 .004 .004 Idgt2
.026 .049 .055 .042 .041 .030 .029 .023 .022 .028
.035 .072 .074 .061 .053 .038 .060 .051 .046 .032
.036 .037 .024 .025 .011 hdgv
.048 .079 .083 .082 .084 .081 .078 .056 .050 .051
.050 .054 .047 .037 .024 .019 .018 .017 .013 .008
.007 .005 .004 .003 .002 Iddv
.057 .097 .099 .094 .098 .082 .070 .039 .033 .029
.026 .041 .030 .028 .024 .020 .026 .025 .021 .014
.012 .012 .009 .007 .007 Iddt
.051 .091 .090 .078 .079 .087 .090 .049 .042 .039
.030 .052 .038 .031 .018 .012 .026 .022 .019 .012
.012 .012 .008 .006 .006 hddv
.133 .152 .149 .115 .083 .080 .065 .049 .033 .029
.022 .090 .000 .000 .000 .000 .000 .000 .000 .000
.000 .000 .000 .000 .000 me
0099 ZM DR1 DR2 Flex Pt File: NTR_IM_B.BER
1 1 1 65 67 7.488 0.186 LDGV
1 1 1 68 69 4.576 0.258
1 1 1 70 71 3.099 0.382
1 1 1 72 74 3.491 0.165
-------
Sample Input File
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
75
76
78
80
81
83
84
85
86
87
88
89
90
91
92
93
95
01
04
65
68
70
72
75
76
77
79
81
83
84
85
86
87
88
89
90
91
92
94
95
01
04
65
70
74
79
81
75
77
79
80
82
83
84
85
86
87
88
89
90
91
92
94
00
03
50
67
69
71
74
75
76
78
80
82
83
84
85
86
87
88
89
90
91
93
94
00
03
50
69
73
78
80
82
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
7.
4.
3.
3.
1.
1.
1.
0.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
9.
6.
6.
0.
1.
.068
.071
.074
.371
.398
.258
.257
.251
.303
.299
.290
.288
.200
.198
.197
.195
.169
.094
.094
.488
.576
.099
.470
.802
.813
.807
.876
.140
.156
.486
.483
.477
.487
.486
.491
.323
.306
.318
.317
.214
.110
.110
.885
.486
.486
.887
.139
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
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.282
.283
.284
.211
.149
.051
.051
.050
.058
.057
.056
.055
.019
.018
.018
.018
.011
.009
.009
.186
.258
.382
.176
.270
.272
.271
.282
.044
.045
.022
.022
.022
.022
.022
.022
.018
.017
.017
.017
.012
.008
.008
.186
.258
.176
.286
.044
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.
0.
.209
.140
.140
.137
.040
.040
.040
.040
.022
.015
.015
.143
.145
.108
.107
.106
.108
.108
.109
.047
.044
.046
.046
.025
.016
.016
.143
1.
2.
2.
2.
2.
2.
2.
2.
8.
7.
7.
1.
1.
4.
4.
4.
4.
4.
4.
2.
2.
2.
2.
9.
8.
8.
1.
.53
.22
.22
.22
.13
.13
.13
.13
.90
.87
.87
.73
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.06
.29
.29
.73
Includes LEV Sulfur Corr
Includes LEV Sulfur Corr
LDGT1
1.36
1.36
Includes LEV Sulfur Corr
Includes LEV Sulfur Corr
LDGT2
1.23
1.23
-------
Sample Input File
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
4
4
4
4
5
5
5
5
5
5
5
5
5
5
6
6
6
6
6
6
6
6
6
6
7
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
83
84
85
86
87
88
89
90
91
92
94
96
97
01
04
94
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
95
96
97
98
99
00
01
02
03
04
94
83
84
85
86
87
88
89
90
91
93
95
96
00
03
50
94
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
95
96
97
98
99
00
01
02
03
50
03
1.
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.159
.492
.500
.509
.513
.508
.508
.340
.306
.318
.317
.318
.260
.258
.258
.586
.586
.589
.589
.589
.589
.593
.593
.593
.593
.453
.161
.161
.161
.161
.161
.161
.066
.066
.066
.066
.271
.271
.231
.231
.231
.231
.202
.202
.202
.202
.320
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.045
.022
.023
.023
.023
.023
.023
.019
.017
.017
.017
.017
.012
.012
.012
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.029
.011
.011
.011
.011
.011
.011
.006
.006
.006
.006
.015
.015
.011
.011
.011
.011
.010
.010
.010
.010
.000
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.146
.109
.111
.113
.114
.113
.113
.049
.044
.046
.046
.046
.030
.030
.030
.021
.021
.021
.021
.021
.021
.011
.011
.011
.011
.038
.038
.027
.027
.027
.027
.024
.024
.024
.024
1.
4.
4.
4.
4.
4.
4.
2.
2.
2.
2.
2.
9.
9.
9.
8.
8.
8.
8.
8.
8.
7.
7.
7.
7.
3.
3.
9.
9.
9.
9.
9.
9.
9.
9.
.73
.41
.41
.41
.41
.41
.41
.13
.13
.13
.13
.13
.25
.25
.25
.90
.90
.90
.90
.90
.90
.87
.87
.87
.87
.87
.87
.21
.21
.21
.21
.01
.01
.01
.01
HDGV
LDDV
LDDT Assumes 25% LDT1 and 75% LDT2
HDDV
-------
Sample Input File
1 7 1 04 50 0.290 0.000
78 31 67 80 08 08
78 31 81 94 08 08
88 67 50 2222 11
TX EVP FRACTIONS :
TX EXH EMISSIONS :
OFFCYCLE FACTORS :
1 90 19.6 76.2 20.
PX90SB.INP Spr I
1 90 19.6 93.6 20.
PX90SB.INP Sum I
1111
1111
096 111 2222
096 111 2222
096 22221111
EVP\PX90SB.EVP
EXH\PX90SB_B.EXH
OFF\IM90.0FF
6 27.3 20.6 7
i 064. 088. 08.1
6 27.3 20.6 7
i 083. 105. 08.1
08.1 20 1 1 2 1
08.1 20 1 1 2 1
-------
Appendix K
Sample T2ATTOX Output For Phoenix
-------
Appendix K
Sample Output File
1MOBTOX5 -- PX90SB.INP
M5TOXRAD based on MobileSb(27FEB98)Mods by Radian 7/98
Reading I/M credits information
Annual Idle Only 220/1.2 Cutpoints IDLE.IMC
Evap Toxic emission frac. data read from file : EVP\PX90SB.EVP
Exhaust Toxic emission data read from file
EXH\PX90SB B.EXH
Off Cycle data read from file
OFF\IM90.0FF
EVP\PX90SB.EVP
EXH\PX90SB_B.EXH
OFF\IM90.OFF
: PX90SB.EVP - Phoenix 1990 Summer Baseline Evap Fractions
: IV MYA MYB TOG-N TOG-H BZ-N BZ-H AC-N
AC-H
FR-N
Off-Cycle Corrections - I/M 1990
UC/FTP Toxics Mass Fraction Ratios
Benzene
Year
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
TX-Lo
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
39 .
36 .
36 .
37 .
35 .
34 .
31.
27 .
27 .
24 .
23 .
23 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.580
.990
.520
.860
.830
.120
.650
.370
.360
.710
.610
.910
& TOG Emissions
TX-
464 .
464 .
464 .
464 .
464 .
464 .
464 .
464 .
464 .
464 .
464 .
464 .
464 .
464 .
464 .
464 .
193 .
192 .
193 .
195 .
194 .
195.
195.
195 .
195 .
195.
195.
195 .
-Hi
.700
.700
.700
.700
.700
.700
.700
.700
.700
.700
.920
.940
.940
.950
.950
.970
.310
.960
.610
.090
.950
.360
.420
.550
.530
.550
.550
.530
TOG-Hi
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.
0.
0 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.640
.628
.628
.639
.644
.641
.612
.570
.557
.535
.514
.519
for LDGVs from files : EXH\PX90SB B . EX EVP\PX90SB . EVP OFF\IM90.
TOG-Lo
10 .
10.
10.
10 .
10 .
10.
10.
10 .
10 .
10.
10.
10 .
10 .
10.
10.
10 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
TXEVHS
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.
0.
0 .
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
TXEVDI
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.
0.
0 .
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
TXEVRF
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.
0.
0 .
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
TXEVRN EVPTXRST
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.
0.
0 .
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
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.
0.
0 .
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
AGG
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.079
.079
.078
.090
.089
.081
.081
.122
.120
.118
.137
.137
.136
.135
.135
.211
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
A/C
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.016
.016
.015
.018
.017
.016
.016
.023
.023
.023
.026
.026
.026
.026
.025
.037
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.OFF
AGG-TOX
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.126
.128
.156
.165
.175
.213
.228
.247
.273
.315
.315
.315
-------
Sample Output File
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
2011
2012
2013
2014
2015
2016
2017
2018
2019
2020
23 .
23 .
15 .
15.
15.
15 .
15 .
15.
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
010 195
170 195
400 195
420 195
420 195
420 195
420 195
420 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
720 195
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
.550
0.498
0 .500
0 .332
0.332
0.332
0 .332
0 .332
0.332
0.117
0 .117
0 .117
0.117
0.117
0 .117
0 .117
0.117
0.117
0 .117
0 .117
0.117
0.117
0 .117
0 .117
0.117
0.117
0 .117
0 .117
0.117
Acetaldehyde & TOG Emissions
Year
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
TX
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
2 .
2 .
2 .
-Lo TX
000 59
000 59
000 59
000 59
000 59
000 59
000 59
000 59
000 59
000 59
000 49
000 48
000 48
000 47
000 47
000 47
460 15
460 16
410 15
-Hi
.340
.340
.340
.340
.340
.340
.340
.340
.340
.340
.080
.430
.430
.790
.790
.150
.980
.150
.840
TOG-Hi
0.000
0.000
0 .000
0 .000
0.000
0.000
0 .000
0 .000
0.000
0.000
0 .000
0 .000
0.000
0.000
0 .000
0 .000
0.640
0.628
0 .628
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
for
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
LDGVs
TOG-Lo
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
4
4
4
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.030
.030
.030
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
from
AGG
1.048
1.048
1 .048
1 .055
1.055
1.050
1 .050
1 .074
1.074
1.073
1 .078
1 .078
1.077
1.077
1 .091
1 .091
1.258
1.249
1 .238
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
0
0
file
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
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 .
0 .
0.
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
: EXH\PX90SB B
A/C
.002
.002
.002
.003
.003
.003
.003
.004
.004
.004
.004
.004
.004
.004
.004
.004
.011
.011
.010
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
.EX OFF\IM90.
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
OFF
.230
.230
.290
.290
.290
.290
.290
.290
.220
.150
.052
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
1.040
1 .040
1 .010
1.010
1.010
1 .010
1 .010
1.010
1.003
0 .995
0 .985
0.980
0.980
0 .980
0 .980
0.980
0.980
0 .980
0 .980
0.980
0.980
0 .980
0 .980
0.980
0.980
0 .980
0 .980
0.980
1.315
1 .315
1 .315
1.315
1.315
1 .315
1 .315
1.315
1.315
1 .315
1 .315
1.315
1.315
1 .315
1 .315
1.315
1.315
1 .315
1 .315
1.315
1.315
1 .315
1 .315
1.315
1.315
1 .315
1 .315
1.315
AGG-TOX
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
0.
0.
0 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.919
.920
.935
-------
Sample Output File
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
2011
2012
2013
2014
2015
2016
2017
2018
2019
2020
2 .330
2 .380
2 .330
2 .260
2 .140
2 .100
2 .050
2 .000
2 .010
1 .960
1 .970
1.310
1.310
1 .310
1 .310
1.310
1.310
0 .400
0 .400
0.400
0.400
0 .400
0 .400
0.400
0.400
0 .400
0 .400
0.400
0.400
0 .400
0 .400
0.400
0.400
0 .400
0 .400
0.400
0.400
Formaldehyde
Year
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
TX-Lo
0.000
0 .000
0 .000
0.000
0.000
0 .000
0 .000
0.000
0.000
0 .000
15.
15 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
14 .
.120
.190
.980
.960
.890
.900
.890
.890
.900
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
.890
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
.639
.644
.641
.612
.570
.557
.535
.514
.519
.498
.500
.332
.332
.332
.332
.332
.332
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
& TOG Emissions
TX-Hi
221.
221 .
221 .
221.
221.
221 .
221 .
221.
221.
221 .
.520
.520
.520
.520
.520
.520
.520
.520
.520
.520
TOG-Hi
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
4
for
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
LDGVs
TOG-Lo
10
10
10
10
10
10
10
10
10
10
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
1.230
1 .230
1 .230
1.230
1.230
1 .230
1 .230
1.230
1.230
1 .230
1 .230
1.290
1.290
1 .290
1 .290
1.290
1.290
1 .223
1 .155
1.061
1.020
1 .020
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
from
AGG
1.044
1 .044
1 .044
1.043
1.042
1 .048
1 .047
1.047
1.046
1 .052
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
file
0
0
0
0
0
0
0
0
0
0
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.010
.008
.005
.002
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
0.940
0 .945
0 .966
0.973
0.983
0 .997
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
1 .020
1 .020
1.020
1.020
: EXH\PX90SB B . EX OFF\IM90 . OFF
A/C
.998
.998
.998
.998
.998
.998
.998
.998
.998
.997
AGG-TOX
1.000
1 .000
1 .000
1.000
1.000
1 .000
1 .000
1.000
1.000
1 .000
-------
Sample Output File
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
2011
2012
2013
2014
2015
2016
2017
2018
2019
2020
0.
0 .
0 .
0.
0.
0 .
6 .
6 .
6 .
6 .
6 .
6 .
5.
5 .
5 .
5.
5.
5 .
5 .
5.
3 .
3 .
3 .
3 .
3 .
3 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.000
.000
.000
.000
.000
.000
.840
.910
.640
.080
.250
.090
.850
.520
.430
.290
.130
.200
.020
.040
.350
.350
.350
.350
.350
.350
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
.020
163 .
160 .
160 .
156 .
156 .
153 .
41 .
42 .
40.
35 .
36 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
34 .
.840
.240
.240
.630
.630
.020
.460
.610
.490
.620
.090
.730
.540
.100
.180
.130
.100
.180
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
.100
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.000
.000
.000
.000
.000
.000
.640
.628
.628
.639
.644
.641
.612
.570
.557
.535
.514
.519
.498
.500
.332
.332
.332
.332
.332
.332
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
10.
10 .
10 .
10.
10.
10 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
.000
.000
.000
.000
.000
.000
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.051
.050
.048
.047
.090
.091
.264
.253
.241
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.230
.290
.290
.290
.290
.290
.190
.090
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.997
.997
.998
.998
.996
.996
.989
.989
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.990
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
1 .
1 .
1 .
1 .
1 .
1 .
0 .
0.
0.
0 .
0 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.000
.000
.000
.000
.000
.000
.894
.897
.936
.949
.964
.018
.039
.066
.103
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
.163
1,3 Butadiene & TOG Emissions for LDGVs from file : EXH\PX90SB_B.EX OFF\IM90.OFF
Year TX-Lo TX-Hi TOG-Hi TOG-Lo AGG A/C AGG-TOX
1965 0.000 90.980 0.000 10.000 1.000 1.000 1.000
-------
Sample Output File
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
2011
2012
2013
2014
2015
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
2 .
2 .
2 .
2 .
2 .
2 .
2 .
2 .
2 .
2 .
2 .
2 .
2 .
2 .
1 .
1 .
1 .
1 .
1 .
1 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.540
.510
.490
.480
.530
.530
.410
.270
.240
.170
.090
.130
.030
.050
.360
.360
.360
.360
.360
.360
.420
.420
.420
.420
.420
.420
.420
.420
.420
.420
.420
.420
.420
.420
.420
90.
90 .
90 .
90.
90.
90 .
90 .
90.
90.
53 .
50 .
50.
48 .
48 .
45 .
33 .
32 .
33 .
38 .
37.
38 .
38 .
39 .
39.
39.
39 .
39 .
39.
39.
39 .
39 .
39.
39.
39 .
39 .
39.
39.
39 .
39 .
39.
39.
39 .
39 .
39.
39.
39 .
39 .
39.
39.
39 .
.980
.980
.980
.980
.980
.980
.980
.980
.980
.030
.660
.660
.280
.280
.910
.190
.230
.990
.040
.650
.780
.930
.300
.230
.280
.300
.230
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
.300
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.640
.628
.628
.639
.644
.641
.612
.570
.557
.535
.514
.519
.498
.500
.332
.332
.332
.332
.332
.332
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
.117
10.
10 .
10 .
10.
10.
10 .
10 .
10.
10.
10 .
10 .
10.
10.
10 .
10 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.708
.712
.760
.776
.793
.860
.885
.918
.963
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
.037
-------
Sample Output File
2016
2017
2018
2019
2020
MTBE
Year
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
0.
0 .
0 .
0.
0.
.420
.420
.420
.420
.420
39.
39 .
39 .
39.
39.
.300
.300
.300
.300
.300
0.
0 .
0 .
0.
0.
.117
.117
.117
.117
.117
& TOG Emissions
TX-Lo
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
TX-Hi
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
TOG-Hi
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.640
.628
.628
.639
.644
.641
.612
.570
.557
.535
.514
.519
.498
.500
.332
.332
.332
.332
.332
.332
.117
.117
.117
.117
.117
.117
4 .
4 .
4 .
4 .
4 .
.030
.030
.030
.030
.030
1 .
1 .
1 .
1 .
1 .
.000
.000
.000
.000
.000
1 .
1 .
1 .
1 .
1 .
.000
.000
.000
.000
.000
1 .
1 .
1 .
1 .
1 .
.037
.037
.037
.037
.037
for LDGVs from files : EXH\PX90SB !
TOG-Lo
10.
10 .
10 .
10.
10.
10 .
10 .
10.
10.
10 .
10 .
10.
10.
10 .
10 .
10.
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
4 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
.030
TXEVHS
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
TXEVDI
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
TXEVRF
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
3. EX
TXEVRN
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
.017
EVP\PX90SB.EVP OFF\IM90
EVPTXRST
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 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
0 .
0.
0.
0 .
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
.016
AGG
1.079
1 .079
1 .078
1.090
1.089
1 .081
1 .081
1.122
1.120
1 .118
1 .137
1.137
1.136
1 .135
1 .135
1.211
1.230
1 .230
1 .230
1.230
1.230
1 .230
1 .230
1.230
1.230
1 .230
1 .230
1.230
1.230
1 .230
1 .290
1.290
1.290
1 .290
1 .290
1.290
1.220
1 .150
1 .052
1.010
1.010
1 .010
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
0
0
0
0
0
A/C
.016
.016
.015
.018
.017
.016
.016
.023
.023
.023
.026
.026
.026
.026
.025
.037
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.040
.010
.010
.010
.010
.010
.010
.003
.995
.985
.980
.980
.980
.OFF
AGG-TOX
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
1 .
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 .
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.000
.965
.963
.943
.936
.929
.900
.890
.876
.856
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
.825
-------
Sample Output File
2007
2008
2009
2010
2011
2012
2013
2014
2015
2016
2017
2018
2019
2020
0
-M170
0.000
0 .000
0 .000
0.000
0.000
0 .000
0 .000
0.000
0.000
0 .000
0 .000
0.000
0.000
0 .000
Warning :
0.000
0 .000
0 .000
0.000
0.000
0 .000
0 .000
0.000
0.000
0 .000
0 .000
0.000
0.000
0 .000
0.117
0 .117
0 .117
0.117
0.117
0 .117
0 .117
0.117
0.117
0 .117
0 .117
0.117
0.117
0 .117
4 .030
4 .030
4 .030
4 .030
4 .030
4 .030
4 .030
4 .030
4 .030
4 .030
4 .030
4 .030
4 .030
4 .030
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0 .017
0.017
0.017
0 .017
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
0 .016
0.016
0.016
0 .016
1.010
1 .010
1 .010
1.010
1.010
1 .010
1 .010
1.010
1.010
1 .010
1 .010
1.010
1.010
1 .010
0.980
0 .980
0 .980
0.980
0.980
0 .980
0 .980
0.980
0.980
0 .980
0 .980
0.980
0.980
0 .980
0.825
0 .825
0 .825
0.825
0.825
0 .825
0 .825
0.825
0.825
0 .825
0 .825
0.825
0.825
0 .825
-Ml54 Warning:
Exhaust emissions for gasoline fueled vehicles
beginning in 1995 have been reduced as a result of
Gasoline Detergent Additive Regulations (1994) .
Refueling emissions for LDGV and LDGT after 1998
model year have been reduced as a result of the
Onboard Refueling Vapor Recovery Regulations (1994)
0
+
0 Eqn.
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
Emission Factor Modification
Reg
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
Veh
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
Pol
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
First
1965
1968
1970
1972
1975
1976
1978
1980
1981
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1995
2001
2004
Last
1967
1969
1971
1974
1975
1977
1979
1980
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1994
2000
2003
2050
7.
4.
3 .
3 .
1.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
Base
.4880
.5760
. 0990
.4910
.0680
.0710
. 0740
.3710
.3980
.2580
.2570
.2510
.3030
.2990
.2900
.2880
.2000
.1980
. 1970
. 1950
.1690
.0940
. 0940
Profile
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
DR1
.1860
.2580
.3820
. 1650
.2820
.2830
.2840
.2110
.1490
.0510
. 0510
. 0500
.0580
.0570
. 0560
. 0550
.0190
.0180
. 0180
. 0180
.0110
.0090
. 0090
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
DR2
.2090
.1400
. 1400
. 1370
.0400
.0400
. 0400
. 0400
.0220
.0150
. 0150
1.
2.
2 .
2 .
2.
2.
2 .
2 .
8.
7.
7.
KINK
.5300
.2200
.2200
.2200
.1300
.1300
. 1300
. 1300
.9000
.8700
. 8700
Altered
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
-------
Sample Output File
24
25
26
27
28
29
30
31
32
33
34
35
36
37
38
39
40
41
42
43
44
45
46
47
48
49
50
51
52
53
54
55
56
57
58
59
60
61
62
63
64
65
66
67
68
69
70
71
72
73
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
4
4
4
4
4
4
4
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1965
1968
1970
1972
1975
1976
1977
1979
1981
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1994
1995
2001
2004
1965
1970
1974
1979
1981
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1994
1996
1997
2001
2004
1994
1995
1996
1997
1998
1999
2000
1967
1969
1971
1974
1975
1976
1978
1980
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1993
1994
2000
2003
2050
1969
1973
1978
1980
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1993
1995
1996
2000
2003
2050
1994
1995
1996
1997
1998
1999
2000
7.
4 .
3 .
3.
1.
1.
1.
0.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
9.
6.
6 .
0.
1.
1.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.4880
. 5760
. 0990
.4700
.8020
. 8130
. 8070
.8760
.1400
. 1560
.4860
.4830
.4770
.4870
.4860
.4910
.3230
.3060
.3180
.3170
.2140
. 1100
. 1100
.8850
.4860
.4860
. 8870
.1390
.1590
.4920
. 5000
.5090
.5130
. 5080
. 5080
.3400
.3060
.3180
.3170
.3180
.2600
.2580
.2580
.5215
.5210
. 5224
. 5219
.5213
.5213
. 5248
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.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
.1860
.2580
.3820
.1760
.2700
.2720
.2710
.2820
.0440
. 0450
. 0220
.0220
.0220
. 0220
. 0220
.0220
.0180
. 0170
. 0170
.0170
.0120
. 0080
. 0080
.1860
.2580
. 1760
.2860
.0440
.0450
. 0220
. 0230
.0230
.0230
. 0230
. 0230
.0190
.0170
. 0170
. 0170
.0170
.0120
. 0120
. 0120
.0329
.0329
. 0328
. 0328
.0327
.0327
. 0327
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.
0.
0.
0.
0.
0.
.1430
. 1450
. 1080
.1070
.1060
. 1080
. 1080
.1090
.0470
. 0440
. 0460
.0460
.0250
. 0160
. 0160
.1430
.1460
. 1090
. 1110
.1130
.1140
. 1130
. 1130
.0490
.0440
. 0460
. 0460
.0460
.0300
. 0300
. 0300
1.
1.
4 .
4.
4.
4 .
4 .
4.
2.
2 .
2 .
2.
9.
8 .
8 .
1.
1.
4 .
4 .
4.
4.
4 .
4 .
2.
2.
2 .
2 .
2.
9.
9.
9.
.7300
. 7300
.4100
.4100
.4100
.4100
.4100
.4100
.1300
. 1300
. 1300
.1300
.0600
.2900
.2900
.7300
.7300
.4100
.4100
.4100
.4100
.4100
.4100
.1300
.1300
. 1300
. 1300
.1300
.2500
.2500
.2500
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
-------
Sample Output File
74 1 4 1
75 1 4 1
76 1 4 1
77 1 4 1
78 1 5 1
79 1 5 1
80 1 5 1
81 1 5 1
82 1 5 1
83 1 5 1
84 1 5 1
85 1 5 1
86 1 5 1
87 1 5 1
88 1 6 1
89 1 6 1
90 1 6 1
91 1 6 1
92 1 6 1
93 1 6 1
94 1 6 1
95 1 6 1
96 1 6 1
97 1 6 1
98 1 7 1
99 1 7 1
2001
2002
2003
2004
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
1994
2004
2001
2002
2003
2050
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
1995
1996
1997
1998
1999
2000
2001
2002
2003
2050
2003
2050
OI/M program #1 selected:
OStart year (Jan 1) :
Pre-1981 stringency
First MYR covered:
Last MYR covered:
Waiver (pre-1981) :
Waiver (1981 + ) :
Compliance Rate:
1978
: 31%
1967
1980
8.%
8.%
96 . %
Inspection type:
Test Only
Inspection frequency: Annual
I/M program #1 vehicle types
LDGV - Yes
LDGT1 - Yes
LDGT2 - Yes
HDGV - Yes
1981 & later MYR test type:
Idle
Cutpoints, HC: 220.000
Cutpoints, CO: 1.200
Cutpoints, NOx: 999.000
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.
.5248
. 5248
. 5248
.4009
.1610
. 1610
. 1610
.1610
.1610
. 1610
. 0660
.0660
.0660
. 0660
.2710
.2710
.2310
.2310
.2310
.2310
.2020
.2020
.2020
.2020
.6516
. 5904
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.
.0327
. 0327
. 0327
.0257
.0110
. 0110
. 0110
.0110
.0110
. 0110
. 0060
.0060
.0060
. 0060
. 0150
.0150
.0110
. 0110
. 0110
.0110
.0100
. 0100
. 0100
.0100
.0000
. 0000
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
.0210
. 0210
. 0210
.0210
.0210
. 0210
. 0110
.0110
.0110
. 0110
. 0380
.0380
.0270
. 0270
. 0270
.0270
.0240
. 0240
. 0240
.0240
I/M program
Start
year
8
8
8
8
8
8
7
7
7
7
3
3
9
9
9
9
9
9
9
9
#2
(Jan
.9000
. 9000
. 9000
.9000
.9000
. 9000
. 8700
.8700
.8700
. 8700
. 8700
.8700
.2100
.2100
.2100
.2100
.0100
. 0100
. 0100
.0100
selected:
1) : 1978
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Pre-1981 stringency: 31%
First
Last
MYR covered: 1981
MYR covered: 1994
Annual
Waiver (pre-1981):
Waiver (1981 + ) :
Compliance Rate:
Inspection type:
Test Only
Inspection frequency:
I/M program #2 vehicle types
LDGV - Yes
LDGT1 - Yes
LDGT2 - Yes
HDGV - Yes
1981 & later MYR test type:
Idle
Cutpoints, HC: 220.000
Cutpoints, CO: 1.200
Cutpoints, NOx: 999.000
Low alt, Annl and Bien Insp Freq TECH 1 & 2 I/M cred data
-------
Sample Output File
Annual Idle Only 220/1.2 Cutpoints IDLE. IMC
OFunctional Check Program Description:
OCheck Start Model Yrs Vehicle Classes Covered Inspection Comp Eff
(Janl) Covered LDGV LDGT1 LDGT2 HDGV Type Freq Rate Adj
ATP 1988 1967-2050 Yes Yes Yes Yes Test Only Annual 96.0% 1.00
OAir pump system disablements: Yes Catalyst removals: Yes
Fuel inlet restrictor disablements: Yes Tailpipe lead deposit test: Yes
EGR disablement: No Evaporative system disablements: No
PCV system disablements: No Missing gas caps: No
OTOG HC emission factors include evaporative HC emission factors.
0
OEmission factors are as of July 1st of the indicated calendar year.
OUser supplied basic exhaust emissions rates, veh registration distributions.
OCal. Year: 1990 I/M Program: Yes Ambient Temp: 82.2 (F) Region: Low
Anti-tarn. Program: Yes Operating Mode: 20.6 / 27.3 / 20.6 Altitude: 500. Ft.
Reformulated Gas: Yes ASTM Class: B
OPX90SB.INP Spr Minimum Temp: 64. (F) Maximum Temp: 88. (F)
Period 1 RVP: 8.1 Period 2 RVP: 8.1 Period 2 Start Yr: 2020
0 Veh. Type: LDGV LDGT1 LDGT2 LDGT HDGV LDDV LDDT HDDV MC
Veh. Speeds:
VMT Mix:
OComposite
Total
Exhst
Evap .
Refuel
Runing
Rsting
Exhst
Exhst
Exhst
Total
Exhst
Evap .
Refuel
Runing
Rsting
Toxic
Bnz
Bnz
Bnz
Bnz
Bnz
Bnz
Act
Frm
But
MTB
MTB
MTB
MTB
MTB
MTB
19.
0.
.6
. 645
Emission
121.
103 .
7.
2.
6.
1.
8.
26 .
10.
0.
0.
0.
0.
0.
0.
.98
. 71
.44
.74
.81
.28
.63
. 73
.70
. 00
. 00
.00
.00
. 00
. 00
19.
0.
.6
. 168
Factors
117.
98 .
8 .
3.
5.
1.
9.
30.
10.
0.
0.
0.
0.
0.
0.
.29
. 16
. 91
.53
.57
. 13
.08
. 13
.60
. 00
. 00
.00
.00
. 00
. 00
19.
0.
.6
. 082
19.
0.
.6 19.6
.031 0.008
19.6 19.6 19.
0.002 0.056 0.
.6
. 008
All Veh
(mg/Mile)
201.
169.
17.
3.
9.
1.
18.
65.
24.
0.
0.
0.
0.
0.
0.
.73
. 96
. 02
.75
.90
. 09
.56
.27
.59
. 00
. 00
.00
.00
. 00
. 00
144.
121.
11.
3.
6.
1.
12.
41.
15.
30.
5.
15.
3.
5.
0.
.92
. 66
. 57
.60
.99
. 11
.18
. 63
.18
. 79
. 71
.57
.13
. 50
. 87
404.
325.
53 .
6.
17.
1.
46.
237.
50.
0.
0.
0.
0.
0.
0.
.32 14.81
.13 14.81
. 81
.14
.28
. 95
.14 9.11
.28 28.58
.54 6.66
.00 0. 00
.00 0. 00
.00
.00
. 00
. 00
20.95 32.59 164.
20.95 32.59 119.
40.
5.
12.89 89.39 15.
40.44 242.72 56.
9.43 18.93 23.
0. 00 0. 00 0.
0. 00 0. 00 0.
0.
0.
.88
. 07
. 09
. 72
.21
. 76
.31
. 00
. 00
.00
. 00
130.724
110 .310
9 .668
2 .859
6 .679
1 .208
15.244
49 .290
13 .576
0 .000
0 .000
0.000
0.000
0 .000
0 .000
-Ml70 Warning:
-Ml54 Warning:
Exhaust emissions for gasoline fueled vehicles
beginning in 1995 have been reduced as a result of
Gasoline Detergent Additive Regulations (1994).
Refueling emissions for LDGV and LDGT after 1998
-------
Sample Output File
model year have been reduced as a result of the
Onboard Refueling Vapor Recovery Regulations (1994).
OEmission factors are as of July 1st of the indicated calendar year.
OUser supplied basic exhaust emissions rates, veh registration distributions.
OCal. Year: 1990 I/M Program
Ant i- tarn. Program
Reformulated Gas
OPX90SB.INP Sum
Period 1 RVP
0 Veh. Type: LDGV LDGT1
Veh. Speeds:
VMT Mix:
19.
0.
.6
.645
OComposite Toxic Emission
Total
Exhst
Evap .
Refuel
Runing
Rsting
Exhst
Exhst
Exhst
Total
Exhst
Evap .
Refuel
Runing
Rsting
Bnz
Bnz
Bnz
Bnz
Bnz
Bnz
Act
Frm
But
MTB
MTB
MTB
MTB
MTB
MTB
157.
122.
12 .
3 .
17.
2.
10.
31.
12 .
0.
0.
0.
0.
0.
0.
.97
.31
.46
. 60
.49
.11
.30
.99
. 57
.00
. 00
. 00
.00
.00
. 00
19.
0.
.6
.168
: Yes
: Yes
: Yes
: 8.1
LDGT2
19.
0.
.6
.082
Ambi ent Temp : 1 0 0 . 4
Operating Mode: 20.6
ASTM Class: B
Minimum Temp: 83.
Period 2 RVP: 8 .1
LDGT HDGV
19.
0.
.6
.031
(F) Region: Low
/ 27.3 / 20.6 Altitude: 500. Ft.
(F) Maximum Temp: 105. (F)
Period 2 Start Yr: 2020
LDDV LDDT HDDV MC
19.6 19.6 19.6 19.
0.008 0.002 0.056 0.
.6
.008
All
Veh
Factors (mg/Mile)
149.
114.
13 .
4 .
14.
1.
10.
35.
12 .
0.
0.
0.
0.
0.
0.
.56
.93
. 98
. 64
.15
.86
. 69
.44
.36
.00
. 00
. 00
.00
.00
. 00
242.
186.
23 .
4 .
25.
1.
20.
69.
25.
0.
0.
0.
0.
0.
0.
.01
.14
. 66
. 93
.48
.80
. 03
.88
. 92
.00
. 00
. 00
.00
.00
. 00
179.
138.
17.
4 .
17.
1.
13 .
46.
16 .
30.
5.
15.
3.
5.
0.
.81
.23
. 15
. 73
.86
.84
. 75
.71
. 80
.79
. 71
. 57
.13
.50
. 87
506.
364.
85.
8 .
44.
3.
51.
265.
56 .
0.
0.
0.
0.
0.
0.
.40
.56
. 74
. 07
.80
.22
. 68
.81
. 62
.00
. 00
. 00
.00
.00
. 00
14.81 20.95 32.59 203.
14.81 20.95 32.59 118.
75.
9.
9.11 12.89 89.39 15.
28.58 40.44 242.72 56.
6.66 9.43 18 . 93 23 .
0.00 0.00 0.00 0.
0. 00 0. 00 0. 00 0.
0.
0.
.70
.40
. 88
.43
. 12
.44
. 18
.00
. 00
. 00
. 00
166 .
127.
15 .
3 .
17.
1 .
16 .
54 .
15 .
0.
0 .
0 .
0.
0.
0 .
.133
.676
.572
.757
.135
.993
.883
.840
.370
.000
.000
.000
.000
.000
.000
------- |