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 ------- 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. ------- 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 ------- 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 ------- 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- ------- 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- ------- 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- ------- 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- ------- 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 ------- 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. ------- 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 ------- 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 ------- 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 ------- 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- ------- 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.) -11- ------- 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. -12- ------- 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. ### -13- ------- 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. -14- ------- 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 -15- ------- 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. -16- ------- 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 -17- ------- 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. -18- ------- 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 ------- 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 -19- ------- 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: -20- ------- 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. -21- ------- 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 -22- ------- 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- ------- 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- ------- 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 -25- ------- 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 -26- ------- 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) -27- ------- 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. ### -28- ------- 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- ------- 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- ------- 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- ------- 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: -32- ------- 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 -34- ------- 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 -35- ------- 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. -36- ------- 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. -37- ------- 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. -38- ------- 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 -39- ------- 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 -40- ------- 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. -41- ------- 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 -42- ------- 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 -43- ------- 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 -44- ------- 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) -45- ------- 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 -46- ------- 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- ------- 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- ------- 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- ------- 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- ------- 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- ------- 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- ------- 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- ------- 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- ------- 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- ------- 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- ------- 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- ------- 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- ------- 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. ------- 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. ------- 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. ------- 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. ------- 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. ------- 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 ------- 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. ------- 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 ------- |