## APPENDIX 4: Technical Support Document for TRIM-Based

M ultipathway Screening Scenario for RTR: Summary of Approach and EvaluationAppendix 5 i 

### [This page intentionally left blank.]Appendix 5 ii 

### TABLE OF CONTENTS

EXECUTIVE SUMMARY

........................................................................................................... vi

1 Introduction

...................................................................................................................... 1

1.1 Background

..................................................................................................................... 1

1.2 Organization of this Document

........................................................................................ 2

2 Approach for Screening Evaluation of Multipathway Exposures

................................ . 2

2.1 Overview

......................................................................................................................... 2

2.2 Chemicals of Potential Concern

...................................................................................... 3

2.3 Use of Screening Threshold Emission Levels

.................................................................. 5

2.4 The TRIM-Based Screening Scenario: Basis for Threshold Emission Rates

.................. 7 2.4.1 Exposure Routes Evaluated

................................................................................ 7 2.4.2 Approach to Configuration and Parameterization

................................................ 8 2.4.3 Modeling Framework

.......................................................................................... 9 2.4.3.1 Fate and Transport Modeling

............................................................... 10 2.4.3.2 Exposure Modeling and Risk Characterization

..................................... 11

2.5 Refined Analyses

.......................................................................................................... 12

3 Description of Modeling Scenario

................................................................................. 12

3.1 TRIM.FaTE Scenario Configuration and Parameterization

............................................ 12 3.1.1 Chemical Properties

........................................................................................... 13 3.1.2 Spatial Layout

.................................................................................................... 13 3.1.3 Watershed and Water Body Parameterization

................................................... 15 3.1.3.1 Water Balance

..................................................................................... 15 3.1.3.2 Sediment Balance

................................................................................ 16 3.1.4 Meteorology

....................................................................................................... 17 3.1.5 Aquatic Food Web

............................................................................................. 19 3.1.6 Using TRIM.FaTE Media Concentrations

........................................................... 19

3.2 Exposure and Risk Calculations

.................................................................................... 21 3.2.1 Calculating Concentrations in Farm Food Chain Media

..................................... 21 3.2.2 Ingestion Exposure Assessment

........................................................................ 22 3.2.2.1 Ingestion Exposure Pathways and Routes of Uptake

........................... 22 3.2.2.2 Exposure Scenarios and Corresponding Inputs

................................... 22 3.2.2.3 Calculating Average Daily Doses

......................................................... 24 3.2.2.4 Infant Ingestion of Breast Milk

.............................................................. 25 3.2.3 Risk Characterization

......................................................................................... 25 3.2.4 Dermal Risk Screening

...................................................................................... 26 3.2.4.1 Hazard Identification and Dose Response Assessment

....................... 26 3.2.4.2 Dermal Exposure Estimation

................................................................ 27 3.2.4.3 Screening-Level Cancer Risks and Non-Cancer Hazard Quotients

...... 31 3.2.4.4 Dermal Screening Results

................................................................... 32

3.3 Summary of Scenario Assumptions

............................................................................... 33Appendix 5 iii



### 4 Evaluation of Screening Scenario

................................................................................. 36

4.1 Overview

....................................................................................................................... 36

4.2 Overall Chemical Mass Partitioning

............................................................................... 38

4.3 Comparison to Measured Concentrations

..................................................................... 38 4.3.1 Scope of the Evaluation

..................................................................................... 38 4.3.2 Methods and Organization of this Section

.......................................................... 40 4.3.3 Chemical-Specific Comparisons

........................................................................ 41 4.3.3.1 Cadmium

............................................................................................. 41 4.3.3.2 Mercury

................................................................................................ 45 4.3.3.3 Dioxins (2,3,7,8-TCDD)

........................................................................ 54 4.3.3.4 PAHs (Benzo[a]pyrene)

....................................................................... 61 4.3.4 Summary

........................................................................................................... 68

5 References

...................................................................................................................... 70

Attachment 1

–

TRIM.FaTE Inputs Attachment 2

–

RTR Access-based Exposure and Risk Calculation Tool - Multimedia Ingestion Risk Calculator (MIRC) Attachment 3

–

Systematic Sensitivity AnalysisAppendix 5 iv 

### LIST OF EXHIBITS

Exhibit 2-1. Conceptual Decision Tree for Evaluation of N on -Inhalation Exposures of PB-HAPs

.............. 4
Exhibit 2-2. OAQPS PB-HAP Compounds a

................................................................................................ 5

Exhibit 2-3. Emission Thresholds for Screening of Multipathway Exposures

.............................................. 6
Exhibit 2-4. Overview of Ingestion Exposure and Risk Screening Evaluation Method

.............................. 10
Exhibit 2-5. Overview of Process Carried Out in the Multimedia Ingestion Risk Calculator

...................... 12
Exhibit 3-1. TRIM.FaTE Surface Parcel Layout

......................................................................................... 13
Exhibit 3-2. Summary of Key Meteorological Inputs

.................................................................................. 18
Exhibit 3-3. Aquatic Biota Parameters for the TRIM.FaTE Screening Scenario

........................................ 20
Exhibit 3-4. Spatial Considerations

– TRIM.FaTE Results Selected for Calculating Farm Food Chain

Media Concentrations and Receptor Exposures

................................................................... 21
Exhibit 3-5. Summary of Ingestion Exposure Pathways and Routes of Uptake

........................................ 23

Exhibit 3- 6. Overview of Exposure Factors Used for RTR Multipathway Screening a,b

............................. 24
Exhibit 3-7. Dose-response Values for PB-HAPs Addressed by the Screening Scenario

........................ 25
Exhibit 3-8. Cancer Slope Factors and Reference Doses Based on Absorbed Dose

............................... 27
Exhibit 3-9. Receptor-Specific Body Surface Area Assumed to be Exposed to Chemicals

...................... 29
Exhibit 3-10. Scenario-Specific Exposure Values for Water and Soil Contact

.......................................... 30
Exhibit 3-11. Chemical-Specific Dermal Exposure Values for Water and Soil Contact

............................. 31
Exhibit 3-12. Summary of Dermal Non-Cancer Hazards

........................................................................... 32
Exhibit 3-13. Summary of Dermal Cancer Risks

........................................................................................ 33
Exhibit 3-14. Summary of RTR Screening Scenario Assumptions and Associated Conservatism

........... 34
Exhibit 4-1. Distribution of Chemical Mass in Screening Scenario

............................................................ 39
Exhibit 4-2. Summary of Modeled and Observed Concentrations of Cadmium in Environmental Media . 43

Exhibit 4-3. TRIM.FaTE Cadmium Concentrations in Fish and Calculated Bioaccumulation Factors with

Respect to Total Water Concentration

................................................................................... 44
Exhibit 4-4. Fraction of Cadmium Mass Sorbed vs. Dissolved in TRIM.FaTE Compartments

.................. 44
Exhibit 4-5. Summary of Modeled and Observed Concentrations of Cadmium in Ingestible Media

......... 46
Exhibit 4-6. Estimated Contribution of Modeled Food Types to Cadmium Ingestion Exposures and

Hazard Quotient

..................................................................................................................... 47
Exhibit 4-7. Summary of Modeled and Observed Concentrations of Total Mercury in Environmental

Media

...................................................................................................................................... 49
Exhibit 4-8. TRIM.FaTE Mercury Concentrations, Speciation, and Calculated Methyl Mercury

Bioaccumulation Factors (in parentheses) in Fish Compartments

........................................ 50
Exhibit 4-9. TRIM.FaTE Mercury Speciation and Partitioning in Environmental Media Compartments

.... 51
Exhibit 4-10. Summary of Modeled and Observed Concentrations of Total Mercury in Ingestible Media 53
Exhibit 4-11. Estimated Contribution of Modeled Food Types to Divalent Mercury and Methyl Mercury

Ingestion Exposures

............................................................................................................... 54
Exhibit 4-12. Estimated Contribution of Summed Modeled Food Types to Divalent Mercury and Methyl

Mercury Hazard Quotients

..................................................................................................... 54Appendix 5 v

Exhibit 4-13. Summary of Modeled 2,3,7,8-TCDD Concentrations and Observed Total Dioxin TEQ

Concentrations in Environmental Media

................................................................................ 57
Exhibit 4-14. TRIM.FaTE 2,3,7,8-TCDD Concentrations in Fish and Calculated Bioaccumulation Factors

with Respect to Total Water Concentration

........................................................................... 58
Exhibit 4-15. Fraction of 2,3,7,8 - TCDD Mass Sorbed vs. Dissolved in TRIM.FaTE Compartments

....... 59
Exhibit 4-16. Summary of Modeled 2,3,7,8-TCDD Concentrations and Observed Total Dioxin TEQ

Concentrations in Ingestible Media

........................................................................................ 60
Exhibit 4-17. Contribution of Modeled Food Types to 2,3,7,8-TCDD Ingestion Exposures (mg/kg/day)

.. 61
Exhibit 4-18. Summary of Modeled and Observed Concentrations of Benzo[a]pyrene in Environmental

Media

...................................................................................................................................... 64
Exhibit 4-19. TRIM.FaTE Benzo[a]Pyrene Concentrations in Fish and Calculated Bioaccumulation

Factors with Respect to Total Water Concentration

.............................................................. 65
Exhibit 4-20. Fraction of Benzo[a]Pyrene Mass Sorbed vs. Dissolved in TRIM.FaTE Compartments

..... 66
Exhibit 4-21. Summary of Modeled and Observed Concentrations of Benzo[a]pyrene in Ingestible Media

................................................................................................................................................ 67
Exhibit 4-22. Contribution of Modeled Food Types to Benzo[a]pyrene Ingestion Exposures (mg/kg/day) 68Appendix 5 vi 

## EXECUTIVE SUMMARY

This report describes the methods used by EPA to evaluate multipathway exposures to hazardous air pollutants and the associated human health risks. In particular, the report explains the methods, assumptions, and input data used to develop a screening scenario that is used in the first tier of Risk and Technology Review II (RTR II) assessments of such emissions. This report describes the development of the screening scenario and its application in generating qualitative, screening-level estimates of human exposure to PB-HAPs and consequent risk

.
BACKGROUND

The Clean Air Act directs the U.S. Environmental Protection Agency (EPA) to assess theresidual risk from hazardous air pollutants (HAPs) emitted by sources regulated by technologybased standards. To evaluate multipathway exposures and human health risks, a two-tiered approach was developed. In the first tier of the approach, a screening evaluation is conducted that uses the identity and magnitude of HAP emissions from a source to determine whether that source meets certain human health risk-based criteria with respect to multipathway exposures

. The purpose of this first-tier screening is to eliminate facilities from further analysis that pose no unacceptable risk to human health, while identifying those facilities that warrant a second-tier, more refined, site-specific analysis of residual risk.

PURPOSE OF THE SCENARIO

The approach described here for evaluating human multipathway exposures and risks consists of an initial, screening-level tier that can be conducted quickly and efficiently to determine those facilities for which multipathway risks are expected to be below levels of concern. The key component of the first tier of this approach is a multipathway screening scenario based on EPA‘s Total Risk Integrated Methodology (TRIM). The TRIM -based modeling scenario provides a means for quickly and efficiently completing an initial non-inhalation exposure and risk screening analysis of a facility

. The scenario is applied for use in RTR evaluations by calculating screening threshold (also called de minimis) emission rates for selected PB- HAP s that correspond to a cancer risk of 1 in 1 million or a chronic non -cancer hazard quotient (HQ) of 1. These screening threshold emission rates then can be used in the first risk screening step without requiring additional model runs. Sources whose emissions exceed the screening threshold emission rate for any PB-HAP would be subjected to refined evaluation(s) in a second tier analysis.

The scenario has been used to calculate numerical exposure and risk values for 4 of the 14 HAPs that OAQPS has identified as candidates for multipathway risk assessments: cadmium, mercury, dioxins (i.e., chlorinated dibenzo- p -dioxins and -furans), and polycyclic organic matter. These compounds were selected because they are expected, based on current knowledge of relative emissions and toxicity, to pose a substantial share of the non-inhalation risks to humans from air emissions at sources subject to residual risk provisions of the Clean Air Act. The scenario is not intended to be used to produce quantitative estimates of actual or potential risk. Rather, it provides a basis for determining if residual human health risks are of potential concern. Such determinations can then be used to support decisions to proceed with or forego more definitive analyses of non -inhalation exposures to HAPs and the associated risks. The scenario does, however, provide a technically defensible starting point for additional fate and transport and exposure/risk analyses of facility emissions that are not ―screened out‖ in the first tier evaluation.Appendix 5 vii



### OVERVIEW OF SCREENING SCENAR IO

Th is screening scenario is intended to reduce the possibility that EPA will fail to identify unacceptable risks. Thus, the scenario‘s conservative approach most likely overestimates risk, which is appropriate for a screening assessment. Parameter values were defined carefully, and properties having more uncertainty were assigned greater conservative bias to prevent underestimating potential risks. The screening scenario is designed to estimate the upper end of the range of individual, long-term, non-inhalation exposures for situations likely to be encountered in the United States. The result of reviewing a broad range of conditions and selecting values representative of higher exposures in conceptualizing and building the screening tool is that the scenario is unlikely to occur at any one location but has a high likelihood of representing the upper end of any potential exposures.

The screening scenario address es non -inhalation exposures, which can occur through both dermal and ingestion exposure pathways

. Pathways examined include incidental ingestion of soil; ingestion of homegrown produce

, beef , cows‘ milk, poultry and eggs, and pork; ingestion of fish ; and exposure through ingestion of breast milk as an infant (for dioxins only)

. Dermal absorption of chemicals that are originally airborne is generally relatively minor, and this pathway was not included in the scenario used to calculate screening emission thresholds. A highly conservative estimate of dermal exposures and risks was calculated for comparison to ingestion exposures and risks.

For this approach, chemicals were modeled separately to evaluate the potential for risks, with exposures for each PB-HAP summed across all ingestion exposure pathways

. Exposures were modeled for a hypothetical farm homestead and fishable lake near an emissions source. For this setting, exposures were estimated for a hypothetical individual assuming subsistence consumption of all potentially contaminated foodstuffs from the farm or lake. The scenario was purposely designed to produce conservative (i.e., health-protective) results, and certain critical exposure/activity assumptions, such as food ingestion rates, were selected from the upper ends (e.g., the 90 th 

### percentile) of representative exposure parameter distributions. The physical/chemical environment was parameterized with a mix of typical and health-protective values

. The scenario‘s spatial/temporal aspects and the components that influence air concentrations were also chosen so that concentrations in environmental media would not be underestimated given the range of possible settings and meteorological conditions that might be encountered. Properties of the environmental media were parameterized with either typical or conservative values, with a more protective bias introduced for properties having greater uncertainty.

MODELING FRAMEWORK

The approach for risk evaluation of ingestion exposures and risk screening has four components:



### 1. fate and transport modeling of PB-HAPs emitted to air that partition into soil, water, and other environmental media (including fish) ; 

### 2. modeling of transfer and uptake of PB-HAPs by farm food chain media from soil and air; 

### 3. estimating ingestion exposures for the selected media contact scenarios and average daily ingestion doses for a hypothetical human receptor; and 

### 4. c alculating lifetime cancer risk estimates or chronic non-cancer HQs for each HAP

.Appendix 5 viii



### TRIM.FATE SCENARIO CONFIGURATION AND PARAMETERIZATION

To model chemical fate and transport in the environment , EPA‘s Fate, Trans port

, and Ecological Exposure ( TRIM .FaTE ) module of the TRIM system was used

. The physical configuration of the scenario was designed to be generally conservative and the environmental and chemical

specific properties were parameterized with either conser vative or central

- tendency values

. Chemical/physical properties were obtained from peer

- reviewed and standard reference

sources

. The spatial layout represents a farm homestead and a fishable lake near an emissions

source

. The predominant wind direction is toward the farm and lake watershed , and the downwind modeling area is symmetrical around a 10

- kilometer east

- west line and divided into five pairs of parcels

. The aquatic food web in the scenario is meant to represent a generic aquatic ecosystem within a 47

- hectare lake

. Fate and transport modeling outputs include average PB-HAP concentrations and deposition rates for various media (air, soil, surface water, and fish) for each year and for each parcel ofthe model scenario. TRIM.FaTE can output instantaneous chemical concentrations for a userspecified time step and also can be configured to calculate temporal averages. For the screening scenario, the model outputs results on a daily basis, and daily concentration results are averaged to obtain annual average concentrations. The source is assumed to emit for 50
years.

EXPOSURE AND RISK CALCULATIONS

The Multimedia Ingestion Risk Calculator (MIRC) was developed to carry out required farm food chain transfer, ingestion exposure, and risk calculations. Concentrations in farm food chain media are calculated using empirical biotransfer factors (e.g., soil- to -plant factors, which are the ratios of the concentrations in plants to concentrations in soil). Ingestion exposures based on exposure factors, including food-type-specific ingestion rates, are calculated for a hypothetical exposed individual

. Lifetime cancer risks and the potential for chronic non-cancer effects are estimated using chemical-specific ingestion cancer slope factors and reference doses

. Exposure pathways evaluated include incidental ingestion of soil and consumption of fish, produce, and farm animals and related products. Cancer risk estimates and HQ s are calculated separately for each PB-HAP included in an analysis.

CALCULATION OF SCRE ENING EMISSION THRESHOLDS

After the configuration of the TRIM.FaTE and MIRC modeling scenarios was completed, screening-level emission rate thresholds were calculated by conducting iterative model simulations to determine emission rates for cadmium, mercury, dioxins, and polycyclic organic matter that correspond to a cancer risk of 1 in 1 million or a chronic non -cancer hazard quotient (HQ) of 1. Given the generally conservative nature of the scenario inputs, these thresholds are assumed to be appropriate for screening sources emitting these HAPs.

EVALUATION OF SCREENING SCENARIO

Model evaluations serve as an important aspect of environmental risk assessments by illustrating the performance of the model under different conditions and assumptions and facilitating the comparison of model outputs to measurement data and other modeling results. Evaluations thereby provide an opportunity to gain confidence in model performance and identify and better characterize uncertainties associated with model construct and inputs. The screening scenario was analyzed through comparisons to the literature and sensitivity analyses

.Appendix 5 ix



### Outputs from the screening scenario based on screening threshold emission values were compared to literature values for cadmium, mercury, 2,3,7,8-TCDD, and benzo[a]pyrene. In general, taking into account the limitations of this type of comparison, the configuration of the models for screening appear to be reasonable. Chemical partitioning predicted by the model is generally consistent with information on environmental partitioning presented in the literature for media of concern. Where results are not consistent with literature values, a more detailed investigation of underlying assumptions may help to identify means of adjusting the scenario configuration.

Sensitivity analyses were performed to evaluate the influence of model parameters and to provide information on which parameters are likely to be most influential in dictating the uncertainty associated with the results. The sensitivity analyses conducted on the RTR screening modeling scenario encompassed the fate and transport modeling carried out using TRIM.FaTE and the farm food chain and ingestion exposure calculations performed using MIRC. A systematic sensitivity analysis was conducted by varying each input independently and calculating the resulting effect on the risk or hazard quotient estimates in order to rank the variables from most to least sensitive

. The analysis suggests that several TRIM.FaTE variables (including wind speed, mixing height, and emission rate) have a large effect on the risk and hazard estimates. The estimates of hazard and risk are also highly sensitive to key parameters in the primary exposure pathway (i.e., ingestion of food types resulting in the highest exposures) for each PB- HAP . Other analyses performed indicated that accounting for temporal correlations in ingestion rates and body weights and varying the body weight and ingestion rate percentiles used in the model scenario have a limited effect on the risk and hazard estimates. The use of site-specific meteorological variable values (as opposed to the generic screening scenario values) resulted in a decrease in the risk and hazard estimates of approximately one order of magnitude.

In addition, media concentrations estimated using the screening scenario were compared to analogous outputs estimated using site-specific TRIM.FaTE model applications configured for two secondary lead smelting sources. The same emission rates for benzo[a]pyrene, 2,3,7,8- TCDD, elemental mercury

, and divalent mercury were entered into the screening scenario and the site-specific model scenarios. Model results were compared for soil, water, and sediment compartment types. In all media, the screening scenario produced higher concentrations for all chemicals than the site-specific model applications, the expected result given that the screening scenario is conservative (and therefore tends to result in higher media concentrations).

Some of the evaluation results included in this document were presented in August 2009 to an expert panel convened by EPA‘s Science Advisory Board (SAB) for formal review and comment. The Panel determined that the screening approach to PB-HAPs developed by EPA for RTR is suitable and effective for the purposes of residual risk assessment. Specifically, in their final report to EPA transmitting their comments, the Panel concluded that ―...the Agency‘s screening approach is based on an appropriate framework and should usefully screen out sources that do not need a detailed site-specific multi- pathway analysis.‖ Evaluations of TRIM.FaTE and MIRC will continue as additional residual risk assessments are conducted and as the state of the science for evaluating multipathway exposures continues to evolve. Consequently, it is possible (or even likely) that the model configurations used to estimate RTR screening thresholds and conduct site-specific risk assessments will be modified as additional knowledge regarding model performance is acquired.Appendix 5 1



## 1 Introduction

1.1 Background

Section 112(f)(2)(A) of the Clean Air Act (CAA) directs the U.S. Environmental Protection Agency ( EPA ) to assess the risk remaining (residual risk) from hazardous air pollutants (HAPs) that continue to be emitted from sources after application of maximum achievable control technology (MACT) standards under section 112(d) of the CAA. Under these requirements, EPA will promulgate additional emission standards for a source category if the MACT standards do not provide an ―ample margin of safety‖ for human health. One aspect of human health that EPA must consider is the potential for exposures to HAPs via non-inhalation pathways and the risks associated with such exposures.

As described in EPA‘s Risk and Technology Review (RTR) Assessment Plan ( EPA 2006a)

, multipathway human health risks were preliminarily evaluated in 2006

. The evaluation used draft National Emissions Inventory (NEI) data for RTR Phase II (RTR II ) source categories and a simplified multipathway exposure modeling approach (see Appendix 5 in EPA 2006a). 1 

### However, as noted in the RTR Assessment Plan , EPA‘s intention was to develop an approach that would supersede the preliminary methods used in 2006 and involve the use of EPA‘s Total Risk Integrated Methodology (TRIM) , a risk assessment modeling system for air toxics developed by OAQPS. The TRIM system can be used to predict the local impacts of persistent and bioaccumulative HAPs (PB- HAPs ) from an emissions source to estimate associated human health risk.

EPA will implement a two-tiered approach to evaluate multipathway exposures and human health risks for RTR II. In the first tier

, a screening evaluation is conducted that focuses on the identity and magnitude of HAP emissions from a given facility to determine whether a facility
pass es certain human health risk-based criteria. S ources that are ―screened out‖ are assumed to pose no unacceptable risks to human health and are not considered in further analyses

. For sources that do not pass the screen, more refined, site-specific multipathway assessments are conducted as appropriate. These human health risk results are considered, in combination with estimated inhalation human health risks, potential ecological risks, and other factors, to support decisions about residual risk for RTR II source categories.

This current document describes the technical basis for the first, screening-level tier of EPA‘s multipathway human health evaluation of RTR emission sources. Specifically, the models, configurations, and inputs used to derive screening threshold (also called de minimis) emission rates in the first tier of the approach are described in detail here. 2 

### Analyses of the screening scenario conducted to evaluate the scenario‘s defensibility are also discussed . EPA expectsthat refined multipathway risk assessment methods (when required) will rely on the same TRIMbased modeling approach used to derive the screening-level thresholds used in the first screening tier. However, the details of refined assessments will vary depending on the facility location, source category, chemicals emitted, and other parameters, and the specific methods and processes involved in multipathway evaluations beyond the first tier are not explored in depth in this document.

1 The preliminary evaluation conducted in 2006 relied on a simpler modeling approach that did not utilize TRIM and involved a less rigorous analysis of parameter input values.

2 De minimis is a Latin phrase that translates to ―regarding minimal things.‖ In the current context, the term de minimis is used in reference to human health risk that is below a level of concern (or, more specifically, a chemical emission rate that is not expected to result in unacceptable risks). See also the definition for ―risk de minimis ‖ in the

― Glossary for Chemists of Terms Used in Toxicology ‖ (IUPAC 1993).Appendix 5 2



### 1.2 Organization of this Document

Th is do cument presents the methods, assumptions, and inputs used to develop a method for evaluation of human multipathway exposures and health risks for RTR II risk assessments. Section 2 presents an overview of the methods for evaluating multipathway exposures andrisks, a conceptual description of the TRIM-based scenario that is the basis for the screeninglevel emission thresholds, and a brief description of how refined analyses will be conducted for facility emissions that cannot be screened out in the first step. Section 3 presents a technical description of the screening-level, TRIM-based modeling scenario and the configuration of the models used to estimate the screening-threshold levels

. Section 4 discuss es evaluation activities conducted for this screening scenario and summarizes uncertainty

. References cited in this report are listed in Section 5

. 

## 2 Approach for Screening Evaluation of Multipathway Exposures

2.1 Overview

As described above, EPA‘s method for evaluating multipathway exposures for RTR risk assessments consists of a two-tiered process. Exhibit 2-1 diagrams the approach for evaluating

non -inhalation, multipathway exposures to PB-HAPs. The first tier of this approach is the screening evaluation that relies on the TRIM- based ―screening scenario‖ as the technical basis for decisions regarding whether a facility passes the screen. Air toxics emitted by a source under consideration are reviewed to determine first whether emissions of any PB -HAPs are reported. If such emissions are reported, the emission rates are compared to available threshold-screening emission levels that have been derived using the TRIM-based screening scenario. 3 

### Th e list of chemicals that are PB-HAPs is discussed in Section 2.2 , and the use of screening-level emission thresholds is discussed in Section 2.3

. The TRIM-based multipathway modeling configuration, referred to in this document as the ―screening scenario,‖ is a key component of the first tier of this approach, as this modeling application is the technical basis for determining the levels of PB- HAP screening-level emission thresholds. The term ―screening scenario‖ is used in this document to refer collectively to the specific TRIM.FaTE and exposure modeling configuration described here, including the set of assumptions and input values associated with a hypothetical watershed and the exposure and risk scenarios evaluated for this watershed. The screening scenario is a static configuration

, and its primary purpose is as a modeling tool to calculate the screening-level emission rates for PB -HAPs of concern. Descriptions of the components of the screening scenario are presented in Section 2.4

. The two potential outcomes of the screening human health evaluation are:

N on -inhalation exposures are unlikely to pose a human health problem; or The potential for unacceptable non- in halation exposures cannot be ruled out and further assessment is required to determine the potential for unacceptable risk.

An ideal screening approach strikes a balance between being conservative

– to ensure that unacceptable risks are identified

, and being accurate

, to minimize results suggesting that additional assessment is required when in fact the actual risk is low. Typically, gains in

3 As described later in this report, to date, TRIM-based modeling has been used to calculate screening threshold emission rates only for those PB-HAPs considered as those of highest concern.Appendix 5 3



### accuracy in environmental modeling are accompanied by additional resource requirements. Stated another way, a suitable approach minimizes both false negatives and false positives

. False negatives (i.e., results that suggest that the risk is acceptable when in fact the actual risk is high) can lead to inappropriate and non-protective health or environmental policy decisions

. False positives (i.e., results that suggest more assessment is required when in fact the actual risk is low) can result in wasted resources by leading to additional, unnecessary analysis

. For the evaluation of multipathway human health exposures to PB-HAPs, the methods for screening described in this document are intended to achieve this balance.

Facilities whose emissions exceed the established screening threshold emission rate for any PB

- HAP would be subjected to more refined evaluations. Be cause the initial screening evaluation enables EPA to confidently eliminate from consideration those facilities where risks from non-inhalation exposures are projected to be minimal, resources can be target ed to ward th os e facilities that do not ―pass‖ the screening test. An overview of the anticipated approach to refined evaluation is described in Section 2.5

.


### 2.2 Chemicals of Potential Concern

EPA‘s a ssessment of multipathway human exposures for RTR focuses on PB-HAPs that OAQPS has identified as candidates for multipathway risk assessments. OAQPS developed a list of 14 chemicals and chemical groups that are PB-HAPs based on a two-step process taking into account the following:

their presence on three existing EPA lists of persistent, bioaccumulative, and toxic substances, and a semi-quantitative ranking of toxicity and bioaccumulation potential of the entire list of HAPs

.

The list‘s development and utility in hazard identification for multipathway risk assessment are further e xplained in Chapter 14 and Appendix D of Volume I of EPA‘s Air Toxics Risk Assessment (ATRA) Reference Library (EPA 2004a). Exhibit 2-2 presents the 14 chemicals and groups that are PB- HAPs

. The screening scenario described in this document is not configured for evaluating the risk potential for all 14 PB -HAPs on the list. Currently, the scenario can be used to quantitatively estimate exposures and risks for four PB -HAP compounds (indicated in bold in Exhibit 2-2 ). These compounds are the focus of the current scenario because, based on current emissions and toxicity considerations, they are expected to pose the vast majority of the non-inhalation risks to humans from air emissions at sources subject to residual risk provisions of the CAA. 4

4 Potential impacts on human health from non-inhalation exposures to lead are evaluated for RTR using the National Ambient Air Quality Standard for lead, which takes into account multipathway risks. Non-inhalation exposures to the other nine PB-HAPs not addressed by the modeling scenario discussed in this report will be evaluated on an indi vidual facility or source category basis as needed.Appendix 5 4 

### Exhibit 2

- 1

. Conceptual Decision Tree for Evaluation of Non

- Inhalation Exposures of PB

- HAPsAppendix 5 5 

### Exhibit 2

- 2

. OAQPS PB

- HAP Compounds a

PB

- HAP Compound Addressed by Screening Scenario? Cadmium compounds Yes
Chlordane No
Chlorinated dibenzodioxins and furans Yes

DDE No Heptachlor No

Hexachlorobenzene No Hexachlorocyclohexane (all isomers) No Lead compounds No
Mer cury compounds Yes Methoxychlor No Polychlorinated biphenyls No Polycyclic organic matter (POM) Yes Toxaphene No
Trifluralin No

a Source of list: EPA 2004a

. Compounds in bold text can be evaluated using the current version of the TRIM

- based screeni ng scenario.



### 2.3 Use of Screening Threshold Emission Levels

The multipathway screening evaluation for RTR compares reported air emission rates of PBHAPs (summed by PB-HAP for each facility) to screening threshold emission rates derived using the screening scenario described here. A screening threshold emission rate is the level that, when input to a risk model that uses emissions as a parameter, corresponds to a specified cancer risk or non-cancer HQ that, for the purposes of the evaluation being conducted, is assumed to be below a level of concern. Threshold rates were calculated for the screening scenario for a cancer risk of 1 in 1 million or an HQ of 1.0 ( Exhibit 2-3 ). 5 

### Conceptually, athreshold level for the RTR multipathway screening evaluation could be obtained by backcalculating the emission rate that results in the specified cancer risk or HQ level, taking into account the exposure and fate and transport calculations included in the model. Because the models used in this assessment are not designed to run ―backwards,‖ t hese rates were derived from regression equations established following a series of TRIM.FaTE and exposure/risk model runs spanning a wide range of emission rates for each chemical.

The more probable risk for each emission rate would be lower than the level corresponding to the screening threshold risk quantities in nearly all circumstances given the conservative and highly general nature of the screening scenario configuration. This conservatism ensures th at a facility with cancer risk greater than 1 in 1 million or a chronic HQ greater than 1.0 is very

un likely to be omitted from refined evaluation.

5 For chemicals that are known to cause both cancer and chronic non-cancer impacts, and for which acceptable quantitative dose-response values are available for both cancer and non-cancer endpoints, the endpoint that results in the lower threshold emission level will be used for screening (i.e., the threshold will be based on the effect that occurs at the lower exposure level). For the set of PB-HAPs for which screening threshold levels have been derived, only chlorinated dibenzo-dioxins and -furans meet both of these criteria. Because the cancer dose-response value is lower than that for non-cancer effects, the screening threshold value is based on the cancer endpoint.Appendix 5 6



### Exhibit 2

- 3

. Emission Thresholds for Screening of Multipat hway Exposures

Chemical Screening Threshold Emission Rate (TPY) Basis of Threshold (Type of Health Endpoint)
POM (as Benzo[a] pyrene toxic equivalents) 3.60E

- 04 Cancer Dioxins (as 2,3,7,8

- TCDD TEQ) 9.18E

- 10 Cancer Divalent Mercury 1.95E

- 0 3 Non

- c ancer
Cadmium 3.51E

- 02 Non

- c ancer
T PY = U.S. short tons per year



### Evaluation of Chemical Groups

In the screening evaluation, emissions of PB-HAPs are summed by chemical group for each facility

. The summed emission rates for each group are then compared to th e emission screening threshold corresponding to the appropriate chemical.

Emissions of polycyclic organic matter (POM, a HAP chemical group that includes polyaromatic hydrocarbons or PAHs) are often reported in NEI as unspeciated or partially speciated groups (such as ―total PAHs‖ or ―16

- PAH‖) rather than as specific PAH compounds . In addition, quantitative data are lacking for some POM compounds and groups that are suspected carcinogens. To evaluate risks associated with exposure to emissions of the various POM species, EPA has grouped each POM species included in NEI into categories and then defined

a cancer slope factor (CSF) for each group that can be used to estimate lifetime cancer risks. The CSFs used to evaluate risk for emissions of POM compounds and groups are listed in Attachment 2.

Similarly, polychlorinated dioxins and furans are reported in NEI as individual congeners, congener groups, or as toxic equivalents (TEQs) that are scaled relative to the toxicity of 2,3,7,8-TCDD. To evaluate cancer risks and non-cancer hazards from these compounds, EPA has developed CSFs and reference doses (RfDs) that apply to congener groups. These values are also presented in Attachment 2.

In the development of the RTR screening thresholds, we determined the threshold levels for one compound from each of the POM and dioxin groups (i.e., benzo[a]pyrene and 2,3,7,8-TCDD). Then, to use this screening threshold in an evaluation of facility emissions of POMs or dioxins, a toxicity-weighted emissions sum is calculated for each group using the toxicity of each modeled chemical

– benzo[a]pyrene and 2,3,7,8-TCDD

– to scale the total POM or dioxin group emissions. This approach avoids the need to develop threshold emission rates for every POM and dioxin congener (some of which are not included in the existing TRIM.FaTE algorithm library)

. A consequence of this approach is that benzo[a]pyrene and 2,3,7,8-TCDD serve as fate and transport surrogates. That is, the behavior of these two compounds is assumed toadequately represent the behavior of all other compounds included in the POM and dioxin PBHAP groups, respectively

. Screening emission thresholds were developed individually for elemental and divalent mercury. Both were based on the lower of the thresholds associated with multipathway exposures to divalent mercury and methyl mercury. 6 

### However, only speciated emissions of divalent mercury

6 Note that TRIM.FaTE models the tr ansformation of mercury within the environment; thus, emissions of only divalent mercury will result in multipathway exposures to both elemental and methyl mercury also. Emissions of only elemental mercury will result in multipathway exposures to both divalent and methyl mercury also.Appendix 5 7



### are screened because the sum of elemental mercury emissions across all NEI facilities is less than the elemental mercury screening threshold level.



### 2.4 The TRIM-Based Screening Scenario: Basis for Threshold Emission Rates

The TRIM-based modeling screening scenario described in this document was used to provide

a means to qualitatively estimate the potential for unacceptable non-inhalation risks for PBHAPs emissions from facilities in the context of residual risk assessments conducted as part of RTR II. The screening scenario used to derive screening threshold emission rates is not intended to be representative of any particular situation. Rather, it was developed for the purpose of RTR to portray an exposure scenario at least as conservative as any situation that might plausibly be encountered in the United States. The range of conditions considered when conceptualizing and building the screening scenario was chosen so that any given individual

, long-term exposure condition for a given geographic region would be reasonably likely to be captured. These criteria were met by constructing a hypothetical scenario that would be protective in key aspects, including spatial orientation, meteorology, types of exposures, and ingestion rates. The overall result is a scenario that is unlikely to occur at any one location but has a high likelihood of representing the upper end of all potential exposures. This latter aspect accomplishes the goal of striking a balance between conservatism and accuracy called for in the ideal screening approach.

For this approach, exposures were modeled for a hypothetical farm homestead and fishable lake near an emissions source. The hypothetical individual exposed to PB-HAPs in this scenario was assumed to derive all potentially contaminated foodstuffs from the farm or lake. Many of the exposure/activity assumptions were selected from the upper ends of representative exposure parameter distributions. The physical/chemical environment was parameterized with a mix of typical values (such as national averages) and health-protective values (i.e., values that would tend to overestimate concentrations in media). The spatial and temporal aspects of the scenario and the components of the scenario that influence air concentrations were chosen from the upper ends of their possible ranges so that concentrations in the environmental media would not be underestimated given the wide range of possible settings and meteorological conditions that might be encountered. Chemical-specific and non-chemical-specific properties of the environmental media were parameterized with either typical or conservative values (with a greater conservative bias introduced for properties having greater uncertainty)

. The development and application of the screening scenario for residual risk evaluations considered EPA‘s technical and policy guidelines presented in the R esidual Risk Report to Congress

(EPA 1999); Volumes I and II of the Air Toxics Risk Assessment Reference Library (EPA 2004a, 2005); and other EPA publications. The scenario described in this document is the culmination of analyses completed over the past 5 years; it provides the basis for an efficient and scientifically defensible method for screening multipathway human health risk and is a solid foundation for conducting more refined analyses when necessary

. Nevertheless, this scenario should not be considered ―final‖ but rather a product that can continue to evolve based on feedback from the scientific community and Agency reviewers, lessons learned as the scenario is further applied for RTR, variations in EPA‘s needs and requirements, and other factors.

2.4.1 Exposure Routes Evaluated

The screening scenario is intended to address non-inhalation exposures (inhalation exposures are being evaluated separately for RTR II using a dispersion modeling approach to estimateAppendix 5 8



### ambient air concentrations). The quantitative aspects of this non-inhalation screening evaluation for human exposures focus primarily on human exposures via the following ingestion pathways:

Incidental ingestion of soil, Ingestion of homegrown produce, Ingestion of homegrown beef, Ingestion of milk from homegrown cows, Ingestion of homegrown poultry and eggs, Ingestion of homegrown pork, Ingestion of fish, and Ingestion of breast milk (for children less than 1 yr old and for dioxins only).

Non-inhalation exposure to PB-HAPs also can occur by way of the dermal pathway (e.g., th rough incidental contact with PB

- HAP -contaminated soil). However, dermal absorption of chemicals that are originally airborne is generally a relatively minor pathway of exposure compared to other exposure pathways (EPA 2006, CalEPA 2000). The risk from dermal exposure in the environmental setting from airborne toxicants is expected to be a fraction of the risk from inhalation exposure or exposure via ingestion of contaminated crops, soil, or breast milk, for example (CalEPA 2000)

. Preliminary calculations of estimated dermal exposures and risk of PB- HAP s , presented in Section 3.2.4

, showed that the dermal exposure route is not a significant risk pathway relative to ingestion exposures. Assessment of dermal exposure through incidental contact with soil could be conducted on facilities that require refined evaluation following the screening evaluation if deemed necessary. Procedures for estimating dermal absorption from soil would be based on EPA‘s dermal exposure assessment pr inciples and applications (EPA1992b) and EPA‘s Superfund Human Health Evaluation M anual (EPA 2004 c).

One other n on -inhalation exposure route discussed in ATRA Volume I of possible concern for PB -HAPs is ingestion of drinking water from surface water sources. This exposure route, however, is not evaluated in the current assessment. The drinking water exposure pathway is not likely for the modeling scenario developed for th is analysis because the likelihood that humans would use a lake as a drinking water source was assumed to be low. 7



### 2.4.2 Approach to Configuration and Parameterization

Th is screening scenario is intended to reduce the possibility that EPA would not mis-identify unacceptable risks. Although the ―conservative‖ approach likely overestimates risk, EPA determined that conservatism is appropriate for the purposes of screening assessments . As in the preliminary multipathway screening for RTR conducted in 2006 (EPA 2006a), exposures were modeled for a hypothetical farm homestead and fishable lake located adjacent to an emissions source. The hypothetical individual for which exposures were calculated was assumed to derive all potentially contaminated foodstuffs from these adjacent locations, and many of the exposure/activity assumptions (e.g., amount of food consumed per day) were selected from the upper ends of representative exposure parameter distributions.

The physical/chemical environment represented in the screening scenario was parameterized with two types of values. One type is typical values

, such as national averages. The second

7 An exception to this generality would be reservoirs used for drinking water supplies. This situation may be worthy of additional analysis, if warranted by the characteristics of a given assessment (e.g., to estimate PB-H AP concentrations in treated drinking water derived from reservoirs).Appendix 5 9



### type is health-protective, conservative values

, or values that would tend to overestimate concentrations in media driving ingestion exposures for humans, based on knowledge of exposure patterns. In general, the spatial and temporal aspects of the scenario and the components of the scenario that influence air concentrations and deposition rates (which in turn affect all other exposures) were defined to be relatively conservative

. That is, they were chosen from the upper ends of their respective possible ranges so that the wide range of possiblephysical settings and meteorological conditions would be captured. Chemical-specific and nonchemical-specific properties of the environmental media were parameterized with either typical or conservative values; properties having greater uncertainty were assigned greater conservative bias

. The spatial layout of the scenario and the meteorological data (or a combination of these two factors) are generally more influentia l than physical/chemical parameters in dictating the screening model outcomes, taking into account the potential range of variation in possible values

. For example, where and how the layout is spatially oriented relative to the dominant wind direction can dramatically affect the concentrations in air, thereby driving estimated concentrations of PB-HAPs in soil, water, and biota. In contrast, a relatively large change in soil characteristics within the range of possible values (e.g., organic carbon content, water content) might result in relatively small changes in outputs.

The mix of conservative and typical approaches and values is expected to result in a scenario configuration that, on average, is likely to over-predict environmental concentrations of PB

HAPs in media of interest for this evaluation. Given the intended application of this scenario as a screening tool

, this conservative bias was deliberate, because of the desire to ensure that unacceptable risks are not overlooked (i.e., to minimize false negatives). Although the inclusion of typical values where warranted is intended to minimize the number of false positives

, some false positives are to be expected from a screening scenario. These false positives would be addressed in iterations of the refined evaluation for a particular source.

2.4.3 Modeling Framework

The approach for risk screening (and ingestion exposure ) evaluation described here can be divided into four steps:

1. Fate and transport modeling of PB-HAPs emitted to air by the source that partition into soil, water, and other environmental media (including fish); 8



### 2. Modeling of transfer and uptake of PB

- HAP s into farm food chain media (produce, livestock, dairy products) from soil and air ;

3. Estimating ingestion exposures as a result of contact with the various selected media and estimating average daily ingestion doses for a hypothetical human receptor; and

4. Calculating lifetime cancer risk estimates or chronic non-cancer H Qs , as appropriate, for each PB -HAP and comparing these metrics to selected risk management points of departure used in the RTR II.

8 As discussed below, concentrations in fish calculated by the TRIM.FaTE model were used in the current approach to estimate ingestion exposures for humans consuming fish. Modeling of fish concentrations is therefore discussed in this document as part of the fate and transport modeling. Uptake of PB-HAPs into all other biotic media assumed to be ingested is modeled in the second step.Appendix 5 10



### The relationship among these four processes is shown in Exhibit 2-4

.
EPA‘s TRIM methodology was conceived as a comprehensive modeling framework for evaluating risks from air toxics, and the TRIM system was designed to address each of the four steps involved in screening ingestion risk. 9 

### Currently, however, only one component corresponding to the first step included in Exhibit 2-4

– the fate and transport module

– is available for application in an ingestion risk assessment. EPA has completed some development activities for TRIM.Expo-Ingestion and TRIM.Risk-Human Health, two additional modules that cover the other three steps. Modeling software, however, is not currently available for these modules. For the RTR screening scenario, the Multimedia Ingestion Risk Calculator (MIRC), a Microsoft Access-based computer framework, was constructed to complete the calculations required for estimating PB-HAP concentrations in farm food chain media, average daily ingestion doses, and cancer risks and chronic non-cancer HQs. This framework is conceptually identical to the ingestion exposure and risk analyses that TRIM is intended to

cover.

2.4.3.1 Fate and Transport Modeling

The fate and transport modeling step depicted in the first box in Exhibit 2-4 is implemented for RTR using the Fate, Transport, and Ecological Exposure module of the TRIM modeling system (TRIM.FaTE). 10 

### In developing th e screening scenario, V ersion 3.6.2 of TRIM.FaTE was used to

9 Information regarding the current status of TRIM modules as well as comprehensive documentation of modules that have been developed thus far can be accessed on EPA‘s Technology Transfer Network (TTN) on the Fate, Exposure, and Risk Analysis web site ( http://www.epa.gov/ttn/fera/ ).

10 TRIM.FaTE is a spatially explicit, compartmental mass balance model that describes the movement and transformation of pollutants over time, through a user-defined, bounded system that includes both biotic and abiotic compartments. Outputs include pollutant concentrations in multiple environmental media and biota, which provide exposure estimates for ecological receptors (i.e., plants and animals)

. The output concentrations from TRIM.FaTE are also intended to be used as inputs to a human ingestion exposure model to estimate human exposures

. Significant features of TRIM.FaTE include: (1) a fully coupled multimedia model; (2) user flexibility in defining scenarios, in terms of the links among compartments, and number and types of compartments, as appropriate for the application spatial and temporal scale; (3) transparent, user-accessible algorithm and input library that allows the user to review and modify how environmental transfer and transformation processes are modeled; (4) a full accounting of 

### E xhibit 2

- 4

. Overview of Ingestion Exposure and Risk Screening Evaluation MethodAppendix 5 11



### model the fate and transport of emitted PB -HAPs and to estimate HAP concentrations in relevant media. Additional information about TRIM.FaTE, including support documentation, software, and the TRIM.FaTE public reference library, is available on EPA ‘s TTN at http://www.epa.gov/ttn/fera/

. The algorithms used to model mercury species and PAHs are described in Volume II of the TRIM.FaTE Technical Support Document (EPA 2002a). A comprehensive evaluation of the performance of TRIM.FaTE for modeling mercury was documented in Volumes I and II of the T RIM.FaTE Evaluation Report (EPA 2002b, 2005b). Algorithms specific to the fate and transport of 14 chlorinated dibenzo-dioxin and -f ur an congeners were added following the addition of those for mercury and PAHs. Documentation of the application of TRIM.FaTE for dioxin emissions is contained in the third volume of the TRIM.FaTE Evaluation Report (EPA 2004 b). Parameterization of the TRIM.FaTE library used for RTR analyses with regard to dioxins is identical to the configuration described in that third evaluation report. More recently (largely as part of th is current project)

, the TRIM.FaTE public reference library has been updated to include information on modeling for cadmium

. In general, many of the algorithms and properties included in the public reference library that are used to model mercury (except for the mercury transformation algorithms) are also applicable to cadmium. Comprehensive technical documentation of TRIM.FaTE algorithms specific to cadmium has not yet been compiled; however, all chemical-specific properties used by TRIM.FaTE to model cadmium (as well as PAHs, mercury, and dioxins) are documented in Attachment 1 to this document. Parameterization of the TRIM.FaTE scenario used for RTR screening is described in more detail in Section 3

. 2.4.3.2 Exposure Modeling and Risk Characterization

The algorithms included in MIRC that calculate chemical concentrations in farm food chain media and ingestion exposures for hypothetical individuals were generally obtained from EPA‘s Human Health Risk Assessment Protocol for Hazardous Waste Combustion Facilities, or HHRAP (EPA 2005a). 11 

### These algorithms, and the required exposure factors and other parameter values, were compiled into a database. An overview of the computational processes this tool carries out and the types of input data it requires is presented in Exhibit 2-5 . This exhibit demonstrates the general relationships between the relevant TRIM.FaTE outputs (i.e., chemical concentrations in environmental media and fish) and the ingestion exposure and risk calculations carried out using MIRC. Additional discussion of exposure and risk calculations for this screening scenario is presented in Section 3.2 and Attachment 2, and all inputs required by these calculations are documented in Attachment 2.

all of the pollutant as it moves among environmental compartments during simulation; (5) an embedded procedure to characterize uncertainty and variability; and (6) the capability to provide exposure estimates for ecological receptors.

11 The farm food chain calculations and ingestion exposure equations to be included in the TRIM.Expo software are expected to be very similar to those included in HHRAP.Appendix 5 12



### Exhibit 2

- 5

. Overview of Process Carried Out in the Multimedia Ingestion Risk Calculato r



### 2.5 Refined Analyses

For facilities that are not screened out by comparison to the screening emission thresholds, additional analysis is required to evaluate the risks via multipathway exposures. EPA envisions that the screening scenario provides a technically defensible ―starting point‖ for additional fate and transport and exposure/risk analyses, by substituting site-specific values for key parameters used in the modeling scenario. As appropriate, the scenario can be further refined in iterative

s teps until either the risks predicted are not of concern or sufficient information has been gathered to inform a risk management decision. Based on the model performance evaluations completed on the screening scenario, settings and parameters that might be appropriate for revision in a more refined analysis include meteorological inputs and spatial configuration assumed for TRIM.FaTE modeling, relevant ingestion exposure scenarios (based on surrounding land-use or other characteristics), and exposure factors such as ingestion rate for individual food types, among other inputs. The refined evaluation could eventually involve developing a site-specific TRIM.FaTE application that incorporat es significant site-specific data (e.g., a model application that includes a site-specific spatial layout taking into account local geographic features and environmental parameter values selected from the best available data for that location).


## 3 Description of Modeling Scenario

3.1 TRIM.FaTE Scenario Configuration and Parameterization

As described in Section 2.4.2 , the physical configuration of the RTR Screening Scenario was designed to be generally conservative, and the environmental and chemical-specific properties were parameterized with either conservative or central-tendency values

. Information regarding the scenario configuration and important aspects of the parameterization process, justifications for selecting particular property values, and model uncertainties is presented in the sections thatAppendix 5 13



### follow

. Comprehensive documentation of TRIM.FaTE property values for this scenario is provided in Attachment 1.

3.1.1 Chemical Properties

The chemical/physical properties that TRIM.FaTE requires , such as Henry‘s law constant, molecular weight , and other ―general‖ parameters, were obtained from peer -reviewed and standard reference sources. Numerous other chemical-specific properties are related more specifically to a particular abiotic or biotic compartment type; these properties are discussed generally in the sections that follow and are documented in Attachment 1.

3.1.2 Spatial Layout

For the purpose of estimating media concentrations, the TRIM.FaTE scenario is intended to represent a farm homestead and a fishable lake (and its surrounding watershed) located near the emissions source of interest. A diagram of the surface parcel layout is presented in Exhibit 3-1 . The source parcel is parameterized as a square with sides of 250 m, which is assumed to be a fair estimation for the size of a relatively small- to -medium facility at the fence line. With a predominant wind direction toward the east, the modeled layout is generally symmetric about an east-west line and is wedge-shaped to reflect Gaussian dispersion of the emission plume.

Exhibit 3

- 1

. TRIM.FaTE Surface Parcel Layout

A lateral, downwind distance of 10 km was established for the watershed included in the scenario. Based on the results of dispersion modeling (results not presented here), the location of the maximum air concentration and deposition rate would be expected to occur relatively close to the facility (probably within a few hundred meters

, with the exact location varying with stack height and other parameters) and well within a 10-km radius. Additionally, deposition rates for the PB-HAPs for which this screening scenario is applicable would be expected to decrease by about two orders of magnitude relative to the predicted maximum rate within a 10 -km radius. Extending the modeling layout beyond a 10-km downwind distance would increase the amount of deposition ―captured‖ by the modeled watershed, but the incremental chemical mass expected to accumulate in the watershed diminishes rapidly with distance. I n addition, the impact of this additional deposited mass on ingestion exposures is expected to beAppendix 5 14



### negligible. 12 

### Given these conditions, a downwind length of 10 km was determined to be appropriate for the screening scenario.

The north-south width of the wed ge -shaped watershed was set based on the observed behavior of chemicals emitted to the ambient air. If meteorological stability is known or can be assumed, the lateral spread of the plume (σ y 

### , measured from the centerline) at a certain distance from the source can be estimated using the Pasquill-Gifford curves. Turner (1970) derived t he equations for these curves, which can be found in the ISC3 Dispersion Model Manual (among other sources). 13 

### For a relatively neutral atmosphere (stability cl ass D), σ at 10 km is about 550 m using this estimation. In a Gaussian distribution, about 99.6 percent of the plume spread area is contained within 3σ of the median line . Therefore, the plume σ was set at 3 times 550 m , or approximately 1.75 km from the centerline at 10 km distance. T he plume width for these conditions is expected to be about twice this distance, or 3.5 km. These dimensions were used to define the dimensions of the overall air and surface parcel layouts for the screening scenario.

The surface (land and surface water) modeling area was initially divided into five pairs of parcels whose areas increase with distance from the source, which approximately corresponds to the spatial gradient that is expected in the downwind direction from the source. The second north parcel from the source was further divided into two parts, one of them tilled soil (Parcel N6) to represent agricultural conditions.

The depth of the surface soil compartments was set to 1 centimeter (cm), except for Parcel N6, for which the depth was set to 20 cm to simulate the effect of tillage. Characteristics of the soil layers (e.g., organic carbon content, air and water content, and sub-soil depth) were typically set to represent typical or national averages as summarized by McKone et al. (2001), for example.

Initial considerations when the layout was configured included the presence of a stream that ran along the bisecting east-west line from the southwestern corner of Parcel N3 through the eastern edge of the layout. In that configuration, the eastern extent of the pond was restricted by a parcel ( S3 ) directly south of Parcel N3 . The stream received chemical mass from Parcel s S3, S4, and S5 and flowed directly into the pond. Preliminary modeling runs showed that the existence of a stream somewhat decreased the concentrations of 2,3,7,8-TCDD in the pond parcel and significantly decreased concentrations in Parcels S3 and S4. Th ese results indicated that the pond was receiving more 2,3,7,8-TCDD mass through surface soil transfer than through the stream, perhaps due to a chemical sink into stream sediment. Given the goal of creating a conservative scenario, a stream was not included in the final layout.

The overall shape and boundaries of the air parcel layout mirror th os e of the surface parcel layout

. A single air parcel (N2) overl ie s surface Parcels N6 and N7, and the air over the lake is divided into air Parcels S2 and S3 (mirroring the analogous parcels on the north side of the lake).

12 Mass deposited at the outer edge of the watershed is expected to result in only a very small increase in estimated exposure via fish consumption by increasing the chemical mass transported to the lake through erosion and runoff. The distance from these more distant locations to the lake would attenuate transport of chemical mass by erosion and runoff, dampening the effect of including additional deposition beyond 10 km. (Other exposure pathways would be largely unaffected; the soil concentrations used to calculate exposures for the farm food scenario are derived from soil parcels located close to the source and unaffected by deposition to the far reaches of the watershed.)

13 http://www.epa.gov/scram001/userg/regmod/isc3v2.pdfAppendix 5 15



### 3.1.3 Watershed and Water Body Parameterization

Properties associated with the watershed soil and lake determine how pollutants in the system are transported through and accumulate in various compartments. These properties describe the physical characteristics of the environmental media included in the modeled region, as well as the assumed connections and relationships between media types and modeled spatial components that in turn affect chemical transport via water runoff, ground seepage, deposition of suspended sediments in the water column, and other processes. This section presents the justification for setting the key properties of the soil, water, and sediment compartments. Also discussed are some of the chemical properties related to watershed and waterbody processes (chemical-specific compartment properties in TRIM.FaTE) and the configuration of terrestrial plants included in the scenario.

3.1.3.1 Water Balance

Water-related properties of the lake and related watershed characteristics (e.g., runoff rates from each surface soil compartment) were set so that a simplified water balance is achieved. Although TRIM.FaTE maintains a chemical mass balance, the model does not calculate or maintain media mass balances (e.g., for water) except where specified in certain formulas. For the screening scenario, the parameters were set to satisfy two equations relating water volume. The first equation maintains a balance of water entering and leaving the terrestrial portion of the scenario:

[ total precipitation] = [evapotranspiration] + [total runoff]

In this equation, total runoff is equal to the sum of overland runoff to the lake and seepage to the lake via groundwater.

The second equation describes the volumetric balance of transfers of water to and from the lake:

[total runoff] + [direct precipitation to the lake] = [evaporation from the lake surface] + [outflow from the lake]

Note that TRIM.FaTE actually uses only some of these properties (e.g., precipitation rate and

s urface runoff, but not evapotranspiration). The water characteristics assumed for the screening scenario are meant to represent a relatively wet and moderately warm location in the United States (USGS 1987). Following are the assumptions for this scenari o:

35 percent of the total precipitation leaves the scenario through evapotranspiration. 65 percent of total precipitation remains in the modeled system and contributes to total runoff. Total runoff is divided between overland runoff and seepage to groundwater as follows:

o 40 percent of total precipitation contributes to overland runoff.

o 25 percent of total precipitation seeps into the groundwater and eventually flows into the lake.

For these calculations, the source parcel was considered to be outside the watershed and therefore was not included in the water balance. The evaporation rate from the lake was assumed to be 700 millimeters per year (mm/yr) based on data reported by Morton (1986) for various lakes. This estimate is probably more representative of cooler locations [by comparison, the overall average of evaporation rates from various reservoirs is reported byAppendix 5 16



### McKone et al. (2001) to be close to 1,200 mm/yr]. The runoff rate was defined to be spatially constant and temporally constant (i.e., it is not linked to precipitation events) throughout the modeled domain. Based on these assumptions, the outflow of water from the lake is about 18 million m 3 

### /yr, which translates to a volumetric turnover rate of about 12.2 lake volumes per year.

Other quantitative water body and watershed characteristics TRIM.FaTE uses are listed in Attachment 1.

3.1.3.2 Sediment Balance

A simplified balance of sediment transfers between the watershed and the lake was also maintained for the screening scenario via the parameterization of sediment-related properties. As with water, the model does not internally balance sediment mass; these calculations were performed externally for the purposes of setting parameter values

. The sediment balance maintained is described by the following equation, where terms represent mass of sediment:

[total surface soil transfers to the lake via erosion] = [removal of sediment from the water column via outflow] + [sediment burial]

where the second term (removal of sediment from the water column via outflow) is accounted for in TRIM.FaTE by lake flushing rate and the third term (sediment burial) is the transfer of sediment from the unconsolidated benthic sediment compartment to the consolidated sediment layer

. To maintain the sediment balance, erosion rates were calculated for each surface soil compartment using the universal soil loss equation (Wischmeier and Smith 1978), assuming a relatively high rate of erosion

. The total suspended sediment concentration is assumed to remain constant in TRIM.FaTE, and the flush rate of the lake (calculated via the water balance approach described above) w as then used to estimate the removal of sediment from the modeling domain via lake water outflow

. The difference between these sediment fluxes was taken to be the sediment burial rate. The sediment burial rate is the rate at which sediment particles in the unconsolidated benthic sediment layer are transported to the consolidated sediment, where the particles can no longer freely interact with the water column.

In TRIM.FaTE, the consolidated sediment layer is represented with a sediment sink; as with all sinks in TRIM.FaTE, chemical mass sorbed to buried sediment that is transported to the sink cannot be returned to the modeling domain. The burial rate is a formula property calculated by the model according to the difference between user-specified values for sediment deposition velocity (from the water column to the benthic sediment) and sediment resuspension velocity (back into the water column from the benthic sediments). These formula properties assume a constant volume of particles in the sediment layer (because the densities for benthic and suspended sediment particles were defined to the same value, the mass of particles in the sediment is also constant).

For the screening scenario described here, the average sediment delivery rate (i.e., transfer of sediment mass from watershed surface soil to the lake due to erosion ) for the entire watershed was estimated to be about 0. 0036 kilograms per square meter per day (kg/m 2



### - day ), based on calculations using the universal soil loss equation (USLE). The HHRAP documentation notes that using the USLE to calculate sediment load to a lake from the surrounding watershed sometimes leads to overestimates (EPA 2005 a) . For th is screening scenario, however, this approach was considered to be appropriate in that conservatism is a goal of the screeningAppendix 5 17



### scenario. 14 

### Surface soil compartments adjacent to the lake are linked directly to the lake for the purposes of estimating erosion and runoff transfers (see layout in Exhibit 3-1 ). Erosion and runoff from the source parcel are linked directly to a sink and do not enter the screening scenario lake. The transport of sediment to the lake via overland flow (e.g., by streams) is thus assumed to be efficient. Note that erosion from parcels not directly adjacent to the lake is assumed to be somewhat attenuated, effected by using a lower sediment delivery ratio in the model.

Using the calculated surface soil erosion rates for the scenario, the total average daily sediment load to the lake from the watershed is about 16 ,600 kg/day. About 15 percent of this load is removed from the lake via outflow of suspended sediments (based on a calculated flush rate of 12.2 volume turnovers per year), with the remainder of the sediment input to the lake transferred to the sediment burial sink.

3.1.4 Meteorology

Meteorological properties used in TRIM.FaTE algorithms include air temperature, mixing height, wind speed and direction, and precipitation rate. These properties, which can vary significantly among geographic locations, as well as seasonally and hourly for a single location, greatly influence the chemical concentrations predicted in media of interest. Because the screening scenario is intended to be generally applicable for any U.S. location, and to minimize the frequency of false negatives

, a conservative configuration was used

. Th e meteorology of the screening scenario was defined to ensure that (when used in combination with the selected spatial layout) the maximum exposures that might be encountered for the scenarios of interest would be encompassed (i.e., consumption of home-grown farm foodstuffs and self-caught fish, with all farm foods and fish obtained from locations impacted by chemicals emitted from the local source). However, ensuring that the meteorological parameters were not overly conservative

, such as always having the wind blow toward the location of interest, was also important to avoid too many false positives.

The meteorological data for the screening scenario are intended to be representative of a location with a low wind speed, a wind direction that strongly favors the watershed, and a relatively high amount of total precipitation falling on the watershed. The values used were based on actual data trends for U.S

. locations as specified in Exhibit 3-2 ; however, an artificial data set was compiled (for example, temporally variable meteorological parameters were made to vary only on a daily basis). This simplified approach allowed for greater control (relative to selecting a data set for an actual location) so that desired trends or outcomes could be specified. Also, using a meteorological data set with values varying on a daily basis rather than a shorter period (such as hourly, which is the typical temporal interval for meteorological measurements) reduced required model run time

. Meteorological inputs are summarized in Exhibit 3-2

. The sensitivity of modeled 2,3,7,8-TCDD concentrations to changes in these meteorological variables was tested. Lower wind speeds and mixing heights affected concentrations the most. This sensitivity is not unexpected because lower wind speeds should increase pollutant deposition into the soil and lower mixing heights should reduce the volume through which pollutants disperse. The wind speed used for the screening scenario was 2.8 m/s, the 5 th 

### percentile of annual average among 239 stations; by comparison, the mean annual average

14 Based on sensitivity analysis, a higher erosion rate will both increase surface water concentrations and decrease surface soil concentrations; however, the relative impact on resulting concentrations will be proportionally greater in the waterbody.Appendix 5 18 

### Exhibit 3

- 2

. Summary of Key Meteorological Inputs Meteorological Property Selected Value Justification

Air temperature Constant at 298 Kelvin Recommended default value listed in HHRA P (EPA 2005a)

. Value is similar to the mean daily June temperature in the U

. S

. Deep South and to the mean daily July temperature in the U

. S

. Central Plains. a Mixing height Constant at 710 meters Value is 5 th percentile of annual average mixing heigh ts for 463 U.S

. locations, using data obtained from EPA‘s SCRAM Web site. b Value is the approximate U

. S

. median for periods without precipitation , based on data compiled by Holzworth (1972)

. Value is conservative compared to the 1

- to 2

- km typical mid

- l atitude daytime value (Stull 1988 )

. Wind direction Blows from source parcel into

scenario domain (west to east) 3 days per week; during other times does not blow into domain A wind direction that favors the location of interest (for example, a watershed downwind of a source of concern) will tend to result in more emitted mass accumulating in the location of interest

. For much of the U.S

. mid

- Atlantic and western regions, the wind tends to favor one direction (eastward). d For the hypothetical RTR scena rio, a more extreme example of this pattern is represented by conditions in Yakima, W ashington , where the wind blows eastward approximately 40 percent of the time based on a review of wind direction data compiled by the National Weather Service (NCDC 1995)

. This pattern was approximated in the RTR scenario with a configuration in which the modeled domain is downwind of the source three days out of seven.

Horizontal wind speed Constant at 2.8 meters per

second Set to 5 th percentile of annual average speed for 239 stations across the contigu o us United States (about 50 years of data per station)

. Value is similar to the annual average wind speeds of the U

. S

. Deep South. c
Precipitation frequency Precipitation occurs 3 days

per week; wind direction blows int o domain 2 of these days This value was selected so that two

- thirds of the total precipitation occurs when the domain is downwind of the modeled source

. This pattern approximates that for rainy U.S

. locations, where precipitation occurs 35

– 40% of the t ime (Holzworth 1972)

. These locations include parts of the U.S

. Northeast and Northwest. c

Total Precipitation 1.5 meters per year Assumed to represent rainy conditions for the United States

. This annual precipitation amount is experienced in parts of t he U

. S

. Deep South and parts of the U

. S

. Northwest Coast. d Conditional precipitation rate (rainfall rate when precipitation is occurring) is 9.59 mm per day, which is similar to conditions along the U

. S

. East Coast and Midwest. c

a National Climatic Da ta Center Historical Climate Series (NCDC

- HCS) ( 2007 )

. http://www5.ncdc.noaa.gov/climatenormals/hcs/HCS_MAP_7100.pdf
b Support Center for Regulatory Atmospheric Modeling; http://www.epa.gov/scram001/tt24.htm

. c National Climatic Data Center CliMaps (NCDC

- CliMaps) ( 2007 )

. http://cdo.ncdc.noaa.gov/cgi

- bin/cl imaps/climaps.plAppendix 5 19



### wind speed is 4.0 m/s in the contiguous United States). The mixing height (mean heights from four states) used was 710 m (the 5th percentile of annual average among all 40 states in the SCRAM database).

3.1.5 Aquatic Food Web

The aquatic food web is an important part of the screening scenario because the chemical concentrations modeled in fish are used to calculate human ingestion exposure and risks associated with eating contaminated fish. A biokinetic approach to modeling bioaccumulation in fish is used in the RTR screening s cenario. The primary producers (first trophic level) in the TRIM.FaTE aquatic ecosystems are algae and macrophytes. The scenario includes a benthic invertebrate compartment to represent the primary invertebrate consumers (second trophic level) in the benthic environment, and the fish compartments represent the higher tropic levels in the aquatic system. For TRIM.FaTE to provide reasonable predictions of the distribution of a chemical across biotic and abiotic compartments in aquatic systems, the biomass of the aquatic biotic compartments must represent all biota in the system and the distribution of biomass among the trophic levels and groups must be as realistic as possible.

To support the development of a relatively generic freshwater aquatic ecosystem in which to model bioaccumulation in fish, a literature search, review, and analysis was conducted in support of developing and parameterizing aquatic biotic compartments for TRIM.FaTE (ICF 2005) . This research demonstrated that the diversity of species and food webs across U.S. aquatic ecosystems is substantial, reflecting the wide range of sizes, locations, and physical/chemical attributes of both flowing (rivers, streams) and low-flow (ponds, lakes, reservoirs) waterbodies. In general, lentic bodies of water (lakes and ponds) are at a higher risk of accumulating contaminants in both sediments and biota than are lotic systems (rivers, streams). Also, the previous research (ICF 2005) suggested that a lake of at least 60 hectares (ha) likely would be sufficient to support higher trophic level predatory fish, with some fraction of the ir diet comprising smaller fish.

The RTR screening scenario includes a generic aquatic ecosystem with a 47-ha lake. Although slightly smaller than the size suggested by the previous review (ICF 2005)

, a 47-ha lake is large enough to support higher trophic level fish given the appropriate conditions. Also, this size was compatible with the overall size of the defined watershed. In the lake ecosystem defined for the screening scenario, benthic invertebrates are an important food source for a large proportion of the total fish biomass. The fish types, biomass, diet fractions, and body weights recommended for fish compartments for the screening scenario of TRIM.FaTE are listed in Exhibit 3-3

. Biomass is based on an assumption that the total fish biomass for the aquatic ecosystem is 5 .4 grams per square meter expressed as a wet weight (g w 

### /m 2 

### , ICF 2005).

A strict piscivore compartment was not selected for the screening scenario because such species are rare in lakes of small to moderate size. In general, the food web implemented in the screening scenario is intended to be generally applicable across the United States and is intended to be generally conservative (to simulate a food web that maximizes bioaccumulation).

3.1.6 Using TRIM.FaTE Media Concentrations

The screening scenario outputs include average PB -HAP concentrations and deposition rates for each year and for each parcel of the model scenario. In each surface parcel, soil concentrations are provided for the surface, root, and vadose zones and grass or leaf concentrations as appropriate for the plants. Groundwater concentrations and deposition rates to the soil are also provided. For each air parcel, air concentrations are provided

. For the lake,Appendix 5 20



### surface water concentrations and concentrations in the various levels of the aquatic food chain are included. For the ingestion exposure calculations, some concentrations are used to calculate direct exposure, and some are used to perform the farm food chain concentration calculations in the various media that humans can ingest (see Exhibit 2-4 ).

Exhibit 3

- 3

. Aquatic Biota Parameters for the TRIM.FaTE Screening Scenario

TRIM.FaTE Compartment Type Organisms

Represented by Compartment Biomass

Diet Average Body Weight (kg) Areal density (g w /m 2 ) Fraction of

Total Fish Biomass

Algae Green algae,

diatoms, blue

green algae 7.95

-- Autotrophic

--

Zooplankton Crustaceans,

rotifers, protozoans and insects 6.36

-- 100% algae a 5.7 E

- 8

Macrophyte hydrilla, milfoil 500

-- -- -- Water column (WC) planktivore young

- of

- the

year, minnows 2 .0 35.1% 1 00% zooplankton 0.025

Water column

o mnivore sucker, carp 0 .5 8.8% 10 0 % WC plankt ivore 0.25

Water column carnivore largemouth bass,

walleye 0. 2 3.5% 10 0% WC omnivore 2.0

Benthic invertebrate aquatic insects,

crustacean, mollusks b 20

-- Feeds in sedime nt 0.000255

Benthic omnivore small catfish,

rock bass 2.0 35.1% 100% benthic invert. 0.25

Benthi c carnivore large catfish 1.0 17.5% 5 0% benthic invert. 5 0% benthic omniv. 2.0

Total F ish Biomass c 5. 7

a Algae is modeled as a phase of surface water in TRIM.FaTE.
b Benthic invertebrates include aquatic insects (e.g., nymphs of mayflies, caddisflies, dragonflies, and other species that emerge from the water when they become adults), crustacea (e.g., amphipods, crayfish), and mollusks (e.g., snails, mu ssels).

c Total fish biomass does not include algae, zooplankton, macrophytes or benthic invertebrates.



### Regardless of whether the concentration and deposition values are used to calculate ingestion directly or are used in farm food chain calculations, selecting the parcel that is the source of the values used as inputs to succeeding calculations is necessary

. The locations that determine direct and indirect exposures were selected assuming generally conservative assumptions. In general, decisions regarding which TRIM.FaTE outputs to use in calculating exposures for the hypothetical scenario assume exposure at locations near the modeled source, thereby resulting in higher exposures to emitted chemicals. These assumptions are summarized in Exhibit 3-4

. TRIM.FaTE can output instantaneous chemical concentrations for a user-specified time step and also can be configured to calculate temporal averages (e.g., annual averages). For theAppendix 5 21



### screening scenario, the model is set up to output results on a daily basis, largely because daily is the smallest time step over which input data change (i.e., wind direction and precipitation rate). Daily concentration results were averaged to obtain annual average concentrations. The default assumption is annual average concentrations for media during the fiftieth year of emissions. For the chemicals modeled in this scenario, long-term concentrations in environmental media will be relatively constant at 50 years (most of the chemicals modeled for RTR approach steady state well before 50 years).

Exhibit 3

- 4

. Spatial Considerations

– TRIM.FaTE Results Selected for Calculating Farm Food Chain Media Concentrations and Receptor Exposures

T RIM.FaTE Output Used in Exposure

Calculations Representative Compartment

Concentration in air, for uptake by plants via vapor transfer Air compartment in air Parcel N2 (air over tilled soil)

Deposition rates, for uptake by farm produce Deposition to s ur face soil compartment in surface Parcel N6 (tilled soil) Concentration in surface soil, for incidental ingestion by humans and farm animals Surface soil compartment in surface Parcel N1 (untilled soil, closest to facility)
C oncentration in soil , for upta ke by farm produce and animal feed Surface soil compartment in surface Parcel N6 (tilled soil)

Concentration in fish consumed by angler Water column carnivore compartment in lake (50% of fish consumed) and benthic carn ivore in lake (50% of fish consumed)



### 3.2 Exposure and Risk Calculations

This section describes the approach for modeling chemical concentrations in farm food chain (FFC) media (Section 3.2.1 ); estimating human exposures associated with ingestion of FFC media, incidental ingestion of soil, consumption of fish, and infant consumption of breast milk (Section 3.2.2 ); and calculating human health screening risk metrics associated with these exposure pathways (Section 3.2.3 ). All of these calculations are conducted using the MIRC modeling software. For this multipathway screening evaluation, partitioning into FFC media is calculated with the same data set used to model exposure and risk, rather than as a component of the TRIM.FaTE modeling scenario. Consequently, processes and inputs related to estimating chemical levels in FFC media are summarized in this section and discussed in detail in Attachment 2.

3.2.1 Calculating Concentrations in Farm Food Chain Media

As was shown in Exhibit 2-5 , MIRC was compiled to calculate concentrations of PB-HAPs in foodstuffs that are part of the farm food chain. The FFC media included in this screening scenario are as follows:

exposed and protected fruit, exposed and protected vegetables, root vegetables, beef, total dairy products, pork, and poultry and eggs.Appendix 5 22



### The algorithms used in MIRC were obtained from EPA‘s Human Health Risk Assessment Protocol for Hazardous Waste Combustion Facilities (HHRAP; EPA 2005a)

. These algorithms model the transfer of concentrations of PB

- HAP s in FFC media using empirical biotransfer factors. As noted in Section 1 of this report, the algorithms involving ingestion exposure to be included eventually in TRIM are expected to be very similar to those presented in HHRAP. Environmental media concentrations (i.e., the chemical source terms in these algorithms) were obtained from TRIM.FaTE

. As noted in Section 3.1.6 , t he TRIM.FaTE outputs included as inputs to MIRC are the following:

PB -HAP concentrations in air; air- to -surface deposition rates for PB-HAPs in both particle and vapor phases; PB

- HAP concentrations in groundwater (used as drinking water); PB -HAP concentrations in fish tissue for fish in trophic levels three and four [T3 and T4]); and PB -HAP concentrations in surface soil and root zone soil.

In general, plant- and animal-specific parameter values, including chemical-specific transfer factors for FFC media, were obtained from the Hazardous Waste Companion Database included in HHRAP (EPA 2005a)

. A list of variables and PB- HAP -specific input parameters, along with the input values used in this screening scenario, are provided in Attachment 2.

3.2.2 Ingestion Exposure Assessment

3.2.2.1 Ingestion Exposure Pathways and Routes of Uptake

MIRC was used to estimate ingestion rates as average daily doses (ADDs) normalized to body weight for a range of exposure pathways

. Exposure pathways included are incidental ingestion of soil and consumption of fish, produce, and farm animals and related products. The ingestion exposure pathways included in the screening evaluation and the environmental media through which these exposures occur are summarized in Exhibit 3-5

. 3.2.2.2 Exposure Scenarios and Corresponding Inputs

Specific exposure scenarios are developed by defining the ingestion activity patterns (i.e., estimating how much of each medium is consumed and the fraction of the consumed medium that is grown in or obtained from contaminated areas) and the characteristics of the hypothetical human exposed (e.g., age and body weight). MIRC computes exposure doses and risks for each ingestion pathway separately, enabling the pathway(s) of interest for each PB- HAP to be determined. Data related to exposure factors and receptor characteristics were obtained primarily from EPA‘s Exposure Factors Handbook (EPA 1997a).

For the screening scenario described here, exposure characteristics were selected that result in a highly conservative estimate of total exposure. The ingestion rate for each medium was set equal to the 90 th percentile of the distribution of national data for that medium. All media were assumed to be obtained from locations impacted by the modeled source. Although this approach results in an overestimate of total chemical exposure for a hypothetical exposure scenario (for example, note that the total food ingestion rate that results is extremely high for a hypothetical consumer with ingestion rates in the 90 th percentile for every farm food type), it was selected to avoid underestimating exposure for any single farm food type

. The exposure characteristics selected for the ingestion screening scenario are summarized in Attachment 2.Appendix 5 23



### Exhibit 3

- 5

. Summary of Ingestion Exposure Pathways and Routes of Uptake

Ingestion Exposure Pathway Medium Ingested Intermediate Exposure Pathway

– Farm Animals a Environmental Uptake Route

Medium Process b

Incidental i ngestion of soil Surface soil N/A Surface soil Deposition; transfer through plants;

transfer via erosion and runoff c

Consumption of fish Fish from local water

body N/A Fish tissue Direct uptake from water and

consumption of food compartments modeled in TRIM.FaTE c Consumption of breast milk d Breast milk N/A Breast milk I ngested by mother and then

partition to breast milk

Consumption of produce Aboveground produce,

exposed fruits and vegetables N/A Air Air Soil Deposition to leaves/plants

Vapor trans fer Root uptake Aboveground produce, protected fruits and vegetables N/A Soil Root uptake

Belowground produce N/A Soil Root uptake

Consumption of farm animals and related food products Beef Ingestion of forage Air Air Soil Direct deposition to p lant

Vapor transfer to plant Root uptake Ingestion of silage
Ingestion of grain Soil Root uptake Ingestion of soil Soil Ingestion from surface

Dairy (milk) Ingestion of forage Air Air Soil Direct deposition to plant

Vapor transfer to plan t Root uptake Ingestion of silage
Ingestion of grain Soil Root uptake Ingestion of soil Soil Ingestion from surface

Pork Ingestion of silage Air Air Soil Direct deposition to plant

Vapor transfer to plant Root uptake Ingestion of grain S oil Root uptake Ingestion of soil Soil Ingestion from surface

Poultry Ingestion of grain Soil Root uptake Ingestion of soil Soil Ingestion from surface

Eggs Ingestion of grain Soil Root uptake Ingestion of soil Soil Ingestion from surface

a C alculation of intermediate exposure concentrations were required only for the farm animal/animal product ingestion pathways.
b Process by which HAP enters medium ingested by humans

. c Modeled in TRIM.FaTE

. d The consumption of breast milk exposure scenario is discussed in Section 3.2.2.4

.Appendix 5 24



### Exhibit 3

- 6

. Overview of Exposure Factors Used for RTR Multipathway Screening a,b

Exposure Factor Selection for Screening Assessment

Age group e valuated Infants under 1 year (breast milk only) Children 1 to 2 years of age Children 3 to 5 years of age Children 6 to 11 years of age Children 12 to 19 years of age Adult (20 to 70 years) Body w eight (BW; varies by age) Weighted mean of nation al distribution Intake rate and ingestion r ate (IR) for farm produce and animal
p roducts (varies by age and media consumed) 90 th percentile of distribution of consumers who produce own food

Ingestion rate for f ish 105.5 g/day ( represents the 9 9 th percent ile of fish consumption in the adult U.S. general population including consumers and non

consumers c ; th is estimate is co n sidered within the range of average v alue s for subsistence fishers d ); lower values were assumed for younger age groups , also based on t he 99 th percentile of U.S. general population

. Value reflects ―as prepared‖ consumption rate so cooking and preparation losses did not need to be considered. Exposure f requency (EF) 365 days/year

Exposure d uration Lifetime, for estimating cancer risk; v aries by chemical for chronic non

- cancer evaluation

Fraction c ontaminated (FC) (varies by media consumed) e 1

Cooking l oss f Assumed to be ―typical;‖ v a ries depending on food product ( see Attachment 2 ) . Cooking losses were not considered for fish
consump tion because intake rates represented ―as prepared‖ values.

a Values for exposure characteristics are presented in Attachment 2

. Exposure parameter values were based on data obtained from the Exposure Factors Handbook (EPA 1997a)

. See Attachment 2 for d etails.
b Exposure factor inputs are used in calculating average daily dose (ADD) estimates for each exposure pathway

. ADD equations for each pathway evaluated in this screening assessment are provided in Attachment 2

. c Fish consumption rates were obtain ed from Estimated Per Capita Fish Consumption in the United States (EPA 2002 c )

. Consumption rates were averaged by body

- weight to represent the age groups used in the screening scenario.
d The relationship equating the 99 th percentile of fish consumption i n the general population with the range of average fish consumption rates f or subsistence fishers wa s obtained from Methodology for Deriving Ambient Water Quality Criteria for the Protection of Human Health (EPA 2000)

. e Fraction contaminated represents the fraction of food product that is derived from the environment included in the screening scenario (e.g., produce grown on soil impacted by PB

- HAPs)

. This parameter is defined separately for each FFC medium

. f Cooking loss inputs were included to simu late the amount of a food product that is not ingested due to loss during preparation or cooking, or after cooking.



### 3.2.2.3 Calculating Average Daily Doses

MIRC calculates chemical-specific ADDs of chemicals normalized to body weight (mg PB- HAP per kg of body weight per day). Equations used to calculate ADDs were adapted from the algorithms provided in the technical documentation of EPA‘s Multimedia, Multipathway, and Multireceptor Risk Assessment (3MRA) Modeling System (EPA 2003), which derived much of its input data from the Exposure Factors Handbook (EPA 1997a). The ingestion exposureAppendix 5 25



### modeling approach embodied by 3MRA is conceptually similar to that presented in HHRAP. A discussion of exposure dose estimation is provided in Attachment 2. The equations to calculate ADDs for each ingestion pathway are provided in Attachment 2.

3.2.2.4 Infant Ingestion of Breast Milk

A nursing mother exposed to contaminants by any ingestion pathway described above can pass the contaminants on to her infant through breast milk (EPA 199 8) . The nursing infant‘s exposure can be estimated from the levels of chemical concentrations in the breast milk, which in turn can be estimated based on the mother‘s chemical intake. Exposures can occur for infants via this pathway for dioxins and possibly also for mercury.

Exposure to dioxins via breast milk consumption during the first year of life was estimated to account for approximately 30% of an adult‘s lifetime ADD , based on the assumptions and configuration of the screening scenario

. Exposure via the breast milk pathway during the first year of life was, therefore, accounted for in developing the threshold screening level for dioxins. For mercury, cadmium and POM, however, the breast milk pathway did not contribute a significant portion of an adu lt‘s lifetime ADD. Therefore, exposures to these chemicals via the breast milk pathway were not considered in developing the screening emission thresholds for mercury, cadmium, and POM.

3.2.3 Risk Characterization

MIRC was used to calculate excess lifetime cancer risk (ELCR) and non-cancer hazard (expressed as an HQ) using the calculated ADDs and ingestion dose-response values

. Chemical dose-response data include CSFs for ingestion and non-cancer oral RfDs for chronic exposures. The CSFs and RfDs for the PB- HA Ps included in this screening scenario are presented in Exhibit 3-7 and are discussed in more detail in Attachment 2. Equations used to estimate cancer risk and non-cancer hazard are provided in Attachment 2.

Exhibit 3

- 7

. Dose

- response Values for PB

- HAPs Addressed by the Screening Scenario

PB

- HAP CSF

([mg/kg

- day] - 1 ) Source RfD (mg/kg

- day) Source

Inorganics
Cadmium C ompounds not available 5E

- 4 IRIS Elemental Mercury NA not available Divalent Mercury not available 3E

- 4 IRIS Methyl M ercury not available 1E

- 4 IRIS Organics a

Benzo [a] pyrene 10 IRIS not available 2,3,7,8

- TCDD 1

. 5 E+5 EPA ORD 1E

- 9 ATSDR

Source: EPA OAQPS 2007 CSF = cancer slope factor; RfD = reference d ose; IRIS = Integrated Risk Information System; CalEPA = California Environmental Protection Agency; ASTDR = Agency for Toxic Substances and Disease Registry; EPA ORD = EPA‘s Office of Research and Development NA = not applicable

a T he CSF listed in IRIS f or benzo[a]pyrene was adjusted for consistency with the overall approach for dose

- response assessment of PAHs; see Attachment 2

.Appendix 5 26



### Estimated individual cancer risks for the PAHs included in the screening scenario were adjusted upward to account for the higher mutagenic cancer potency of these compounds during childhood, as specified by EPA in supplemental guidance for cancer risk assessment (EPA 2005c). Specifically, cancer potency is assumed to be tenfold greater for the first 2 years of life and threefol d greater for the next 14 years for PAHs. These factors were incorporated into a time-weighted total increase in potency over a lifetime of 70 years. The cancer potency adjustment for chemicals with a mutagenic mode of action is discussed in Attachment 2.

3.2.4 Dermal Risk Screening

Non-inhalation exposure to PB-HAPs can occur by way of the dermal pathway through contact with PB

- HAP -contaminated soil and water

. However, dermal absorption of chemicals that are originally airborne is generally a relatively minor pathway of exposure compared to other exposure pathways (EPA 2006, CalEPA 2000). This section demonstrates that for the conservative screening scenario developed for RTR multipathway evaluation, the dermal exposure route is not a significant risk pathway when compared to the ingestion pathway

. In general, the assessment followed the protocol for evaluating a reasonable maximum exposure as described in EPA‘s Risk Assessment Guidance for Superfund (RAGS), Volume I: Human Health Evaluation Model, Part E, Supplemental Guidance for Dermal Risk Assessment ( EPA 2004 c).

3.2.4.1 Hazard Identification and Dose Response Assessment

To assess the potential contribution of dermal exposure to non-inhalation exposure, w e evaluated the potential for cancer and chronic non-cancer effects for the four PB-HAPs currently assessed in the multipathway screening evaluation for RTR: cadmium, divalent mercury, 2,3,7,8-TCDD, and benzo(a)pyrene. EPA has not developed carcinogenic potency slope factors (CSFs) and non-cancer reference doses (RfDs) specifically for evaluating potential human health concerns associated with dermal exposure to PB- HAPs . Instead, dermal toxicity values can be derived from oral toxicity values via route- to -route extrapolation by adjusting for gastrointestinal (GI) absorption. EPA recommends making this adjustment only when GI absorption of the chemical is significantly less than 100% (i.e., less than 50 percent). Otherwise, a default value of complete (100 percent) oral absorption is assumed, and no adjustment is made (EPA 2004 c).

The absorbed cancer slope factor (C SF ABS 

### ) is based on the oral cancer slope factor (C SF O 

### ) and the fraction of the contaminant absorbed in the gastrointestinal track (ABS GI 

### ), as follows:

where:

C SF ABS = Absor bed slope factor ( mg/kg

- day) - 1

C SF o = Oral slope factor ( mg/kg

- day) - 1

ABS GI = Fraction of chemical absorbed in gastrointestinal tract (unitless)Appendix 5 27



### The absorbed reference dose (RfD ABS 

### ) is based on the oral reference dose (RFD O 

### ) and the fraction of the contaminant absorbed in the gastrointestinal track (ABS GI 

### ), as shown below.

where:

RfD ABS = Absorbed reference dose ( mg/kg

- day)

RfD o = Oral reference dose ( mg/kg

- day)

ABSGI = Fraction of chemical absorbed in gastrointestinal tract ( unitless)



### GI absorptions for 2,3,7,8-TCDD and all polycyclic aromatic hydrocarbons (PAHs) (which includes benzo[a]pyrene) were estimated to be greater than 50 percent. Therefore, as shown in Exhibit 3-8 , no adjustments to the available oral CSFs were required. Similarly, no adjustment to the oral RfD for 2,3,7,8-TCDD was required. For cadmium and divalent mercury, adjustments were made based on absorption data provided in RAGS Part E, Exhibit 4-1. The RfDs for dermal exposure to cadmium and divalent mercury are also shown in Exhibit 3-8

.
Exhibit 3

- 8

. Cancer Slope Factors and Reference Doses Based on Absorbed Dose

PB

- HAP ABS GI (unitless) C SF ABS a (mg/k g - day) - 1 RfD ABS a (mg/kg

- day)

Cadmium C ompounds 0.05 NA 2.5E

- 05

Divalent M ercury 0.07 NA 2.1E

- 05

2,3,7,8

- TCDD No adjustment required b 1.5E+05 1.0E

- 09

Benzo[a] pyrene No adjustment required b 1.0E+01 NA

NA = Not applicable

a Oral dose response values are presented in Exhibit 3

- 7

. Only the resulting adjusted dose response values are presented in this table.
b According to RAGS Part E, Exhibit 4

- 1, GI absorption is expected to be greater than 50%.



### 3.2.4.2 Dermal Exposure Estimation

Dermal exposures and risks resulting from absorption of the chemical through the skin from contact with contaminated water and soil were evaluated for the RTR screening scenario. Individuals were assumed to be exposed on a fraction of their bodies (i.e., their head, forearms, hands, lower legs, and feet) to contaminated soil from the TRIM.FaTE surface soil parcel with the highest concentration (N1) on a daily basis. For the water evaluation, individuals were assumed to be exposed to contaminated surface water with the same PB-HAP concentration as the TRIM.FaTE screening scenario lake over their entire bodies on a daily basis.Appendix 5 28



### Equations for Estimating Dermal Exposure The general equation used to estimate dermal absorbed dose (DAD) for water or soil is shown below, and is expressed in milligrams of PB-HAP per kilogram of receptor body weight per day (mg/kg-day)

. DAD is calculated separately for the water and soil pathways.

where:

DA event 

### = Absorbed dose per e vent; c hemical

- specific; equation for DA event also differs depending on water or soil contact (mg/cm 2

- event)

EV 

### = Event frequency ( events/day)

ED 

### = Exposure duration (years)

EF 

### = Exposure frequency (days/year)

SA 

### = Skin surface area available for conta ct (cm 2 )

BW 

### = Body weight (kg)

AT 

### = Averaging time ; f or non

- cancer effects, equals ED x 365 days/year ; f or cancer

effects, equals 70 years x 365 days/year (days)



### DA event 

### is estimated to be the total dose absorbed through the skin at the end of exposure and the equation for calculation is different for organic and inorganic chemicals in water and for soil. The equations for calculating these chemical-specific DA event 

### values for water contact are provided in RAGS Part E, Chapter 3 (see Equations 3.2

– 3. 4) . For soil, the equation for calculating these chemical-specific DA event 

### values is provided in RAGS Part E, Chapter 3 (see Equation 3.12).

Water

– Organic Chemicals:

Water

– Inorganic Chemicals:

Soil

– A ll Chemicals:

where:

DA event = Absorbed dose per event (mg/cm 2

- event)

C w C s = Chemical concentration in water (mg/cm 3 ) or soil (mg/kg)

K p = Chemical

- specific dermal permeability coefficient of compound in water (cm/hr)

FA = Chem ical

- specific fraction absorbed; accounts for loss due to the regular

shedding of skin cells of some chemical originally dissolved into skin (unitless)



# τ event = Chemical

- specific lag time per event (hr/event)

t event = Receptor

- specific event duration (hr /event)

AF = Receptor

- and activity

- specific adherence factor of soil to skin (mg/cm 2

- event)

ABS = Chemical

- specific dermal absorption fraction (unitless)

CF = Conversion factor (10 - 6 kg/mg)Appendix 5 29



### Exposure Factors and Assumptions The exposure parameters included in this assessment and their default and other value options are summarized in this subsection. Default values were selected to result in a highly conservative estimated of exposure (i.e., exposures are likely overestimated). Parameter values were primarily obtained or estimated from RAGS Part E ( EPA 2004 c ) and the CSEFH ( EPA 2008) . Receptor-and scenario-specific exposure assumptions are discussed first, and a discussion of chemical-specific parameters values follows

. Estimated water and soil exposure concentrations are presented at the end of this subsection.

Receptor-Specific Parameters Dermal exposures and risks were estimated for the same age groups used in the ingestion exposure assessment: adults (ages 20 to 70 years) and five child age groups: <1 year; 1 to 2 years; 3 to 5 years; 6 to 11 years; and 12 to 19 years. The body weight values used in the ingestion exposure assessment were used in the dermal exposure assessment.

Body surface areas for water and soil exposures for adults were calculated using Appendix C, Exhibit C-1, of RAGS Part E. For children, SAs for water and soil exposures for the five children‘s age groups were estimated using Table s 7-1 and 7-2 of the CSEFH, respectively

. For SA (water), individuals were assumed to shower or bathe in the water with 100 percent of their body exposed

. For SA (soil), it was assumed that individuals were exposed on a fraction of their total body, specifically their head, forearms, hands, lower legs, and feet. Based on information provided in RAGS Part E, the SA for forearms was calculated using the SA for arms and assuming a forearm- to -arm ratio of 0.45, and the SA for lower legs was estimated using the SA for legs and assuming a lower leg- to -leg ratio of 0.4.

Values for body SA by age group are summarized in Exhibit 3-9

.

Exhibit 3

- 9

. Receptor

- Specific Body Surface Area Assumed to be Exposed to Chemicals Age Group a (years) Surface Area for Water Exposure ( c m 2 ) Surface Area for Soil Exposure ( c m 2 )
Adult 20

- 70 18,150 g 6,87 8 h
Child <1 b 3,992 1,772 Child 1

- 2 c 5,700 2,405 Child 3

- 5 d 7,600 3,354 Child 6

- 11 e 10,800 4,501 Child 12

- 19 f 17,150 6,906

a Sources for the child groups included Table 7

- 1 (total b ody surface area for SA

- Water), and Table 7

- 2 (fraction of total body surface area for SA

- Soil) of the 2008 CSEFH.
b Represents a time

- weighted average for age groups birth to <1 month, 1 to <3 months, 3 to <6 months, and 6 to <12 months

. c Represents a time

- weighted average for age groups 1 to <2 years and 2 to <3 years

. d Values for age group 3 to <6 years in the 2008 CSEFH.

e Values for age group 6 to <11 years in the 2008 CSEFH

. Represents a conservative (i.e., slightly low) estimate for ages 6 thr ough 11 years since 11

- year olds are not included in this CSEFH age group.
f Represents a time

- weighted average for age groups 11 to <16 years and 16 to <21 years

. Note that estimated values include 11

- year

- olds and individuals through age 20, which contr ibutes to uncertainty in the estimates for 12 to 19 years.

g Represents the average total surface area of adults from Table C

- 1 of RAGS Part E.
h Represents the average surface area of adults for head, forearms, hands, lower legs, and feet from Table C

- 1 o f RAGS Part E.Appendix 5 30



### Scenario-Specific Parameters

Exhibit 3- 10 summarizes the exposure values related to frequency and duration of contact. In general, these are the recommended defaults for calculating a reasonable maximum exposure (RME) for a residential scenario as proposed by EPA in RAGS Part E, Chapter 3.

Exhibit 3

- 10 . Scenario

- Specific Exposure Values for Water and Soil Contact Exposure Parameter Receptor Value Source Water Contact
Event Duration (t event ) (hr/event) Child 1 Reasonable maximum exposure scenario for showering/bathing from RAGS Part E

, Exhibit 3

- 2 Adult 0.58
Soil Contact

Soil Adherence Factor (AF ) ( mg/cm 2 ) Child 0.2 For children, valu e is geometric mean value for children playing (wet soil) and for adults, value is geometric mean value for an adult farmer from RAGS Part E, Exhibit 3

- 3 Adult 0.1

Both Media Event Frequency (EV) (events/day) All 1 Reasonable maximum exposure scenario from RAGS Part E

, Exhibits 3

- 2 & 3

- 5

. Exposure Frequency (EF) ( days/year) All 350

Exposure Duration (ED) (years) Child <1 1 Represents the number of years included in the age group ; also used in ingestion exposure calculations. Child 1

- 2 2 Child 3

- 5 3 Child 6

- 11 6 Child 12

- 19 8 Adult 20

- 70 50

Averaging Time (AT) (days) For cancer assessment , an AT equal to a lifetime (70 years) x 365 day s /year is used . Same value used in ingestion exposure calculations.

For non

- cancer assessment, an A T equal to the exposure duration (ED) x 365 days/year is used, so AT will vary by receptor group. Same value used in ingestion exposure calculations.



### Chemical-Specific Parameters The chemical-specific parameters required to quantitatively evaluate dermal pathway exposures are listed in Exhibit 3- 11 . For the water concentration in the dermal analysis, the modeled TRIM.FaTE chemical concentration in the screening scenario pond at the screening threshold emission rate was used. For the soil concentration, the modeled TRIM.FaTE chemical concentration in surface soil in parcel N1 of the screening scenario at threshold emission rate was used. This same soil concentration was also used in ingestion exposure calculations for soil ingestion.

Dermal absorption of chemicals in water is based on the use of a dermal permeability coefficient (K p 

### ), which measures the rate that a chemical penetrates the skin. Dermal absorption of soilbound chemicals is based on the use of a dermal absorption fraction (ABS), which is a measure of how much of a chemical the skin absorbs through contact with soil.Appendix 5 31



### Exhibit 3

- 11

. C hemical

- Specific Dermal Exposure Values for Water and Soil Contact

PB

- HAP Cadmium Div alent Mercury 2,3,7,8

-

TCDD Benzo[a]

pyrene Source

Chemical concentration in Water (Cw) (mg/cm3) 2.4E

- 08 1.9E

- 09 2.6E

- 18 2.1E

- 13 TRIM.FaTE modeled concentration in screening scenario pond

Chemical concentration in Soil (Cs) (mg/kg) 6.9E

- 02 6.3E

- 02 2.2E

- 10 1.4E

- 04 TRIM.FaTE modeled concentration in surface soil in parcel N1 in screening scenario
Permeability coefficient in water (Kp) (cm/hour) 0.001 0.001 0.81 0.7 Values from RAGS Part E, Exhibits B

- 3 (organics) and B

- 4 (inorganics)

Fraction absorbed wate r (FA) (unitless) NA NA 0.5 1.00 Values from RAGS Part E, Exhibits B

- 3; only used for organic chemicals
Lag time per event (τevent) (hr/event) NA NA 6.82 2.69 Values from RAGS Part E, Exhibits B

- 3; only used for organic chemicals Dermal absorption fraction (ABS) from soil (unitless) 0.001 0.045 a 0.03 0.13 Values from RAGS Part E, Exhibit 3

- 4, unless otherw ise noted

a Value obtained from Bioavailability in Environmental Risk Assessment (Hrudey et al. 1996).



### 3.2.4.3 Screening-Level Cancer Risks and Non-Cancer Hazard Quotients

Toxicity values were used in conjunction with exposure information to evaluate the potential for cancer risks and non -cancer health hazards. Risk estimation methods are presented below

.

Dermal Cancer Risk Cancer risk for the dermal route was calculated as the product of the age-specific DAD s and the absorbed CSF for each chemical, as follows:

Dermal Cancer Risk = DAD x C SF ABS


### where:

DAD = Dermal Absorbed Dose (mg/kg

- day)

C SF ABS = Absorbed cancer slope factor ( mg/kg

- day) - 1


### Lifetime dermal cancer risks were calculated for 2,3,7,8-TCDD and benzo[a]pyrene. The total risk accounts for dermal exposures that an individual might receive from these PB

- HAP s in water plus soil over his or her lifetime (70 years).

Dermal Hazard Quotient Dermal hazard quotient (HQ) was estimated as the ratio of age-specific DAD s to the absorbed RfD for each chemical, as shown below:

Dermal HQ = DAD / RfD ABS


### where:

DAD = Dermal Absorbed Dose (mg/kg

- day)

RfD ABS = Absorbed reference dose ( mg/kg

- day)Appendix 5 32



### The aggregate HQ accounts for exposures that an individual in a receptor group may receive from the PB

- HAP in water and soil over the exposure duration. Non-cancer hazard is not additive across

the age groups evaluated here.

3.2.4.4 Dermal Screening Results

Exhibit 3- 12 presents a summary of estimated dermal non-cancer hazards by age group. A summary of estimated lifetime dermal cancer risks is provided in Exhibit 3- 13 . All HQ values were 0.006 (representing divalent mercury exposure for children less than 1 year of age) or less. This is approximately 1 70 times less than the potential ingestion hazard quotients associated with the screening scenario. The highest estimated individual lifetime cancer risk associated with potential dermal exposures was 4.1E-09 for benzo[a]pyrene; this value is approximately 240 times smaller than the ingestion risk estimated for the same screening threshold emission rate.

Exhibit 3

- 12

. Summary of Dermal Non

- Cancer HazardsAppendix 5 33 

### Exhibit 3

- 13

. Summary of Dermal Cancer Risks

PB

- HAP Dermal Lifetime

Cancer Risk Magnitude of Difference

2,3,7,8

- TCDD Water 2.64 E

- 10 > 3,700 Soil 1.49 E

- 11 > 67,300 Total 2.79 E

- 10 > 3,500 Benzo[a]pyrene Water 1. 50E

- 09 > 600 Soil 2. 63E

- 09 > 300 Total 4.12 E

- 09 > 200



### Based on these results and taking into consideration the extremely conservative nature of the dermal exposure calculations, it was assumed that it is not necessary to incorporate dermal exposures in calculating multipathway screening threshold levels

. Sp ecifically, the daily exposure durations of 0.58 hour for adults and 1 hour for children used to calculate dermal exposure from water are highly conservative and assume that the individual is bathing in surface water taken directly from a contaminated lake or is swimming in the lake for 350 days of the year. The exposure frequency of 350 days and corresponding skin surface area available for contact with contaminated soils (i.e., head, hands, arms, legs, and feet) likely also grossly overestimates dermal exposure to soil.



### 3.3 Summary of Scenario Assumptions

As emphasized previously, the screening scenario created for evaluating PB -HAP emissions from RTR facilities is intended to be generally conservative to prevent underestimating risk. The overall degree of conservatism of the scenario is the sum total of the multiple assumptions that affect the outputs of the fate and transport, exposure, and risk modeling. Exhibit 3- 14 summarizes important characteristics that influence exposure and risk estimates for this scenario and indicates the general degree of conservatism associated with the values for each assumption. Although this summary does not provide a quantitative estimate of the output uncertainty or the degree to which exposures and risks estimated using the scenario would be overestimated, it does demonstrate qualitatively that the scenario generally overestimates exposure and thus favors a health-protective risk output.Appendix 5 34



### Exhibit 3

- 14

. Summary of RTR Screening Scenario Assumptions and Associated Conservatism

Characteristic Value Conservatism Comments on Assumptions General Spatial Attributes

Farm location 375 m from source ;

generally downwind Conservative Location dictates soil an d air concentrations and deposition rates used to calculate chemical levels in farm produce.

Lake location 375 m from source ;

generally downwind Conservative Location dictates where impacted fish population is located

. Surface soil properties Typical val ues or national averages Neutral Based on existing EPA documentation and other references

. Size of farm parcel About 4 h a Conservative Relatively small parcel size results in higher chemical concentration.
Size of lake 46 ha; about 3 m average depth Cons ervative Lake is large enough to support an aquatic ecosystem with higher trophic level fish, but is relatively small and shallow (thus increasing surface area

- to

- volume ratio). Meteorological Inputs Total precipitation 1.5 m/yr Conservative Intended to represent rainy U.S

. location; set to highest state

- wide average for the contiguous U.S. Precipitation frequency (with respect to impacted farm/lake) 2/3 of total precipitation fall on farm/lake and watershed Conservative Most of total precipitation occu rs when the farm/lake are downwind of the source.

Wind direction Farm/lake are downwind 40% of the time Conservative Farm/lake located in the predominantly downwind direction

. Temporal dominance of wind direction based on data from Yakima, WA, where wind is predominantly from the west. Wind speed 2.8 m/sec Conservative Low wind speed (5 th percentile of long

- term averages for contiguous U.S.); increases net deposition to lake/watershed

. Air temperature 298 K Neutral Typical for summer temperature s in cen tral and southern U.S. Mixing height 710 m Conservative Relatively low long

- term average mixing height (5 th percentile of long

- term averages for contiguous U.S.); increases estimated air concentration

. Watershed and Water Body Characteristics Evaporatio n of lake surface water 700 mm/yr Neutral Value is representative of cooler climates

.

Surface runoff into lake Equal to 40 % of total precipitation Conservative Based on typical water flow in wetter U.S

. locations; higher runoff results in greater transfe r of chemical to lake

.Appendix 5 35



### Exhibit 3

- 14

. Summary of RTR Screening Scenario Assumptions and Associated Conservatism

Characteristic Value Conservatism Comments on Assumptions

Surface water turnover rate in lake About 12 turnovers
per year Neutral Consistent with calculated water balance; reasonable in light of published values for small lakes

. M ay overestimate flush rate if water inputs are also overest imated

. Note that after evapotranspiration, remaining water volume added via precipitation is assumed to flow into or through lake.
Soil erosion from surface soil into lake Varies by parcel; ranges from 0.002 to 0.01 kg/m 2

- day Neutral Erosion rates were calculated using the universal soil loss equation (USLE); inputs to USLE were selected to be generally conservative with regard to concentration in the pond (i.e

. higher erosion rates were favored)

. May underestimate erosion for locations susceptible to high erosion rates

. Note that higher erosion increases concentration in lake (and fish) but decreases levels in surface soil (and farm products)

. Aquatic food web structure and components Multi

- level; includes large, upper trophic level fish Conservati ve Inclusion of upper

- trophic level fish and absence of large

- bodied herbivore/detri ti vore fish favor higher concentrations of bioaccumulative chemicals and result in higher concentrations in consumed fish

. Linear food

- chain maximizes concentration of bioa ccumulative chemicals in higher

- trophic level fish. Parameters for Estimating Concentrations in Farm Food Chain Media Fraction of plants and soil ingested by farm animals that is contaminated 1.0 (all food and soil

from contaminated areas) Conservative A ssumes livestock feed sources (including grains and silage) are all derived from most highly impacted locations.

S oil

- and air

- to

- plant transfer factors for produce and related parameters Typical (see

Attachment 2 for details) Neutral Obtained from peer

- r eviewed and standard EPA reference sources.

Biotransfer factors for efficiency of uptake by animal of chemical in food/soil Typical (see

A ttachment 2 for details) Neutral Obtained from peer

- reviewed and standard EPA reference sources.

Bioavailability of chemicals in soil ( for soil ingested by animals ) 1.0 (relative to bioavailability of chemical in plant matter) Conservative Probably overestimates bioavailability in soil; many chemicals are less bioavailable in soil than in plants.

Ingestion Exposure Ass umptionsAppendix 5 36



### Exhibit 3

- 14

. Summary of RTR Screening Scenario Assumptions and Associated Conservatism

Characteristic Value Conservatism Comments on Assumptions Ingestion rates for all farm produce/livestock types Person obtains all food sources from local farm; ingestion rate is 90 th percentile of rates for home

produced food items Conservative All food derived from impacted farm; total food ingestion r ate wo uld exceed expected body weight

- normalized ingestion rates (prevents underestimating any individual food type).

Fish ingestion rate 1 .4 8 g/ kg

- day for

adult s ; between 1

. 29 and 2 .08 g/ kg

- day for children age d 1

- 19 C onservative R ate s are based on the 9 9 th percentile of general population fish consumption from EPA‘s analysis of freshwater and estuarine fish consumption derived from the USDA‘s Continuing Survey of Food Intake by Individuals (2002 c )

. Consumption rates were averaged by body

- weight to repre sent the age groups used in the screening scenario. T h ese ingestion rates likely overestimate long

- term fish consumption rates for the general population

. See Attachment 2 for a detailed discussion. Exposure frequency Consumption of

contaminated food ite ms occurs 365 days/yr Conservative All meals from local farm products.

Body weight Mean of national

distribution Neutral Note that this d oes not affect the body weight

- normalized rates for produce and animal products

. Other Chemical

- Specific Characterist ics
General chemical properties used in fate and transport modeling (Henry‘s law, K ow , etc.) Varies Neutral Obtained from peer

- reviewed sources; intended to be representative of typical behavior and characteristics.

"General" physical properties (plant

m atter density, aquatic life biomass, algal growth rate, etc.) Varies Neutral Obtained from peer

- reviewed sources; intended to be representative of typical behavior and characteristics.

Dose

- response values Varies Neutral to conservative Values used are those determined to be

appropriate for risk assessment by OAQPS; some values may be health

- protective.



## 4 Evaluation of Screening Scenario

4.1 Overview

To evidence our understanding of the models used, their configuration, and the total uncertainty associated with this model application, the screening scenario developed for RTR was subjected to a series of evaluations

. These analyses were somewhat more focused onAppendix 5 37



### TRIM.FaTE, given the complexity and variability associated with the fate and transport modeling pha se relative to other aspects of the screening calculations

. These evaluations emphasized the application of this approach (and especially TRIM.FaTE) in the context of ingestion exposure and risk screening for RTR. The analyses were not intended to be general model performance evaluations of TRIM.FaTE. EPA has conducted such analyses, which are documented in detail in Volumes I and II of the TRIM.FaTE Evaluation Report (EPA 2002b

, 2005 b ).

The purpose of the current evaluations, however, is similar to that of the previous model evaluations, in that both are intended to increase the confidence associated with model performance. Although the focus of the screening scenario evaluation (assessing the utility of the constructed modeling scenario) differs from the purpose of TRIM.FaTE model evaluations, the underlying objectives are comparable. In summary, the current evaluations are intended to achieve several objectives:

enhance understanding of how the scenario operates; better characterize the uncertainty of model results; measure model sensitivity to changes in parameter values and scenario configuration; and strengthen the defensibility of the scenario‘s application as a component of air toxics residual risk assessment.

That these analyses do not attempt to validate or ―prove‖ the accuracy of model results is important to note. As specified in the TRIM.FaTE mercury test case evaluation report (EPA 2005b) :

 ̳ Validation ‘ of such models, in the classic sense (e.g., proving the model produces accurate results across a range of input conditions), is not generally possible, in part because there are no comprehensive data sets of measured chemical concentrations (and associated contributing pollutant sources) for use in such comprehensive studies, nor are there other fully validated multimedia models against which TRIM.FaTE can be benchmarked. Thus, evaluation of TRIM.FaTE is not a yes/no exercise but a continuing accumulation of evidence leading to model refinement and eventually to increasing levels of confidence in the model results.

The screening scenario was evaluated through a series of analyses:

a general evaluation of TRIM.FaTE fate and transport modeling outputs; comparisons of model outputs to the literature (e.g., measured concentrations of the chemicals evaluated, information on the expected distribution of chemical mass in the environment); sensitivity analyses of TRIM.FaTE and MIRC inputs and model configurations on endpoints of interest; and an evaluation of related information.

As noted previously, most of these evaluations focused on the TRIM.FaTE modeling scenario. Methods and results of this evaluation are discussed in the remainder of Section 4 and in Attachment 3

.Appendix 5 38



### 4.2 Overall Chemical Mass Partitioning

A general evaluation of TRIM.FaTE outputs from simulations run using the screening scenario was conducted to inform the set-up and parameterization of the scenario and confirm that the model outputs were generally reasonable

. One approach for evaluating the overall performance of the model is to review the distribution of chemical mass among the various compartment types and chemical sinks included in the scenario. In general, many persistent and bioaccumulative chemicals emitted to the air do not readily deposit within close range of a source but instead are transported in the air away from the source (sometimes great distances) before depositing on land or water surfaces or being transformed to other chemical species.

This is true of the PB-HAPs that can be evaluated using the RTR screening scenario, and thus much of the chemical mass emitted by the modeled sources, regardless of chemical, was not expected to accumulate in the soil, water, or sediment compartments

. Instead, most of the chemical mass emitted by the source was expected to be removed through advective transport in the air and to end up in the air sinks (the compartments that capture chemical mass blown outside of the modeling domain). This outcome also would be expected, given the relatively small modeling domain. For chemical mass that remains in the domain (is deposited and does not degrade or leave the domain by other means, such as sediment burial), the overall distribution would be expected to approximate environmental observations, with much of the mass remaining in the soil or benthic sediment.

Exhibit 4-1 illustrates the distribution of chemical mass for the screening scenario for the PBHAPs of primary concern (one dioxin, one PAH, cadmium, and mercury). Results show the distribution at the end of a 50 -year simulation (or similar duration) for each chemical performed at the screening threshold emission rate (the overall distribution for each chemical is not expected to be substantially different for other emission rates, given a relatively long simulation period). As anticipated

, much of the chemical mass emitted to the screening scenario is largely removed from the scenario via air advection processes and transported to air sinks (blown out of the modeled domain of the scenario). The amount remaining in the scenario varies by chemical, with a larger fraction of mass deposited for mercury (which deposits relatively quickly as a divalent species) and much lower deposition for dioxin

. Of the chemical mass deposited to plants, land, or water and remaining in the modeled domain, most accumulates in the soil. For 2,3,7,8-TCDD and the two metals evaluated (mercury and cadmium), the sediment compartment also contains a significant amount of mass.

The mass distribution for mercury presented in Exhibit 4-1 was calculated from a single simulation with all emissions assumed to be of the divalent mercury species. Recall that TRIM.FaTE models mercury transformation among elemental, divalent, and methyl mercury

s pecies. Consequently, the distribution of mercury mass shown in the middle and lower parts of the table accounts for inter-species transformation within media as well as movement between media (and all methyl mercury in the scenario was derived from emitted divalent or elemental mercury).



### 4.3 Comparison to Measured Concentrations

4.3.1 Scope of the Evaluation

This section presents environmental measurements of the PB-HAPs evaluated for RTR and compares them to modeled concentrations estimated by TRIM.FaTE and the Multimedia Ingestion Risk Calculator (MIRC). Model outputs correspond to the estimates associated withAppendix 5 39 

### Exhibit 4

- 1

. Distribution of Chemical Mass in Screening Scenario

emission rates at the screening threshold levels for each representative PB-HAP calculated for RTR multipathway screening. We emphasize that this analysis is not intended to ―validate‖ the accuracy of the models used for RTR or the specific model configurations used to calculate screening threshold emission levels

. In general, although the comparison of environmental data to model results is often a central component of model evaluation, deriving useful conclusions from such comparisons is complicated by a range factors, including: fundamental differences between the modeling scenario and the environmental system in which samples were collected; temporal and spatial issues (e.g., model results representative of long-term average concentrations vs

. measured point estimates); data quality issues; and other factors. In the current evaluation, it is difficult to derive conclusions from model- to -measurement comparisons given the use of a modeling scenario that is intended to be representative but hypothetical and conservative (i.e., possessing characteristics that lead to higher exposures while not representing any real location or specific site). In addition, the RTR modeling scenario is intended to calculate incremental environmental concentrations and exposures without accounting for any ―background‖ concentrations from natural or anthropogenic sources.

In spite of these complications, this comparative analysis is an appropriate

— and necessary

— aspect of the model evaluation process because environmental data provide a general frame of reference for the model outputs. Basic differences between the modeling scenario and the data sets collected preclude the verification or validation of model configuration, performance, orAppendix 5 40



### results, and the comparisons should be viewed in light of the complicating issues listed above. However, we believe that this comparative analysis, considered in conjunction with other aspects of the evaluation, is a useful tool in gauging the effectiveness of the screening scenario in informing regulatory decision-making.

4.3.2 Methods and Organization of this Section

The TRIM.FaTE and MIRC outputs presented in this section are those used to calculate the screening threshold emission levels in the screening scenario (see Section 2 for discussion o f screening threshold emission rates). Model outputs from the source parcel are not used for comparisons; instead, concentrations from the land parcel closest to the source (N1) are used in comparisons for soil results, while outputs from the pond parcel are used for comparing results for water, sediment, and fish (See Exhibit 3-1 for Surface Parcel Layout). Chemical concentrations in air are not evaluated in this section for two reasons. First, the TRIM.FaTE model was not designed to estimate air concentrations for the assessment of inhalation exposure, as noted in Section 2.4.1. Second, chemical concentrations in the air compartment affect exposure concentrations less directly than deposition of the chemical

. Therefore, the

c omparison of chemical concentrations in air to observed values is not included in this evaluation

. The purpose of the 50-year duration of the scenario is to represent long-term input of source emissions over a hypothetical facility lifetime (many compartments also attain an approximate steady state by this time). For all environmental media compartments, the maximum annual average concentrations, taken from the final year of the simulation, are used in MIRC to determine the maximum average concentrations in ingestible products. These concentrations, along with ingestion rates for each food product, are used to calculate average daily doses (ADDs) for each chemical, from which the lifetime cancer risk or age-group-specific hazard quotient (HQ) is then calculated. The model results presented in this section are the environmental media concentrations used to calculate the screening threshold emission rates (i.e., those concentrations calculated for the 50th year of the TRIM.FaTE simulation) and the ingestible media concentrations calculated in MIRC using those environmental media concentrations (s ee Exhibit 3-5 fo r TRIM.FaTE outputs used in exposure calculations).

The evaluations described in this section are presented separately for each chemical for which a screening threshold has been derived

. Each chemical-specific section provides a review of the emission profiles used in the modeling process, and a summary of the expected chemical behavior in the environment. This is followed by comparisons between model results and ranges of observed concentrations in environmental media, partitioning behavior, and observed concentrations in ingestible products.

In the charts displaying the comparisons between model results and observed concentrations, the horizontal bars in the graph represent measured concentrations reported in the literature for various environmental media

. The green bars show ranges of measured concentrations that were reported as less than a maximum concentration or detection limit, with the upper bound of the bar representing the limit of detection

. Blue bars indicate a range of values reported by a particular source. The vertical red lines in the graph represent the modeled TRIM.FaTE concentrations obtained using the screening threshold emission rates. Observed data from areas exposed to varying ranges of chemical emissions were chosen for the comparison in order to represent a variety of scenarios

. In general, the low end of the range represents concentrations from remote areas not located near a considerable pollution source, while theAppendix 5 41



### high end of the range represents concentrations observed near industrial sources (e.g., metal smelters, chlor-alkali plants, incineration/combustion facilities ) a nd/or in urban areas. The observed values provided as examples in this section include data collected from a range of sampling techniques, locations, emissions profiles, historical contributions, and other factors influencing concentration. They do not represent the entire range of possible measured values, and therefore should not be combined to create a contiguous range of concentrations representative of all patterns in the United States. Model outputs were derived using a generally conservative set of fate and transport inputs, and they reflect the estimated environmental levels assuming concentrations from only one source and no ambient background concentrations.

4.3.3 Chemical-Specific Comparisons

4.3.3.1 Cadmium

Behavior in the Environment

Based upon reviewed literature, some of the largest anthropogenic sources of cadmium to airare facilities that process, mine, or smelt cadmium-zinc or cadmium-zinc-lead ores; coal and oilfired boilers; other urban and industrial facilities; phosphate fertilizer manufacturing facilities; road dust; and municipal sewage sludge incinerators (ATSDR 2008). These facilities can emit airborne cadmium particles that are capable of traveling long distances before depositing onto soil or water bodies via dust, rain, or snow. Cadmium adsorbs to soil particles in the surface layers of the soil profile, but to a lesser degree than many other heavy metals (HSDB 2005a). It may enter surface waters through atmospheric fallout, runoff, or wastewater streams, but most cadmium compounds will be removed from the surface water compartment through adsorption to organic matter in sediment or to other suspended compounds. Concentrations in bed sediment are expected to be roughly an order of magnitude higher than those in overlying surface water (HSDB 2005a).

Freshwater fish accumulate cadmium primarily through direct uptake of the dissolved form through the gills and secondarily through diet, which plays a variable role in total cadmium uptake (Reinfelder et al

. 1998, Chen et al

. 2000, Saiki et al

. 1995) . The degree to which cadmium bioaccumulates in fish is largely dependent upon water pH and humus content (ATSDR 2008). Reported bioaccumulation factors (BAFs), or bioconcentration factors (BCFs), of 3 to 4,190 (ATSDR 2008) and 907 (EPA 2005a) have been reported for freshwater organisms and fish

. Although some biomagnification of cadmium has been reported for aquatic food chains involving fish in saltwater systems, biomagnification in freshwater systems appears to be present only at lower trophic levels (Chen et al. 2000) and in narrowly defined niches (e.g., plankton/macroinvertebrate food chains; Croteau et al. 2005). Biomagnification factors (BMFs) of less than 1 have generally been reported for fish at higher trophic levels, indicating that cadmium concentrations generally biodiminish from lower to higher trophic levels (Chen et al. 2000, Mason et al. 2000).

Emission Profile

The cadmium screening threshold emission rate derived from the RTR PB-HAP screening is 3.51E- 02 TPY

(tons per year) or 87 .2 g/day (based on an HQ of 1 in children aged 1-2). Although the annual concentration from year 50 is used for comparison, modeled concentrations of cadmium in most compartments generally leveled off after year 20. One notable exception was the soil compartment in parcel N6, where the soil in the screeningAppendix 5 42



### scenario is tilled and no plants are modeled in the TRIM.FaTE scenario

. Cadmium concentrations in this compartment continued to rise through year 50. The steady build-up of cadmium in this parcel is likely due to the thickness of the surface soil layer in the N6 parcel

. Because this parcel is tilled, the surface soil layer is thicker than in the other parcels, and the rate of exchange between the surface soil and the root zone soil is correspondingly lower.

Concentrations in Environmental Media

Exhibit 4-2 displays measured concentrations in environmental media with TRIM.FaTE outputs for the screening scenario. Modeled concentrations and BAFs in fish compartments are shown in Exhibit 4-3

. Because relationships between fish compartments in the screening scenario are established within a food web structure, there is no explicit delineation to specific trophic levels. However, for evaluation of trophic level patterns, the water column herbivore (WCH) can be considered to represent the lowest trophic level among fish, while the water column carnivore (WCC) represents the highest trophic level.

The cadmium concentrations output by the RTR screening scenario were consistent with reported values in all environmental media compartments. Consistent with trends noted in the literature, modeled cadmium concentrations were highest in fish at the lower trophic levels (i .e., BC ). Though modeled concentrations did not uniformly decrease with an increase in trophic level, the concentrations for all but the benthic carnivore (BC) compartment were markedly lower than those in the WCH compartment. It should be noted that BAFs for the other chemicals evaluated in this section are several orders of magnitude greater

— and span much wider ranges

— than the BAFs reported for cadmium in fish. Thus, in the context of comparison between chemicals, the difference between cadmium BAFs in fish compartments is quite small.

The BAFs calculated using model outputs from the RTR screening scenario were consistent with the range of values presented in the literature for freshwater systems. Overall, modeled concentrations and BAFs in all fish compartments were reasonably consistent with observed trends, with cadmium levels generally diminishing from lower to higher trophic levels, and consistent with the assumption that diet plays a variable role in the bioaccumulation of this substance in fish.

Partitioning Behavior

Because most cadmium emitted to the air will eventually deposit onto soils, cadmium has been observed to partition primarily to soil when released to the environment (ATSDR 2008). Cadmium mobility in soil depends strongly on soil pH, clay content, and availability of organic matter

— factors that determine whether the cadmium is dissolved or sorbed in surface soil. In general, cadmium binds strongly to organic matter, rendering the metal immobile; however, some plants are able to efficiently take up cadmium, thus providing an entry point for cadmium into the food chain (ATSDR 2008).

Most cadmium in a natural water column is dissolved, but some adsorption to humic substances and other organic complexing agents can occur. This behavior can be especially important i n polluted or organic-rich waters, playing a dominant role in cadmium transport (ATSDR 2008). Concentrations in surface water tend to be lower than those in bed sediment because cadmium readily adsorbs to mineral surfaces, hydrous metal oxides, and organic materials present in sediment. Cadmium that has adsorbed to mineral surfaces in the sediment is not easily bioaccumulated in the aquatic food web unless the sediment is disturbed, and the metal is redissolved.Appendix 3 43 

### Exhibit 4

- 2

. Summary of Modeled and Observed Concentrations of Cadmium in Environmental Media

WCC = Water Column Carnivore, BC = Benthic Carnivore, SWP = Stormwater Pond, TS = Tilled Soil, US = Untilled Soil

a Source: ATSDR Toxicological Profile for Cadmium (ATSDR 2008 ) b Source: Hazardous Substances Databank Record for Cadmium Compounds ( HSDB 2005a )

c Source: Copper, Cadmium, and Zinc Concentrations in Aquatic Food Chains from the Upper Sacramento River and S el e cted T ributaries (Saiki et al. 1995) d Source: Accumulation of Heavy Metals in Food Web C ompon ents Across a Gradient of Lakes ( Chen et al. 2000)Appendix 5 44 

### Exhibit 4

- 3 . TRIM.FaTE Cadmium Concentrations in Fish and Calculated Bioaccumulation Factors with Respect to Total Water Concentration

For the RTR screening scenario, approximately 5 percent of cadmium in the pond compartment partitioned to surface water, while 95 percent partitioned to sediment. The percentages of cadmium in sorbed and dissolved states in surface water, sediment, and surface soil are presented in Exhibit 4-4

. The partitioning behavior modeled in TRIM.FaTE is consistent with the behavior of cadmium in the natural environment. The presence of cadmium primarily in the dissolved state in surface water and sorbed to sediment and surface soil is consistent with trends noted in supporting literature.

Exhibit 4

- 4

. Fraction of Cadmium Mass Sorbed vs. Dissolved in

TRIM.FaTE Compartments Compartment Sorbed Dissolved

Surface Soil 100.0% 0.0%

Surface Water 4.6% 95.4%

Sediment 99.9% 0.1%



### Concentrations in Ingestible Products

The major source of non-inhalation exposure to cadmium outside of occupational settings is through dietary intake. Available data indicate that cadmium accumulates in plants, aquatic organisms, and animals, offering multiple ingestion exposure pathways (ATSDR 2008). However, actual cadmium levels in ingestible products can vary based upon type of food,Appendix 5 45



### agricultural and cultivation practices, atmospheric deposition rates, conditions in environmental media, and presence of other anthropogenic pollutants. General trends indicate that high levels of cadmium can be found in green, leafy vegetables; peanuts; soybeans ; and sunflower seeds. Meat and fish generally contain lower amounts of cadmium, overall, but cadmium can be found highly concentrated in certain organ meats, such as kidney and liver (ATSDR 2008). In a study of cadmium concentrations in 14 food groups (including prepared foods), meat, cheese, and fruits generally contain ed low levels of cadmium (ATSDR 2008).

Modeled cadmium concentrations in ingestible products are displayed in Exhibit 4-5 along with cadmium concentrations reported in literature. In the screening scenario we assume that individuals consume equal amounts of benthic carnivores and water column carnivores, so the concentration for fish is given as the average of these two fish compartments. The cadmium concentrations output by MIRC were consistent with reported values in all ingestible media products. The products with higher reported cadmium levels in the literature, including soil, plants, and fish, also contained the highest modeled concentrations.

To determine media types most relevant to exposure and risk, the estimated media concentrations must be combined with ingestion exposure factors (i.e., a higher concentration for a particular medium do es not necessarily mean higher risk). The contribution of ingestion exposure pathways to the ADD (and thus the HQ) for the different age categories are displayed i n Exhibit 4-6

. The HQ of 1 for children aged 1- 2 was used to determine the screening threshold level for cadmium in the screening scenario. The dominant exposure pathway for this age group was consumption of fish, which comprises almost 96 percent of ADD.

4.3.3.2 Mercury

Behavior in the Environment

Mercury emitted by anthropogenic sources undergoes changes in form and species as it moves through environmental media

. The three most relevant forms of mercury in the environment are elemental mercury, divalent inorganic mercury, and methyl mercury. Based upon reviewed literature, some of the largest anthropogenic sources of mercury to air are facilities that process, mine, or smelt mercury ores; industrial/commercial boilers; fossil fuel combustion activities (primarily coal); cement production facilities; other urban and industrial facilities; and medical and municipal waste incinerators (ASTDR 1999). Stack emissions can include a mixture of elemental and divalent forms, mostly in the gaseous phase, with some divalent forms in particlebound phases (EPA 1997b). Although elemental mercury is more prevalent in the atmosphere, divalent mercury can be found at higher concentrations near emissions sources. Elemental mercury has a very long residence time in the atmosphere and will thus be distributed relatively evenly on a global scale, resulting in negligible impacts from any single source on local and regional scales. Divalent mercury, however, is removed from the atmosphere at a faster rate than elemental mercury, and may be tr ansferred to the surface near the emission source via wet or dry deposition, where it appears to adsorb tightly to soil particles (EPA 1997b). Some adsorbed divalent mercury can be reduced to elemental mercury and be revolatilized back into the atmosphere. Methylation to methyl mercury by microbes can also occur in the soil ; however, divalent mercury is generally the dominant species in soil (EPA 1997b). Small amounts of divalent and methyl mercury in soil can be transported to surface water through runoff and leaching. Direct deposition to water can occur through atmospheric fallout. Once in the water body, divalent mercury may be methylated through microbial activity, and both divalent and methyl mercury may be further reduced to elemental mercury, which will reenter the atmosphere. But, as in soil, divalent mercury will generally be the dominant species in bothAppendix 5 46



### Exhibit 4

- 5

. Summary of Modeled and Observed Concentrations of Cadmium in Ingestible Media

* except soil, which is expressed as mg/kg dry weight. SWP = Stormwater Pond

a Source: Hazardous Substances Databank for Cadmium Compounds ( HSDB 2005a )
b Source: ATSDR Toxicological Profile for Cadmium (ATSDR 2008 )

c Source: Total Diet Study, Market Baskets 1991

- 3 through 2005

- 4 ( FDA 2007 )Appendix 5 47



### Exhibit 4

- 6

. E stimated Contribution of Modeled Food Types to Cadmium Ingestion Exposures and Hazard Quotient

surface water and sediment. Methyl mercury is readily bioaccumulated and efficiently biomagnified in aquatic organisms and is typically the species of greatest concern for mercury exposure via the food chain.

Emission Profile

TRIM.FaTE assumes that only elemental mercury and divalent mercury are emitted from the source (see Section 2.3); but once in the environment, these species may change form, resulting in ingestion exposure to methyl mercury as well as divalent mercury

. Relative to these two species, elemental mercury does not comprise a significant amount of total mercury in environmental media other than air. Because human health effects from exposure to methyl mercury and divalent mercury are not additive, two screening threshold rates for emissions of divalent mercury were calculated for exposure to methyl mercury and divalent mercury, respectively, to determine the most health-protective level

. The emission rate calculated for the HQ for methyl mercury was lower, and thus was used to define the emission threshold.

The screening threshold emission rate used for mercury in the RTR screening scenario is 1.95 E-03 TPY

or 4.8 g/day

of divalent mercury (based on an HQ of 1 for methyl mercury exposure for children aged 1- 2) . Annual concentrations from year 50, which were used to calculate the emission screening threshold are presented here, and these values are used for comparison to concentrations found in literature. Modeled concentrations of mercury in all compartments but untilled soil continued to rise up to the end of the simulation, with the rate of increase steadily diminishing over time.Appendix 5 48



### Concentrations in Environmental Media

Exhibi t 4-7 displays measured ranges of total mercury concentrations in environmental media with TRIM.FaTE outputs for the screening scenario. The total mercury concentrations estimated by TRIM.FaTE were generally consistent with reported values in all environmental media compartments. Overall, modeled total mercury concentrations were generally within therange of values reported for areas near a significant pollution point source (e.g., smelter, chloralkali facility).

Methyl mercury is formed via microbial transformation of inorganic mercury in sediment, surface water, and soil and readily accumulates in the tissues of planktivorous and piscivorous fish. There seems to be a relationship between methyl mercury levels in fish and water pH, showing higher levels of methyl mercury in fish found in acidic lakes (EPA 1997b). Lake alkalinity and dissolved oxygen content may also influence the ability of fish to bioaccumulate methyl mercury (EPA 1997b). BAFs on the order of 10 5 

### to 10 7 

### have been reported for methyl mercury concentrations in fish (Alpers et al. 2008). Modeled concentrations of mercury species in fish compartments along with estimated methyl mercury BAFs are shown in Exhibit 4-8 . The TRIM.FaTE outputs for the fish compartments mirror a trend noted in the literature in which divalent mercury is observed more prominently in lower trophic level organisms, while methyl mercury is the more prominent species in higher trophic level organisms (ATSDR 1999). Calculated BAFs are consistent with reported values, with the higher trophic levels exhibiting BAFs of approximately 10 6 

### . Th e biomagnification of the methylated species in the aquatic ecosystem can be observed in Exhibit 4-8

, with modeled methyl mercury concentrations increasing substantially from the lower to higher trophic levels

. Partitioning Behavior

Soil acts as the primary reservoir for divalent mercury emitted from anthropogenic sources. In some cases, divalent mercury will be adsorbed onto forms of dissolved organic carbons (DOCs), which are susceptible to runoff

. However, most divalent mercury from atmospheric deposition remains in the soil profile in the form of inorganic compounds bound to soil organic matter. The ability of mercury to form complexes with soil organic matter is highly dependent on soil conditions such as pH, temperature, and soil humic content. For example, mercury strongly ad sorbs to humic materials and sesquioxides in soil at pH > 4 and in soils with high iron and aluminum content (ATSDR 1999). Although inorganic compounds containing divalent mercury are relatively soluble, this complexing behavior with organic matter significantly limits mercury transport. Only very small amounts of mercury present in soil are partitioned to runoff

. Elemental mercury present in soil (e.g., as a result of the reduction of divalent mercury) will readily volatilize, especially in acidic soils, and this species therefore comprises very little of the total mercury content in soil

. Typically, methyl mercury comprises 1 to 3 percent of total mercury in soil (EPA 1997b). Fo r the TRIM.FaTE results in the RTR screening scenario, divalent mercury comprised approximately 95 percent of total mercury in the surface soil compartment; this result is consistent with environmental trends.

Solubility of mercury in water depends on the species and form of mercury, water pH, chloride ion concentrations, and other factors (ATSDR 1999). Solid forms of inorganic mercury compounds will partition to particulates in the water column and then partition to the sediment bed (EPA 1997b). Low pH favors the methylation of mercury in the water column, typically performed by sulfur-reducing bacteria in anaerobic conditions. Methyl mercury generally comprises 10 percent of total mercury observed in surface water (EPA 1997b). A considerableAppendix 5 49 

### Exhibi t 4

- 7

. Summary of Modeled and Observed Concentrations of Total Mercury in Environmental Media

BC = Be n thic Carnivore, WCC = Water Column Carnivore , TS = Tilled Soil, US = Untilled Soil

a Source: ATSDR Toxicological Profile for Mercury (ATSDR 1999)
b Source: Mercury Study Report to Congress ( EPA 1997b )

c Source: National Study of Chemical Residues in Fish ( EPA 1992a )Appendix 5 50



### Exhibit 4

- 8

. TRIM.FaTE Mercury Conc entrations
, Speciation , and Calculated Methyl Mercury Bioaccumulation Factors ( in parentheses ) in Fish Compartments

amount (25 to 60 percent) of both divalent mercury compounds and methyl mercury will be strongly particle-bound in the water column (EPA 1997b). The remaining mercury will be in a dissolved state. Most of the elemental mercury produced as a result of reduction of divalent mercury by humic acid will volatilize

. Screening scenario modeling results for mercury speciation in environmental media compartments are displayed in Exhibit 4-9 along with the percent of each species that was present in both adsorbed and dissolved states in surface soil, surface water, and sediment. Consistent with observed trends, divalent mercury was the most prevalent species in modeled surface soil, surface water, and sediment compartments, while methyl mercury was the dominant species in fish. For the RTR screening scenario, roughly 99 percent of total mercury in the pond (i.e., surface water and sediment) was divalent mercury. The TRIM.FaTE outputs of approximately 2 percent methyl mercury in soil and 1 percent methyl mercury in surface water are also consistent with trends noted in the literature (EPA 1997b ).

Overall, the partitioning behavior in the RTR screening scenario is consistent with the behavior of mercury in the natural environment. Within the pond compartment of the model

, 95 percent or more of each mercury species partitioned to the sediment. Though all mercury in natural soils and sediment may not be in the sorbed state, the percentage of mercury that does not complex with organic matter would likely be negligible. The behavior in the TRIM.FaTE surface water compartment is consistent with trends observed in natural waters in which divalent and methyl mercury species exhibit a strong preference for adsorption to suspended matter in theAppendix 5 51



### water column. These species may also form complexes with dissolved organic carbon and thus be considered as dissolved in the water column; however, this is not as prevalent as complexation with suspended solids. Conversely, elemental mercury does not adsorb readily to suspended particles, and is therefore found primarily in the dissolved form in natural waters, where it is highly susceptible to revolatilization into the atmosphere. The high percent dissolved elemental mercury estimated by TRIM.FaTE (when compared to percent dissolved divalent or methyl mercury) in surface water is consistent with this trend. It has been estimated that more than 97 percent of dissolved gaseous mercury in the water column is elemental mercury (EPA 1997b).

Exhibit 4

- 9 . TRIM.FaTE Mercury Speciation and Partitioning in Environmental Media Co mpartments

Chemical Methyl Mercury Elemental Mercury Divalent Mercury

Sorbed Dissolved Sorbed Dissolved Sorbed Dissolved

Surface soil 100.0% 0.0% 100.0% 0.0% 100.0% 0.0% Surface Water 80.7% 19.3% 4.8% 80.7% 83.0% 17.0% Sediment 100.0% 0.0% 100. 0% 0.0% 100.0% 0.0%



### Concentrations in Ingestible Products

Available data indicate that mercury bioaccumulates in plants, aquatic organisms, and terrestrial animals, providing multiple ingestion exposure pathways (EPA 1997b, ASTDR 1999). Low levels of mercury are found in plants, with leafy vegetables containing higher concentrations than potatoes, grains, legumes, and other vegetables and fruits (ASTDR 1999, EPA 1997b). Cattle are capable of demethylating mercury in the rumen, and therefore store little of the small amount of mercury that is transferred to livestock via foraging or silage/grain consumption. Mercury content in meat and cow‘s milk is therefore low (ASTDR 1999) . Concentrations ofAppendix 5 52



### methyl mercury in fish are generally highest in larger, older specimens at the higher trophic levels (EPA 1997b).

Concentrations of total mercury in ingestible products are presented in Exhibit 4-9 10 . Though data on mercury in foods other than fish are not abundant in the literature, total mercury concentrations output by MIRC were generally consistent with the reported values that were available

. The exposure pathways that most influence the mercury HQs in the model can be seen in Exhibit 4- 11 , which displays the contributions of ingestion exposure pathways to the methyl mercury and divalent mercury ADDs for all age groups analyzed in the screening scenario. As can be seen in Exhibit 4- 11 , the dominant exposure pathway for methyl mercury was ingestion of fish for all age groups. Methyl mercury concentrations in fish were very high relative to divalent mercury (approximately 95 percent of total mercury), and fish consumption contributed the overwhelming majority to the methyl mercury ADD. All ingestion products except for beef and dairy contributed to the ADD for divalent mercury. However, as can be seen in Exhibit 4- 12 , the screening level HQ is driven by methyl mercury ingestion, and this primarily is from fish ingestion.Appendix 5 53



### Exhibit 4

- 10

. Summary of Modeled and Observed Concentrations of Total Mercury in Ingestible Media

*except soil, which is expressed as mg/kg dry weight

a Sourc e: Hazardous Substances Databank Report for Mercury Compounds ( HSDB 2005b )
b Source: ATSDR Toxicological Profile for Mercury (ATSDR 1999)

c Source: Mercury Study Report to Congress ( EPA 1997b )
d Source: National Study of Chemical Residues in Fish ( EPA 1992 a )

e Source: Total Diet Study, Market Baskets 1991

- 3 through 2005

- 4 ( FDA 2007 )Appendix 5 54 

### Exhibit 4

- 12

. Estimated Contribution of Summed Modeled Food Types to

Divalent Mercury and Methyl Mercury Hazard Quotients

4.3.3.3 Dioxins (2,3,7,8-TCDD)

Behavior in the Environment

Polychlorinated di benzo- di oxins and -furans 15 

### are reported in the National Emission Inventory (NEI) as individual congeners, congener groups, or toxic equivalents (TEQs). The dioxincongener 2,3,7,8-TCDD was used as a surrogate to evaluate risks for chlorinated dibenzo-pdioxins in the screening scenario. Of the chlorinated dioxin congeners, this compound has been the most widely studied, and is considered to be one of the two most toxic congeners to

15 Group is commonly referred to as ―dioxins;‖ this short hand is used in this section. 

### Exhibit 4

- 11 . Estimated Contribution of Modeled Food Types to Divalent Mercury

and Methyl Mercury Ingestion Exposure sAppendix 5 55



### vertebrates (ASTDR 1998). As a result, the World Health Organization (WHO) assigned a toxic equivalency factor (TEF) of 1 to this congener, meaning that the concentrations of the other congeners are scaled relative to the toxicity of 2,3,7,8-TCDD (See Attachment 2 for TEFs). We deemed this species an appropriate surrogate to represent the fate and transport behavior of the dioxin group.

Incineration/combustion processes are believed to be the primary emission sources for chlorinated dioxins (ASTDR 1998). The five stationary source categories that generate the vast majority of 2,3,7,8-TCDD emissions in the United States are municipal waste incineration, medical waste incineration, hazardous waste kilns from Portland cement manufacturing, secondary aluminum smelting, and biological incineration. Dioxins emitted to the atmosphere may be transported long-range as vapors or bound to particulates, depositing in soils and water bodies in otherwise pristine locations far from the source. Though airborne dioxins are susceptible to wet and dry deposition, most dioxins emitted to the atmosphere through incineration/combustion processes are not deposited close to the source (ASTDR 1998).

Dioxins strongly adsorb to organic matter in soil and show very little vertical movement, particularly in soils with a high organic carbon content (ASTDR 1998). Most surface water deposition occurs through dry deposition from the atmosphere and from wind-transported eroded soil particles contaminated with dioxins

. Most dioxins entering the water column will partition to bed sediment, which appears to be the pr imary environmental sink for this chemical group (EPA 2004b). Although dioxins bound to aquatic sediment will primarily be buried in the sediment compartment, some resuspension and remobilization of congeners may occur as a result of disturbance of sediments by benthic organisms (ASTDR 1998).

Bioaccumulation factors in fish are high for 2,3,7,8-TCDD as a result of the lipophilic nature of chlorinated dioxins

. Though the process es by which freshwater fish accumulate dioxins are not well understood, it has been shown that fish and invertebrates both bioaccumulate congeners when exposed to contaminated sediments, and bioconcentrate congeners dissolved in water (EPA 2004b). However, because most dioxins in the aquatic environment are ad sorbed to suspended particles, it is unlikely that direct uptake from the water is the primary route of exposure for most aquatic organisms at higher trophic levels (ASTDR 1998). At the lower trophic levels, the primary route of exposure appears to be through uptake of water in contaminated sediment pores, whereas the primary route of exposure in the higher trophic levels appears to be through food chain transfer. Following ingestion, some fish are capable of slowly metabolizing certain congeners, such as 2,3,7,8-TCDD, and releasing the polar metabolites in bile. This may ultimately limit bioaccumulation at higher trophic levels (ASTDR 1998) . Measured bioaccumulation factors for 2,3,7,8-TCDD are not widely reported due to the difficulty of detecting trace levels of congeners in ambient water. Reported bioconcentration factors, which can be measured in laboratory conditions, but do not account for exposure pathways other than direct uptake from water, range from 200-100,000, depending on the species and medium (ASTDR 1998)

.

Emission Profile

The 2,3,7,8-TCDD threshold emission rate used for the RTR screening scenario is 9. 18 E-1 0 TPY or 2. 3E- 06 g/day (based on lifetime cancer risk of 1- in -a-million)

. Although the annual concentration from year 50 is used for comparison, modeled concentrations of 2,3,7,8-TCDD either reached an approximate steady state or had begun to level off in all compartments by year 20.Appendix 5 56



### Concentrations in Environmental Media

Measured ranges of total dioxin TEQ concentrations 16 

### in environmental media are displayed with modeled TEQ concentrations of 2,3,7,8-TCDD i n Exhibit 4- 13 . Modeled concentrations and BAFs in fish compartments are shown in Exhibit 4- 14

. The 2,3,7,8-TCDD concentrations output by the RTR screening scenario were consistently lower than values reported in the literature. Three main factors likely contributed to this trend. These are the high background values resulting from the ubiquitous nature of dioxins in the environment, limited availability of 2,3,7,8-TCDD-specific data, and the use of conservative exposure factors to calculate the screening threshold. Firstly, due to the quantity of dioxins that have been emitted in the past and their persistence in the environment, dioxins are typically present in environmental media at relatively high background levels when compared with concentrations output from the screening scenario, which only considers emissions from a single facility and do es not consider background levels. As a result, it is not unreasonable that some of the TRIM.FaTE outputs were several orders of magnitude smaller than those reported in the literature, as background levels will be higher than incremental levels. Secondly, though measured data for 2,3,7,8-TCDD were used when available, concentrations in most media were available only for total dioxin TEQ concentrations. Thus, those ranges are not representative of 2,3,7,8-TCDD alone and may contain values that are higher and ranges that are wider thanthose for a single chemical. Thirdly, it should be noted that in order to maintain a healthprotective approach to screening emissions, a collection of conservative exposure factors were used, which likely resulted in low, but not implausible media concentrations.

It should also be noted that because dioxin congeners are often present at trace levels, analytical instruments must be very sensitive if congeners are to be detected in environmental media. As a result, limits of detection in many instruments may not be sufficiently sensitive to produce quantifiable results for very low levels of dioxin congeners. Many of the concentrations output by TRIM.FaTE are low enough to be considered nondetects by most analytical instruments.

Though the 2,3,7,8-TCDD concentrations in environmental media estimated by TRIM.FaTE are generally low, they are not outside the range of plausible values when considered as a surrogate for the dioxin profile. In the screening scenario, the amount of chemical mass in the water column is small relative to the amount in the sediment. This is consistent with the trend that most congeners are removed from water bodies through adsorption to organic matter in soil and sediment. The screening scenario BAFs are also consistent with observed trends that indicate that 2,3,7,8-TCDD accumulates much less readily in herbivorous fish than in carnivorous fish that consume other contaminated organisms (ATSDR 1998).

16 It was not possible to confirm that TEQ concentrations reported in the literature and summarized here were all estimated using the most recent TEF scheme adopted by the WHO in 1998. TEQ concentrations reported here may represent values determined using TEFs from EPA‘s 1989 scheme, WHO‘s 1994 scheme, or WHO‘s 1998 scheme (EPA 1997b).Appendix 5 57



### Exhibit 4

- 13

. Summary of Modeled 2,3,7,8

- TCDD Concentrations and Observed Total Dioxin TEQ Concentrations in Environmental Media

BC = Benthic Carnivore, WCC = Water Column Carnivore, TS = Tilled Soil, US = Untilled Soil

a Source: Exposure and Human Health Reassessment of 2,3,7,8

- Tetrachlorodibenzo

- p

- Dioxin (TCDD) and Related Compounds ( EPA 2004b ) b Source: Toxicological Profile for Chlorinated Dibenzo

- p

- dioxins (ATSDR 1998)Appendix 5 58



### Exhibit 4

- 14

. TRIM.FaTE 2,3,7, 8

- TCDD Concentrations in Fish and Calculated Bioaccumulation Factors with Respect to Total Water Concentration

Partitioning Behavior

Chlorinated dioxins have been observed to partition mostly to soil when released to the environment, and sorbed congeners are unlikely to leach or volatilize out of the soil profile. In soils with a high organic carbon content, congeners below the top few millimeters of the soil are very strongly adsorbed to organic matter and exhibit very little migration. Most dioxins deposited onto soil are expected to remain buried in the soil profile, and erosion of contaminated soil particles is the only significant mechanism for transport to water bodies.

Because of the hydrophobic nature of the 2,3,7,8-TCDD congener, and its affinity for organic carbon, 70 to 80 percent of the congener is expected to bind to suspended organic particles in natural waters. The remainder in the water column is associated with dissolved organic substances (ASTDR 1998). Because most of the dioxins in water are in a sorbed state, the ultimate fate of most congener-laden particles is in the bed sediment. For the RTR screening scenario, more than 99.5 percent of 2,3,7,8-TCDD in the pond compartment was found in the sediment. The percentages of 2,3,7 ,8 -TCDD in sorbed and dissolved states in surface water, sediment, and soil are presented in Exhibit 4- 15 . Also, because 2,3,7,8-TCDD is lipophilic, it readily partitions to breast milk.

The partitioning behavio r exhibited 2,3,7,8-TCDD in TRIM.FaTE is consistent with observed trends. In the surface water compartment, approximately 75 percent of 2,3,7,8-TCDD was present in the sorbed state, which is within the reported 70- 80 percent range reported in the literatu re . In the sediment and soil compartments, 100 percent of the congener is in the sorbed state, which is representative of the strong preference of dioxins for adsorption to soil and sediment organic matter.Appendix 5 59 

### Exhibit 4

- 15

. Fraction of 2,3,7,8

- TCDD Mass Sorbed vs. Dissolved

in TRIM.FaTE Compartments Compartment Sorbed Dissolved

Surface Soil 100.0% 0.0%

Surface Water 75.1% 24.9%

Sediment 100.0% 0.0%



### Concentrations in Ingestible Products

The primary source of non-inhalation exposure to dioxins outside of occupational settings is through dietary intake, which accounts for over 90 percent of daily dioxin intake (ATSDR 1998). Available data indicate that dioxins concentrate in plants, aquatic organisms, and animals, offering multiple ingestion exposure pathways

. However, actual congener levels in ingestible products can vary based upon type of food, agricultural and cultivation practices, atmospheric deposition rates, conditions in environmental media, and presence of other anthropogenic pollutants. Dioxins appear to enter the terrestrial food chain primarily through vapor phase deposition onto plant surfaces, which are then consumed by larger animals. Another major source of exposure to dioxins is through ingestion of contaminated soil by animals.

Observed trends indicate that meat, dairy, and fish are the dominant exposure pathways, comprising 90 percent of dioxin dietary intake (ATSDR 1998). Though concentrations in vegetables are generally exceptionally low, root vegetables normally contain slightly higher concentrations of dioxins than vegetables that are affected primarily by atmospheric deposition, such as lettuce and peas (ATSDR 1998). The 2,3,7,8-TCDD concentrations in ingestible product compartments are displayed in Exhibit 4- 16

. Data for concentrations of dioxin congeners in ingestible products are not abundant and sophisticated analytical instruments with sufficiently sensitive limits of detection were not widely available for older studies, which likely resulted in a greater number of nondetects in samples. As a result, the data available for comparison were limited. Overall, modeled concentrations of 2,3,7,8-TCDD in ingestible products were slightly lower than the available dioxin TEQ values ( Exhibit 4- 16 ). Given the conservative nature of the ingestion rates used in the screening assessment, the modeled values are not unreasonable. Consistent with the literature, the modeled concentration in the fish compartment for the screening scenario was at least one order of magnitude greater than concentrations in the other compartments. Among the compartments with the lowest concentrations were fruits and vegetables, which do not readily accumulate 2,3,7,8-TCDD

. The percent contributions of ingestion exposure pathways to the lifetime ADD are displayed in Ingestion of breast milk during infancy and fish ingestion contribute to nearly all (99%) of lifetime dioxin exposure in the screening scenario. Daily intakes of 2,3,7,8- TCDD from cow‘s milk, produce, and fish have been reported in the literature to comprise 27 percent, 11 percent, and 10 percent, respectively, of the total daily intake in the general population. However, some studies note that specific subpopulations, such as subsistence farmers and fishers, may have very different exposure profiles in which fish, meat, and dairy drive congener exposure (ATSDR 1998). Given the subsistence diet modeled in the RTR screening scenario, the high exposure from consumption of fish are appropriate within the context of this analysis.

Exhibit 4- 17Appendix 5 60



### Exhibit 4

- 16

. Summary of Modeled 2, 3,7,8

- TCDD Concentrations and Observed Total Dioxin TEQ Concentrations in Ingestible Media

*except for soil, which is expressed as mg/kg dry weight.

a Source: Exposure and Human Health Reassessment of 2,3,7,8

- Tetrachlorodibenzo

- p

- Dioxin (TCDD) and Re lated Compounds ( EPA 2004b ) b Source: Toxicological Profile for Chlorinated Dibenzo

- p

- dioxins (ATSDR 1998)Appendix 5 61



### Ingestion of breast milk during infancy and fish ingestion contribute to nearly all (99%) of lifetime dioxin exposure in the screening scenario. D aily intakes of 2,3,7,8

- TCDD from cow‘s milk, produce, and fish have been reported in the literature to comprise 27 percent, 11 percent, and 10 percent, respectively, of the total daily intake in the general population. However, some studies note that spe cific subpopulations, such as subsistence farmers and fishers, may have very different exposure profiles in which fish, meat, and dairy drive congener exposure (ATSDR 1998). Given the subsistence diet modeled in the RTR screening scenario, the high exposu re from consumption of fish are appropriate within the context of this analysis.

Exhibit 4

- 17

. Contribution of Modeled Food Types to 2,3,7,8

- TCDD Ingestion Exposures (mg/kg/day)

4.3.3.4 PAHs (Benzo[a]pyrene)

Behavior in the Environment

Emissions of POMs are often reported in terms of unspeciated or partially speciated groups, such as total PAHs, because they are often found in the environment as mixtures of two or more compounds exhibiting comparable behavior and toxicity

. Because there are relatively few data concerning the behavior and toxicity of individual PAH compounds, EPA has proposed assigning a relative potency factor to PAHs based on the relative toxicity of these compounds to the most carcinogenic PAH compound(s) (EPA 1993). Like TEFs, this allows for risks from exposure to certain PAH compounds that are likely carcinogens to be determined relative to the toxicity of other PAH compounds that have been identified as probable carcinogens. Benzo[a]pyrene, a high molecular weight PAH identified by EPA as a probable carcinogenic compound (possibly the most potent carcinogen of the PAH group), was used to represent PAH s in the screening scenario. A relative potency factor of 1 has been proposed by EPA forAppendix 5 62



### this compound (EPA 1993). However, because the relative potency index has not been widely adopted by the scientific community, modeled concentrations of benzo[a]pyrene are mostly compared to reported concentrations of this species, rather than to total PAHs

. Data for benzo[a]pyrene comprises much of the available exposure information on carcinogenic PAHs for the last few decades

. PAHs can enter the atmosphere as a result of a variety of combustion processes, both natural and anthropogenic. Based upon reviewed literature, stationary emission sources account for approximately 80 percent of total annual PAH emissions. Though the primary producer of stationary source PAH emissions is thought to be residential wood burning, other processes such as power generation; incineration; coal tar, coke, and asphalt production; and petroleum catalytic cracking are also major contributors (ASTDR 1995). PAHs emitted to the atmosphere can travel long distances in vapor form or attached to particles, or they can deposit relatively close to an emission source via wet or dry deposition onto water, soil, and vegetation

. In the atmosphere, PAHs are found primarily in the particle-bound phase, and atmospheric residence time and transport distances are highly influenced by climatic conditions and the size of the particles to which they are bound (ASTDR 1995).

As a result of sustained input from anthropogenic combustion sources and other sources, PAHs are ubiquitous in soil. Like other high molecular weight PAHs, benzo[a]pyrene strongly adsorbs to organic carbon in soil, indicating that adsorption to soil particles will limit the mobility of these compounds following deposition to soil. Most PAHs enter the water column directly through atmospheric fallout (ASTDR 1995). Following deposition onto surface waters, approximately two-thirds of PAHs adsorb strongly to sediment and suspended particles, while only small amounts revolatilize back to the atmosphere (ASTDR 1995). Aquatic organisms may accumulate PAHs via uptake of water, sediment, or food. Though fish and other organisms readily take up PAHs from contaminated food, biomagnification generally does not occur because many organisms are capable of rapidly metabolizing them (ASTDR 1995). As a result, concentrations of PAHs have generally been observed to decrease with increasing trophic levels (ASTDR 1995). Based upon observed data, bioaccumulation factors in fish are also not expected to be especially high because fish are able to readily metabolize the compound. BCF s in the range of 10-10,000 have been reported for fish and crustaceans, with the higher end of the range attributable to greater accumulation of the higher molecular weight compounds, such as benzo[a]pyrene (ASTDR 1995). Higher BCFs have also been observed in species at lower trophic levels

. Additionally, sediment-dwelling organisms may experience increased exposure to PAHs through association (e.g., direct uptake and/or consumption) with contaminated sediment (ASTDR 1995).

Emission Profile

The benzo[a]pyrene threshold emission rate used for the RTR screening scenario is 3.6 0E

- 04 TPY or 0.89 g/day

(based on lifetime cancer risk of 1- in -a-million)

. Although the annual concentration from year 50 is used for comparison, modeled concentrations benzo[a]pyrene either reached a steady state or had begun to level off in all compartments by year 10

.Appendix 5 63



### Concentrations in Environmental Media

Measured ranges of benzo[a]pyrene (and occasionally PAH -group concentrations) in environmental media are presented in Exhibit 4- 18 with concentrations from the screening scenario. Modeled concentrations and BAFs in fish compartments are shown in Exhibit 4- 19

. The benzo[a]pyrene concentrations output by the RTR screening scenario were consistently lower than values reported in the literature. Three main factors likely contributed to this trend. These are the high background values resulting from ubiquitous nature of PAHs in the environment, limited availability of benzo[a]pyrene-specific data, and use of conservative exposure factors to calculate the screening threshold

. Firstly, due to the quantity of PAHs that are emitted from mobile sources (~20 percent), as well as stationary synthetic and natural sources, PAHs are typically present in the environment at relatively high background levels.

The concentrations output from the screening scenario consider only emissions from a single facility. As a result, it is not unreasonable that some of the TRIM.FaTE outputs were several orders of magnitude smaller than those reported in the literature, as background exposure will be higher than incremental exposure. Secondly, though measured data for benzo[a]pyrene were used when available, concentrations in many media were available only for groups of PAHs or total PAHs. Thus, those ranges are not representative of benzo[a]pyrene alone and may contain values that are higher

—and ranges that are wider

—than those for a single chemical. Thirdly, it should be noted that in order to maintain a health-protective approach to screening emissions, a collection of moderately conservative exposure factors were used, which likely resulted in low, but not implausible values. For these reasons, we believe that the TRIM.FaTE outputs for concentrations of benzo[a]pyrene in environmental media are within the range of plausible values for this chemical. However, because of this discrepancy between the reported data and the screening scenario outputs, further investigation is necessary regarding site-appropriate biotransfer factors for facilities that do not pass the screen as a result of PAH emissions.

The screening scenario BAFs for benzo[a]pyrene in fish compartments were consistent with trends reported in the literature. No biomagnification of this chemical was exhibited in the fish compartments in the screening scenario, and the highest concentration of benzo[a]pyrene was in the zooplankton compartment, which represents the lowest trophic level evaluated in th e scenario.Appendix 5 64 

### Exhibit 4

- 18

. Summary of Modeled and Observed Concentrations of Benzo[a]pyrene in Environmental Media

* Source of literature data : ATSDR Toxicological Profile for Polycyclic Aromatic Com pounds (PAHs) (ATSDR 1995)

. Data are for benzo[a]pyrene (BaP) exclusively, unless otherwise noted

.Appendix 5 65



### Partitioning Behavior Data suggest that benzo[a]pyrene partitions mainly to soil (82 percent) and sediment (~ 17 percent) following deposition to a 1 km 2 

### area adjacent to an emission source (ASTDR 1995). Once in soil, PAHs can volatilize, undergo abiotic or biotic degradation, accumulate in plants, or remain sorbed to soil organic matter. High molecular weight PAHs, such as benzo[a]pyrene, tend to adsorb more strongly to organic carbon than PAHs having lower molecular weights (ASTDR 1995). As a result of this affinity for organic carbon, volatilization is not an important loss mechanism for benzo[a]pyrene from soils (ASTDR 1995). Because of its low solubility and affinity for organic carbon, most benzo[a]pyrene is expected to be particle- bound in natural waters. Le ss than one-third of PAHs in aquatic systems are generally present in the dissolved phase (ASTDR 1995). The remainder may be associated with suspended particles in the water column or particles that have settled on the bed sediment. Because most of the benzo[a]pyrene found in natural water is in a sorbed state, the ultimate fate of most contaminant-laden particles is burial in the bed sediment. For the RTR screening scenario, approximately 99 percent of benzo[a]pyrene in the pond compartment partitioned to the benthic sediment. The percentage of benzo[a]pyrene in sorbed and dissolved states in soil, surface water, and sediment are presented in Exhibit 4- 20

. Exhibit 4

- 19

. TRIM.FaTE Benzo[a]Pyrene Concentrations in Fish and Calculated Bioaccumulation Factors wit h Respect to Total Water ConcentrationAppendix 5 66 

### Exhibit 4

- 20

. Fraction of Benzo[a]Pyrene Mass Sorbed vs.

Dissolved in TRIM.FaTE Compartments Compartment Sorbed Dissolved

Surface Soil 100.0% 0.0%

Surface Water 30.7% 69.3%

Sediment 100.0% 0.0%



### The partitioning behavior of benzo[a]pyrene in the screening scenario is generally consistent with trends reported in the literature. The presence of this chemical in the sorbed state in the soil and sediment compartments is consistent with reported trends. A different trend was observed in the surface water compartment where more of the chemical was estimated by TRIM.FaTE to be dissolved. The dissolved concentration in TRIM.FaTE is affected by suspended sediment concentration, organic carbon content, and suspended sediment deposition and resuspension rates. Additional evaluation may be required to determine the specific factors affecting this behavior.

Concentrations in Ingestible Products

The primary source of non-inhalation exposure to benzo[a]pyrene outside of occupational settings is through dietary intake. Exposure may depend equally on the origin of the food (higher values often recorded at contaminated sites) and the method of food preparation (higher values reported for food that is smoked or grilled). PAHs have been observed to bioaccumulate in aquatic organisms and terrestrial animals through uptake of contaminated water, soil, and food. However, these compounds are readily metabolized by higher trophic level organisms, including humans, so biomagnification is not considered to be significant (ASTDR 1995). Plants accumulate PAHs primarily through atmospheric deposition, but chemical concentrations tend to be below detection levels. In general, grains and cereals may contain slightly higher concentrations of benzo[a]pyrene than fruits and vegetables. PAHs in meat have also been observed at concentrations below detection levels up to higher concentrations when the meat is smoked. Similar concentrations have been reported for fish, with smoked fish concentrations sometimes quadruple those found in terrestrial animals. Because PAH concentrations are highest in products that are smoked or grilled, most of the available data for benzo[a]pyrene in food is for products that have been prepared using these processes. As a result, reported values may be significantly higher than those output by MIRC. Measured concentrations of benzo[a]pyrene in ingestible products are presented in Exhibit 4- 21 along with RTR screening scenario concentrations.

The RTR screening scenario concentrations were generally lower than the reported ranges for benzo[a]pyrene in ingestible products. This trend is likely the result of background exposure in reported measurements and available data that is skewed toward concentrations in highly contaminated products. Considering these mitigating factors, the RTR screening scenario output concentrations are within the range of plausible values for benzo[a]pyrene in ingestible products. The percent contributions of ingestion exposure pathways to the lifetime ADD for benzo[a]pyrene are displayed in Exhibit 4- 22

. For the screening scenario, ingestion of fish drives human exposure to benzo[a]pyrene, but all media contribute a small amount to total exposure.Appendix 5 67



### Exhibit 4

- 21

. Summary of Modeled and Observed Concentrations of Benzo[a]pyrene in Ingestible Media

* except for soil, which is expressed as mg/kg dry weight

a Source: Hazardous Substances Databank Record for Benzo[a]pyren e (HSDB 2005c)
b Source: Analysis of 200 Food items for Benzo[a]pyrene and Estimation of its In take in an Epidemiologic Study ( Kazerouni et al. 2001)

c Source: ATSDR Toxicological Profile for Polycyclic Aromatic Compounds (PAHs) (ATSDR 1995)Appendix 5 68



### Exhibit 4

- 22

. Contribution of Modeled Food Types to Benzo[a]pyrene

Ingestion Exposures (mg/kg/day)

4.3.4 Summary

This analysis compared outputs from the RTR screening scenario (using screening threshold emission values) to observed data reported in the literature for cadmium, mercury, 2,3,7,8- TCDD, and benzo[a]pyrene. In general, most results from TRIM.FaTE appear to be reasonable for a screening modeling approach based on this comparison to measured values

. Briefly, the results of the evaluation are as follows:

Cadmium: Modeled concentrations in environmental media and ingestible products and behavior with respect to partitioning and bioaccumulation appear to be reasonable.

Mercury: Modeled concentrations in environmental media are comparable to levels for contaminated sites, and modeled concentrations in ingestible products are generally consistent with reported values

. Speciation of mercury appears to be consistent with observed patterns in the environment.

2,3,7,8-TCDD : Modeled concentrations in environmental media and ingestible products are slightly lower than reported values, but still within a reasonable range

. Both modeled values and measured values were primarily located in the noise around the limit of detection, which increases the uncertainty of the data.

Benzo[a]pyrene: Modeled concentrations in both environmental media and ingestible products are generally lower than those reported in the literature, in some cases by several orders of magnitude. Because this chemical is found in the environment atbackground levels that would far exceed concentrations resulting from single facilityemissions, a comparison to measured concentrations is not as informative for this chemical.Appendix 5 69



### Note that the exposure factors driving farm food chain ingestion rates are also conservative, and that these parameters were not considered in this evaluation, meaning that the ―actual‖ concentration associated with a given risk level (if such a value could be calculated) would be higher than the level associated with the modeled screening threshold emission rate. Also, even ―correct‖ model results may mask incorrect model assum ptions that combine to produce compensating errors. Where results differ significantly from reported values, such as with benzo[a]pyrene, a more detailed investigation of underlying assumptions may be necessary to determine appropriate adjustments to the scenario configuration. As noted in the overview of this section, this type of evaluation cannot be used to verify model results.Appendix 5 70



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### Technical Support Document for TRIM-Based Multipathway Screenin g Scenario for RTR: Summary of Approach and Evaluatio n



# ATTACHMENT 1: TRIM.FaTE Inputs

### [This page intentionally left blank.]

Attachment 1 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 1-i

### TABLE OF CONTENT S

1 TRIM.FaTE Inputs

.................................................................................................................. 1

1.1 Introduction

........................................................................................................................ 1

Exhibit 1. TRIM.FaTE Simulation Parameters

............................................................................ 2

Exhibit 2. Meteorological Inputs

................................................................................................ . 3

Exhibit 3. Air Parameters

.......................................................................................................... 4

Exhibit 4. Soil and Groundwater Parameters

............................................................................. 5

Exhibit 5. Runoff Assumptions

.................................................................................................. 8

Exhibit 6. USLE Erosion Parameters

......................................................................................... 9

Exhibit 7. Terrestrial Plant Placement

....................................................................................... 1 0

Exhibit 8. Terrestrial Plant Parameters

..................................................................................... 1 1

Exhibit 9. Surface Water Parameters

....................................................................................... 1 3

Exhibit 10 . Sediment Parameters

............................................................................................. 1 4

Exhibit 11 . Aquatic Plant Parameters

....................................................................................... 1 5

Exhibit 12 . Aquatic Animals Food Chain, Density, and Mass

.................................................... 1 6

Exhibit 13 . Cadmium Chemical-Specific

................................................................................... 1 7

Exhibit 14 . Mercury Chemical-Specific Properties

.................................................................... 1 8

Exhibit 15

. PAH Chemical-Specific Properties

.......................................................................... 1 9

Exhibit 16 . Dioxin Chemical-Specific Properties

....................................................................... 2 0

Exhibit 17 . Cadmium Chemical-Specific Properties for Abiotic Compartments

......................... 2 3

Exhibit 18 . Mercury Chemical-Specific Properties for Abiotic Compartments

........................... 2 4

Exhibit 19

. PAH Chemical-Specific Properties for Abiotic Compartments

................................ .2 8

Exhibit 20 . Dioxin Chemical-Specific Properties for Abiotic Compartments

............................... 3 0

Exhibit 21 . Cadmium Chemical-Specific Properties for Plant Compartments

........................... 3 4

Exhibit 22 . Mercury Chemical-Specific Properties for Plant Compartments

.............................. 3 5

Exhibit 23

. PAH Chemical-Specific Properties for Plant Compartments

................................... 3 7

Attachment 1 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 1- ii

### Exhibit 24 . Dioxin Chemical-Specific Properties for Plant Compartments

................................ .3 8

Exhibit 25 . Cadmium Chemical-Specific Properties for Aquatic Species

.................................. 3 9

Exhibit 26 . Mercury Chemical-Specific Properties for Aquatic Species

..................................... 4 0

Exhibit 27

. PAH Chemical-Specific Properties for Aquatic Specie s

.......................................... 4 1

Exhibit 28. Dioxin Chemical-Specific Properties for Aquatic Species

........................................ 4 2

Attachment 1 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 1- iii

## 1 TRIM.FaTE Inputs

1.1 Introduction
This attachment provides the tables of the detailed modeling inputs for the TRIM.FaTE screening scenario. Exhibit 1 presents runtime settings for TRIM.FaTE. Exhibits 2 and 3 present air parameters entered into the model. Exhibits 3 through 8 present the terrestrial parameters. Exhibits 9 through 12 pr esent the lake parameters, and 13 through 28 present the chemical specific parameters.

Attachment 1 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 1-1Exhibit 1. TRIM.FaTE Simulation Parameters for the TRIM.FaTE Screening Scenario

Parameter Name Units Value Used Reference

Start of simulation date/time 1/1/1990, midnight Consistent with met data.

End of simulation date/time 1/1/2040, midnight Consistent with met data set; selected to provide a 50-year modeling period. Simulation time step hr 1 Selected value.
Output time step a hr 4 Selected value.

a Output time step is set in TRIM.FaTE using the scenario properties "simulationStepsPerOutputStep" and "simulationTimeStep."Exhibit 2. Meteorlogical Input s for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Used Reference Meteorological Inputs (all TRIM.FaTE scenario properties, except mixing height)
Air temperature degrees K 298 USEPA 2005.

Horizontal wind speed m/sec 2.8 5th percentile annual average value for contiguous US, calculated from 30 yrs of annual normal temperature values.

Vertical wind speed m/sec 0.0 Professional judgment; vertical wind speed not used by any of the algorithms in the version of the TRIM.FaTE library used for screening.

Wind direction degrees clockwise from N (blowing from) 3-days-on 4-days-off On is defined as time during which wind is blowing into the model domain. A conservative estimate of time during which wind should blow into the modeling domain was determined by evaluating HUSWO; it was concluded that a conservative estimate would be approximately 42% of the time.

Rainfall Rate m 3 [rain]/m 2 [surface area]-day varies daily 1.5 m/yr is the maximum statewide 30-year (1971-2000) average for the contiguous United States, excluding Rhode Island because of extreme weather conditions on Mt. Washington. Data obtained from the National Climatic Data Center at http://www.ncdc.noaa.gov/oa/climate/online/ccd/nrmpcp.txt. The precipitation frequency was 3-days-on:4-days-off based on data from Holzworth, 1972.

Mixing height (used to set air VE property named “top”) m 710 5th percentile annual average mixing heights (calculated from daily morning and afternoon values), for all stations on SCRM (40 state, 70 stations).

isDay_SteadyState_forAir unitless

-­ Value not used in current dynamic runs (would need to be reevaluated if steady-state runs are needed). isDay_SteadyState_forOther unitless

-­Exhibit 3. Air Parameter s for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Used Reference
Atmospheric dust load kg[dust]/m 3 [air] 6.15E-08 Bidleman 1988

Density of air g/cm 3 0.0012 U.S. EPA 1997

Dust density kg[dust]/m 3 [dust] 1,400 Bidleman 1988

Fraction organic matter on particulates unitless 0.2 Harner and Bidleman 1998

Height m 800 5th percentile for United States

### Exhibit 4. Soil and Groundwater Parameters for the TRIM.FaTE Screening Scenario

Parameter Name Units Value Used Reference Surface Soil Compartment Type
Air content volume[air]/volume[compartment] 0.28 McKone et al. 2001. Average vertical velocity of water (percolation) m/day 8.22E-04 Assumed to be 0.2 times average precipitation for site. Boundary layer thickness above surface soil m 0.005 Thibodeaux 1996; McKone et al. 2001 (Table 3). Density of soil solids (dry weight) kg[soil]/m 3 [soil] 2600 Default in McKone et al. 2001 (Table 3)

Thickness - untilled a m 0.01 McKone et al. 2001 (p. 30).

Thickness - tilled a m 0.20 USEPA 2005.
Erosion fraction [Link property] unitless varies b See Erosion and Runoff Fraction table. Fraction of area available for erosion m 2 [area available]/m 2 [total] 1 Professional judgment; area assumed rural. Fraction of area available for runoff m 2 [area available]/m 2 [total] 1 Professional judgment; area assumed rural. Fraction of area availabe for vertical diffusion m 2 [area available]/m 2 [total] 1 Professional judgment; area assumed rural.

Fraction Sand unitless 0.25 Professional judgment.

Organic carbon fraction unitless 0.008 U.S. average in McKone et al. 2001 (Table 16 and A-3).
pH unitless 6.8 Professional judgment.
Runoff fraction [Link property] unitless varies b See Erosion and Runoff Fraction table.

Total erosion rate kg [soil]/m 2 /day varies b See Total Erosion Rates table.

Total runoff rate m 3 [water]/m 2 /day 1.64E-03 Calculated using scenario-specific precipitation rate and assumptions associated with water balance.

Water content volume[water]/volume[compartment] 0.19 McKone et al 2001 (Table 15).

### Exhibit 4. Soil and Groundwater Parameters for the TRIM.FaTE Screening Scenario

Parameter Name Units Value Used Reference Root Zone Soil Compartment Type

Air content volume[air]/volume[compartment] 0.25 McKone et al 2001 (Table 16).

Average vertical velocity of water (percolation) m/day 8.22E-04 Assumed as 0.2 times average precipitation for New England in McKone et al. 2001. Density of soil solids (dry weight) kg[soil]/m 3 [soil] 2,600 McKone et al. 2001 (Table 3).

Fraction Sand unitless 0.25 Professional judgment.

Thickness - untilled a m 0.79 McKone et al. 2001 (Tabel 16 - U.S. Average).

Thickness - tilled a m 0.6 Adjusted from McKone et al. 2001 (Table 16).
Organic carbon fraction unitless 0.008 McKone et al. 2001 (Table 16 and A3, U.S. Average).
pH unitless 6.8 Professional judgment.

Water content volume[water]/volume[compartment] 0.21 McKone et al. 2001 (Table 16).
Vadose Zone Soil Compartment Type

Air content volume[air]/volume[compartment] 0.22 McKone et al. 2001 (Table 17).

Average vertical velocity of water (percolation) m/day 8.22E-04 Assumed as 0.2 times average precipitation for New England in McKone et al. 2001. Density of soil solids (dry weight) kg[soil]/m 3 [soil] 2,600 Default in McKone et al. 2001 (Table 3).

Fraction Sand unitless 0.35 Pofessional judgment.

Thickness a m 1.4 McKone et al. 2001 (Table 17).

Organic carbon fraction unitless 0.003 McKone et al. 2001 (Table 16 and A3, U.S. Average).
pH unitless 6.8 Professional judgment.

Water content volume[water]/volume[compartment] 0.21 McKone et al. 2001 (Table 17 ­ national average).

### Exhibit 4. Soil and Groundwater Parameters for the TRIM.FaTE Screening Scenario

Parameter Name Units Value Used Reference Ground Water Compartment Type

Thickness a m 3 McKone et al. 2001 (Table 3).

Fraction Sand unitless 0.4 Professional judgment.

Organic carbon fraction unitless 0.004 Professional judgment.

pH unitless 6.8 Professional judgment.

Porosity volume[total pore space]/volume[compartment] 0.2 Default in McKone et al. 2001 (Table 3). Density of Solid material in aquifer kg[soil]/m 3 [soil] 2,600 Default in McKone et al. 2001 (Table 3).

a Set using the volume element properties file

b See separate tables for erosion/runoff fractions and total erosion rates.

### Exhibit 5. Runoff Assumption s for the TRIM.FaTE Screening Scenari o
Originating Compartment Destination Compartment Runoff/Erosion Fraction

SurfSoil_Source SurfSoil_N1 0.0 SurfSoil_S1 0.0 sink 1.0

SurfSoil_N1 SW_Pond 1.0 SurfSoil_Source 0.0

SurfSoil_N6 0.0 SurfSoil_S1 0.0
sink 0.0

SurfSoil_S1 SW_Pond 1.0 SurfSoil_Source 0.0

SurfSoil_N1 0.0 sink 0.0

SurfSoil_N6 SW_Pond 1.0 SurfSoil_N1 0.0 SurfSoil_N7 0.0 sink 0.0

SurfSoil_N7 SW_Pond 1.0 SurfSoil_N6 0.0 SurfSoil_N3 0.0 sink 0.0

SurfSoil_N3 SW_Pond 1.0 SurfSoil_N7 0.0 SurfSoil_N4 0.0 sink 0.0

SurfSoil_N4 SW_Pond 1.0 SurfSoil_N3 0.0 SurfSoil_N5 0.0 SurfSoil_S4 0.0 sink 0.0

SurfSoil_S4 SW_Pond 1.0 SurfSoil_N4 0.0 SurfSoil_S5 0.0 sink 0.0

SurfSoil_N5 a SW_Pond 0.0 SurfSoil_N4 0.5 SurfSoil_S5 0.5 sink 0.0

SurfSoil_S5 a SW_Pond 0.0 SurfSoil_N5 0.0 SurfSoil_S4 1.0 sink 0.0

a Assumes that N5 is higher ground that S5, and half of the runoff flows into N4, and the other half in S5. Assumes all runoff from S5 flows into S4.

### Exhibit 6. USLE Erosion Parameters for the TRIM.FaTE Screening Scenario

Soil Parcel Area Rainfall/ Erosivity

Index Soil Erodibility Index LengthSlope Factor Land Use Cover Mgmt Factor Supporting Practices

Factor Unit Soil Loss Sediment Delivery

Ratio a Calculated (Adjusted) Erosion Rate

m 2 R (100 ftton/ac) K(ton/ac/(100 ftton/acre)) LS (USCS) type C (USCS) P A (ton/ac/yr) A (kg/m 2 /d) SDR a calculated (adjusted) erosion rate

(kg/m 2 /d) N1 5.8E+04 300 0.39 1.5 grass 0.1 1 17.55 0.010779 0.533 0.005740 N6 4.1E+04 300 0.39 1.5 crops 0.2 1 35.1 0.021557 0.557 0.012014 N7 7.3E+04 300 0.39 1.5 grass 0.1 1 17.55 0.010779 0.518 0.005580 N3 3.5E+05 300 0.39 1.5 grass 0.1 1 17.55 0.010779 0.385 0.004151 N4 2.0E+06 300 0.39 1.5 forest 0.1 1 17.55 0.010779 0.309 0.003331 N5 6.7E+06 300 0.39 1.5 forest 0.1 1 17.55 0.010779 0.196 0.002116 S1 5.8E+04 300 0.39 1.5 grass 0.1 1 17.55 0.010779 0.533 0.005740 S4 2.0E+06 300 0.39 1.5 forest 0.1 1 17.55 0.010779 0.309 0.003331 S5 6.7E+06 300 0.39 1.5 forest 0.1 1 17.55 0.010779 0.196 0.002116

a Calculated using SD = a * (AL) -b ; where a is the empirical intercept coefficient (based on the size of the watershed), AL is the total watershed area receiving deposition (m 2 ), and b is the empirical slope coefficient (always 0.125).

### Exhibit 7. Terrestial Plant Placement for the TRIM.FaTE Screening Scenario

Surface Soil Volume Element Surface Soil Depth (m) Coniferous Forest Grasses/ Herbs None

Source 0.01 x

N1 0.01 x N6 0.20 (tilled) N7 0.01 x N3 0.01 x N4 0.01 x N5 0.01 x S1 0.01 x S4 0.01 x S5 0.01 x

### Exhibit 8. Terrestrial Plant Parameters for the TRIM.FaTE Screening Scenario

Parameter Name Units Coniferous a Grass/Herb a
Value Used Reference Value Used Reference 

### Leaf Compartment Type Allow exchange 1=yes, 0=no 1

- seasonal b

- Average leaf area index m 2 [leaf]/ m 2 [area] 5.0 Harvard Forest, dom. red oak and red maple, CDIAC website 5.0 Mid-range of 4-6 for old fields, R.J. Luxmoore, ORNL. Calculate wet dep interception fraction (boolean) 1=yes, 0=no 0 Professional judgment. 0 Professional judgment.

Correction exponent, octanal to lipid unitless 0.76 From roots, Trapp 1995. 0.76 From roots, Trapp 1995.

Degree stomatal opening unitless 1 Set to 1 for daytime based on professional judgment (stomatal diffusion is turned off at night using a different property, IsDay). 1 Set to 1 for daytime based on professional judgment (stomatal diffusion is turned off at night using a different property, IsDay). Density of wet leaf kg/m 3 820 Paterson et al. 1991. 820 Paterson et al. 1991.

Leaf wetting factor m 3.00E-04 1E-04 to 6E-04 for different crops and elements, Muller and Prohl 1993. 3.00E-04 1E-04 to 6E-04 for different crops and elements, Muller and Prohl 1993.
Length of leaf m 0.01 Professional judgment. 0.05 Professional judgment. Lipid content kg/kg wet weight 0.00224 European beech, Riederer 1995. 0.00224 European beech, Riederer 1995.

Litter fall rate 1/day 0.0021 value assumes 1st-order relationship and that 99% of leaves fall over 6
years seasonal c

-

Stomatal area normalized effective diffusion path length 1/m 200 Wilmer and Fricker 1996. 200 Wilmer and Fricker 1996.

Vegetation attenuation factor m 2 /kg 2.9 Grass/hay, Baes et al. 1984. 2.9 Grass/hay, Baes et al. 1984.

Water content unitless 0.8 Paterson et al. 1991. 0.8 Paterson et al. 1991.

Wet dep interception fraction unitless 0.2 Calculated based on 5 years of local met data, 1987-1991. 0.2 Calculated based on 5 years of local met data, 1987-1991.

Wet mass of leaf per soil area kg[fresh leaf]/m 2 [area] 2.0 Calculated from leaf area index, leaf thickness (Simonich & Hites, 1994), density of wet foliage. 0.6 Calculated from leaf area index and Leith 1975.


### Particle on Leaf Compartment Type Allow exchange 1=yes, 0=no 1

- seasonal b

-

### Exhibit 8. Terrestrial Plant Parameters for the TRIM.FaTE Screening Scenario

Parameter Name Units Coniferous a Grass/Herb a
Value Used Reference Value Used Reference

Volume particle per area leaf m 3 [leaf particles]/m 2 [leaf] 1.00E-09 Based on particle density and size distribution for atmospheric particles measured on an adhesive surface, Coe and Lindberg 1987. 1.00E-09 Based on particle density and size distribution for atmospheric particles measured on an adhesive surface, Coe and Lindberg 1987. 

### Root Compartment Type - Nonwoody Only Allow exchange 1=yes, 0=no seasonal b

- Correction exponent, octanol to lipid unitless 0.76 Trapp 1995.
Lipid content of root kg/kg wet weight 0.011 Calculated. Water content of root kg/kg wet weight 0.8 Professional judgment. Wet density of root kg/m 3 820 Soybean, Paterson et al. 1991.

Wet mass per soil area kg/m 2 1.4 Temperate grassland, Jackson et al. 1996. 

### Stem Compartment Type - Nonwoody Only Allow exchange 1=yes, 0=no seasonal b

- Correction exponent, octanol to lipid unitless 0.76 Trapp 1995
Density of phloem fluid kg/m 3 1,000 Professional judgment. Density of xylem fluid kg/cm 3 900 Professional judgment. Flow rate of transpired water per leaf area m 3 [water]/m 2 [leaf] 0.0048 Crank et al. 1981.
Fraction of transpiration flow rate that is phloem rate unitless 0.05 Paterson et al. 1991.

Lipid content of stem kg/kg wet weight 0.00224 Leaves of European beech, Riederer 1995.
Water content of stem unitless 0.8 Paterson et al. 1991 Wet density of stem kg/m 3 830 Professional judgment.

Wet mass per soil area kg/m 2 0.24 Calculated from leaf and root biomass density based on professional judgment.

a See separate table for assignment of plant types to surface soil compartments.

b Begins March 9 (set to 1), ends November 7 (set to 0). Nation-wide 80th percentile

. Begins November 7, ends December 6; rate = 0.15/day during this time (value assumes 99 percent of leaves fall in 30 days)

. c

### Exhibit 9. Surface Water Parameters for the TRIM.FaTE Screening Scenario

Parameter Name Units Value Used Reference
Algae carbon content (fraction) unitless 0.465 APHA 1995.

Algae density in water column g[algae]/L[water] 0.0025 Millard et al. 1996 as cited in ICF 2005.

Algae growth rate 1/day 0.7 Hudson et al. 1994 as cited in Mason et al. 1995b Algae radius um 2.5 Mason et al. 1995b.

Algae water content (fraction) unitless 0.9 APHA 1995.
Average algae cell density (per vol cell, not water) g[algae]/m 3 [algae] 1,000,000 Mason et al. 1995b, Mason et al. 1996. Boundary layer thickness above sediment m 0.02 Cal EPA 1993.

Chloride concentration mg/L 8.0 Kaushal et al. 2005.
Chlorophyll concentration mg/L 0.0029 ICF 2005.

Depth a m 3.18 WI DNR 2005 - calculation based on relationship between drainage basin and lake area size.

Dimensionless viscous sublayer thickness unitless 4 Ambrose et al. 1995.

Drag coefficient for water body unitless 0.0011 Ambrose et al. 1995.

Flush rate 1/year 12.17 Calculated based on pond dimensions and flow calculations.

Fraction Sand unitless 0.25 Professional judgment.
Organic carbon fraction in suspended sediments unitless 0.02 Professional judgment.

pH unitless 7.3 Professional judgment. Suspended sediment deposition velocity m/day 2 USEPA 1997.
Total suspended sediment concentration kg[sediment]/m3[water column] 0.05 USEPA 2005.

Water temperature degrees K 298 USEPA 2005.

a Set using the volume element properties named "top" and "bottom."

### Exhibit 10. Sediment Parameter s for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Used Reference

Depth a m 0.05 McKone et al. 2001 (Table 3).

Fraction Sand unitless 0.25 Professional judgment.

Organic carbon fraction unitless 0.02 McKone et al. 2001 (Table 3).

Porosity of the sediment

zone volume[total pore space]/volume[sediment compartment] 0.6 USEPA 1998.

Solid material density in sediment kg[sediment]/m 3 [sediment] 2,600 McKone et al. 2001 (Table 3).

a Set using the volume element properties named "top" and "bottom."

### Exhibit 11. Aquatic Plant s for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Used Reference Macrophyte biomass per water area kg/m 2 0.5 Professional judgment. Density of macrophytes kg/L 1 Professional judgment.

### Exhibit 12. Aquatic Animals Food Chain, Density, and Mass for the TRIM.FaTE Screening Scenario

Aquatic Biota (Consuming

Organism) Fraction Diet

Biomass (g/m 2 ) Body Weight ReferenceAlgaeMacrophyteZooplanktonBethicInvertebrateWaterColumnPlanktivoreBenthicOmnivoreWaterColumnOmnivoreBenthicCarnivoreWaterColumnCarnivore

Algae 0% 0% 0% 0% 0% 0% 0% 0% 0% 7.95

-­ Professional judgment Macrophyte 0% 0% 0% 0% 0% 0% 0% 0% 0% 500

-­ Professional judgment Zooplankton 100% 0% 0% 0% 0% 0% 0% 0% 0% 6.36 5.70E-08 Professional judgment
Benthic Invertebrate 0% 0% 0% 0% 0% 0% 0% 0% 0% 20 2.55E-04 Professional judgment
Water Column Planktivore 0% 0% 100% 0% 0% 0% 0% 0% 0% 2 0.025 Professional judgment
Benthic Omnivore 0% 0% 0% 100% 0% 0% 0% 0% 0% 2 0.25 Professional judgment
Water Column Omnivore 0% 0% 0% 0% 100% 0% 0% 0% 0% 0.5 0.25 Professional judgment
Benthic Carnivore 0% 0% 0% 50% 0% 50% 0% 0% 0% 1 2 Professional judgment
Water Column Carnivore 0% 0% 0% 0% 0% 0% 100% 0% 0% 0.2 2 Professional judgment

### Exhibit 13. Cadmium Chemical-Specific Propertie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name a Units Value Reference

CAS number b unitless 7440-43-9

-

Diffusion coefficient in pure air m 2 [air]/day 0.71 USEPA 1999 (Table A-2­ 35).
Diffusion coefficient in pure water m 2 [water]/day 8.16E-05 USEPA 1999 (Table A-2­ 35).

Henry's Law Constant Pa-m 3 /mol 1.00E-37 USEPA 1999 (Table A-2-35; assumed to be zero).

Melting point degrees K 594 ATSDR 1999.

Molecular weight g/mol 112.41 ATSDR 1999.

Octanol-air partition coefficient (Koa) m3[air]/m3[octanol]

- -
Octanol-carbon partition coefficient (Koc) - -
Octanol-water partition coefficient (Kow) L[water]/kg[octanol]

- -

a All parameters in this table are TRIM.FaTE chemical properties

. b These CAS numbers apply to elemental Cd; however, the cations of cadmium are being modeled

.

### Exhibit 14. Mercury Chemical-Specific Propertie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference Hg(0) b Hg(2) b MHg b

CAS number unitless 7439-97-6 14302-87-5 22967-92-6

- Diffusion coefficient in pure air m 2 [air]/day 0.478 0.478 0.456 USEPA 1997.

Diffusion coefficient in pure water m 2 [water]/day 5.54E-05 5.54E-05 5.28E-05 USEPA 1997.

Henry's Law constant Pa-m 3 /mol 719 7.19E-05 0.0477 USEPA 1997.

Melting Point degrees K 234 5.50E+02 443 CARB 1994.

Molecular weight g/mol 201 201 216 USEPA 1997.

Octanol-water partition coefficient (Kow) L[water]/kg[octanol] 4.15 3.33 1.7 Mason et al. 1996.

Vapor washout ratio m 3 [air]/m 3 [rain] 1,200 1.6E+06 0 USEPA 1997, based on Petersen et al. 1995.

a All parameters in this table are TRIM.FaTE chemical properties.

b On this and all following tables, Hg(0) = elemental mercury, Hg(2) = divalent mercury, and MHg = methyl mercury.

### Exhibit 15. PAH Chemical-Specific Propertie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference BaP BaA BbF BkF Chr DahA IcdP

CAS number unitless 50-32-8 56-55-3 205-99-2 207-08-9 218-01-9 53-70-3 193-39-5

-

Diffusion coefficient in pure air m 2 /day 0.188 0.213 0.197 0.197 0.214 0.156 0.164 USEPA 1998.

Diffusion coefficient in pure water m 2 /day 5.05E-05 5.37E-05 4.74E-05 4.74E-05 5.37E-05 5.19E-05 4.89E-05 USEPA 1998.

Henry's Law constant Pa-m 3 /mol 8.50E-02 3.67E-01 6.26E-01 4.20E-02 1.23E-01 1.13E-03 4.92E-04 USEPA 1998.

Melting point degrees K 452 433 441 490 531 539 437 Budavari 1996.

Molecular weight g/mol 252.32 228.29 252.32 252.32 228.29 278.33 276.34 Budavari 1996.

Octanol-water partition coefficient (Kow) L[water]/L[octanol] 9.33E+05 6.17E+05 3.98E+06 6.92E+06 5.37E+05 3.16E+06 4.57E+07 Hansch et al. 1995.

### Exhibit 16. Dioxin Chemical-Specific Propertie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value1,2,3,4,6,7,8,9­OCDD1,2,3,4,6,7,8,9­OCDF1,2,3,4,6,7,8­HpCDD1,2,3,4,6,7,8­HpCDF1,2,3,4,7,8,9­HpCDF1,2,3,4,7,8­HxCDD1,2,3,4,7,8­HxCDF

CAS number unitless 3268-87-9 39001-02-0 35822-46-9 67562-39-4 55673-89-7 39227-28-6 70648-26-9

Diffusion coefficient in pure air m 2 /day 0.0883 0.123 0.0925 0.129 0.129 0.0958 0.135

Diffusion coefficient in pure water m 2 /day 3.08E-06 3.15E-05 3.24E-05 3.33E-05 3.33E-05 3.43E-05 3.53E-05

Henry's Law constant Pa-m 3 /mol 0.68 0.19 1.28 1.43 1.43 1.08 1.45

Melting Point degrees K 603 259 538 236.5 222 546 499.0

Molecular weight g/mol 460.0 443.76 425.2 409.31 409.31 391.0 374.87

Octanol-water partition coefficient (Kow) L[water]/L[octanol] 1.58E+08 1.00E+08 1.00E+08 2.51E+07 7.94E+06 6.31E+07 1.00E+07

### Exhibit 16. Dioxin Chemical-Specific Propertie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value1,2,3,6,7,8­HxCDD1,2,3,6,7,8­HxCDF1,2,3,7,8,9­HxCDD1,2,3,7,8,9­HxCDF1,2,3,7,8­PeCDD1,2,3,7,8­PeCDF2,3,4,6,7,8­HxCDF

CAS number unitless 57653-85-7 57117-44-9 19408-74-3 72918-21-9 40321-76-4 57117-41-6 60851-34-5

Diffusion coefficient in pure air m 2 /day 0.0958 0.135 0.0958 0.135 0.101 0.142 0.135

Diffusion coefficient in pure water m 2 /day 3.43E-05 3.53E-05 3.43E-05 3.53E-05 3.65E-05 3.76E-05 3.53E-05

Henry's Law constant Pa-m 3 /mol 1.08 0.74 1.08 0.74 3.33 0.5 0.74

Melting point degrees K 558.0 506.0 517.0 509.0 513.0 499.0 512.5

Molecular weight g/mol 390.84 374.9 390.8 374.9 356.4 340.4 374.9

Octanol-water partition coefficient (Kow) L[water]/L[octanol] 1.62E+08 8.24E+07 1.62E+08 3.80E+07 4.37E+06 6.17E+06 8.31E+07

### Exhibit 16. Dioxin Chemical-Specific Propertie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value

Reference2,3,4,7,8­PeCDF2,3,7,8-TCDD2,3,7,8-TCDF

CAS number unitless 57117-31-4 1746-01-6 51207-31-9

-

Diffusion coefficient in pure air m 2 /day 0.142 0.106 0.149 USEPA 1999.

Diffusion coefficient in pure water m 2 /day 3.76E-05 5.68E-05 4.04E-05 USEPA 1999.

Henry's Law constant Pa-m 3 /mol 0.5 3.33 1.46 Mackay et al. 1992 as cited in USEPA 2000a. Exceptions include 1,2,3,4,6,7,8,9-OCDF; 1,2,3,4,7,8-HxCDF; and 1,2,3,6,7,8-HxCDF which are calculated by the VP/WS Ratio Technique (USEPA 2000a)

Melting point degrees K 469.3 578.0 500.0 Mackay et al. 2000, exceptions include USEPA 2000b (1,2,3,6,7,8­ HxCDD; 1,2,3,7,8,9-HxCDF; 1,2,3,7,8--PeCDD), ATSDR 1998(1,2,3,6,7,8­ HxCDF; 1,2,3,7,8-PeCDF; 2,3,4,6,7,8-HxCDF) and NLM 2002 (1,2,3,7,8,9­ HxCDD)

Molecular weight g/mol 340.4 322.0 306.0 Mackay et al. 2000, exceptions include: ATSDR 1998(1,2,3,6,7,8-HxCDF; 1,2,3,7,8,9-HxCDF; 1,2,3,7,8-PeCDD; 1,2,3,7,8-PeCDF; 2,3,4,6,7,8­

HxCDF) and NLM 2002 (1,2,3,6,7,8-HxCDD; 1,2,3,7,8,9-HxCDD)

Mackay et al. 1992a as cited in USEPA 2000a, exceptions include: Octanol-water partition USEPA 2000b (1,2,3,6,7,8-HxCDD; 1,2,3,6,7,8-HxCDF; 1,2,3,7,8,9­ L[water]/L[octanol] 3.16E+06 6.31E+06 1.26E+06 coefficient (Kow) HxCDD; 1,2,3,7,8,9-HxCDF; 2,3,4,6,7,8-HxCDF) and Sijm et al. 1989 (1,2,3,7,8-PeCDD)

### Exhibit 17. Cadmium Chemical-Specific Properties for Abioti c Compartments Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference
Air Compartment Type

Particle dry deposition velocity m/day 260 Calculated from Mulbaier and Tisue 1980.

Washout Ratio m3[air]/m3[rain] 200,000 MacKay et al. 1986.

Surface Soil Compartment Type
Use input characteristic depth (boolean) 0 = no, Else = yes 0 Professional judgment.

Root Zone Soil Compartment Type
Use input characteristic depth (boolean) 0 = no, Else = yes 0 Professional judgment.

Vadose Zone Soil Compartment Type
Use input characteristic depth (boolean) 0 = no, Else = yes 0 Professional judgment.

Surface Water Compartment Type

Ratio of concentration in water to concentration in algae to concentration dissolved in water L[water]/g[algae wet wt] 1.87 McGeer et al. 2003.

### Exhibit 18. Mercury Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference Hg(0) Hg(2) MHg Air Compartment Type Particle dry deposition velocity m/day 500 500 500 CalTOX value cited in McKone et al. 2001. Demethylation rate 1/day N/A N/A 0 Professional judgment. Methylation rate 1/day 0 0 0 Professional judgment.

Oxidation Rate 1/day 0.00385 0 0 Low end of half-life range (6 months to 2 years) in USEPA 1997. Reduction rate 1/day 0 0 0 Professional judgment. Washout Ratio m3[air]/m3[rain] 200,000 200,000 200,000 Professional judgment. Surface Soil Compartment Type Input characteristic depth (user supplied) m 0.08 0.08 0.08 Not used (model set to calculate value).
Use input characteristic depth (boolean) 0 = no, Else = yes 0 0 0 Professional judgment.

Soil-water partition coefficient L[water]/kg[soil wet wt] 1,000 58,000 7,000 USEPA 1997.

Vapor dry deposition velocity m/day 50 2500 0 Hg(0) - from Lindberg et al. 1992 Hg(2) - estimate by USEPA using the Industrial Source Complex (ISC) Model - [See Vol. III, App. A of the Mercury Study Report (USEPA, 1997)].

Demethylation rate 1/day N/A N/A 0.06 Range reported in Porvari and Verta 1995 is 3E-2 to 6E-2 /day; value is average maximum potential demethylation rate constant under anaerobic conditions.

Methylation rate 1/day 0 0.001 0 Range reported in Porvari and Verta 1995 is 2E-4 to 1E-3 /day; value is average maximum potential methylation rate constant under anaerobic conditions. Oxidation rate 1/day 0 0 0 Value assumed in USEPA 1997.

Reduction rate 1/day 0 1.25E-05 0 Value used for untilled surface soil (2cm), 10% moisture content, in USEPA 1997; general range is (0.0013/day)*moisture content to (0.0001/day)*moisture content for forested region (Lindberg 1996; Carpi and Lindberg 1997).

### Exhibit 18. Mercury Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference Hg(0) Hg(2) MHg Root Zone Soil Compartment Type Input characteristic depth (user supplied) m 0.08 0.08 0.08 Not used (model set to calculate value).
Use input characteristic depth (boolean) 0 = no, Else = yes 0 0 0 Professional judgment.

Soil-water partition coefficient L[water]/kg[soil wet wt] 1,000 58,000 7,000 USEPA 1997

Demethylation rate 1/day N/A N/A 0.06 Range reported in Porvari and Verta 1995 is 3E-2 to 6E-2 /day; value is average maximum potential demethylation rate constant under anaerobic conditions.

Methylation rate 1/day 0 0.001 0 Range reported in Porvari and Verta 1995 is 2E-4 to 1E-3 /day; value is average maximum potential methylation rate constant under anaerobic conditions. Oxidation rate 1/day 0 0 0 Value assumed in USEPA 1997.

Reduction rate 1/day 0 3.25E-06 0 Value used for tilled surface soil (20cm), 10% moisture content, in USEPA 1997 (Lindberg 1996; Carpi and Lindberg, 1997). Vadose Zone Soil Compartment Type Input characteristic depth (user supplied) m 0.08 0.08 0.08 Not used (model set to calculate value),
Use input characteristic depth (boolean) 0 = no, Else = yes 0 0 0 Professional judgment.

Soil-water partition coefficient L[water]/kg[soil wet wt] 1,000 58,000 7,000 USEPA 1997.

Demethylation rate 1/day N/A N/A 0.06 Range reported in Porvari and Verta 1995 is 3E-2 to 6E-2 /day; value is average maximum potential demethylation rate constant under anaerobic conditions.

Methylation rate 1/day 0 0.001 0 Range reported in Porvari and Verta 1995 is 2E-4 to 1E-3 /day; value is average maximum potential methylation rate constant under anaerobic conditions. Oxidation rate 1/day 0 0 0 Value assumed in USEPA 1997.

Reduction rate 1/day 0 3.25E-06 0 Value used for tilled surface soil (20cm), 10% moisture content, in USEPA 1997 (Lindberg 1996; Carpi and Lindberg, 1997).

### Exhibit 18. Mercury Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference Hg(0) Hg(2) MHg Ground Water Compartment Type
Soil-water partition coefficient L[water]/kg[soil wet wt] 1,000 58,000 7,000 USEPA 1997.

Demethylation rate 1/day N/A N/A 0.06 Range reported in Porvari and Verta 1995 is 3E-2 to 6E-2 /day; value is average maximum potential demethylation rate constant under anaerobic conditions.

Methylation rate 1/day 0 0.001 0 Range reported in Porvari and Verta 1995 is 2E-4 to 1E-3 /day; value is average maximum potential methylation rate constant under anaerobic conditions.

Oxidation rate 1/day 1.00E-08 0 0 Small default nonzero value (0 assumed in USEPA 1997).

Reduction rate 1/day 0 3.25E-06 0 Value used for tilled surface soil (20cm), 10% moisture content, in USEPA 1997 (Lindberg 1996; Carpi and Lindberg 1997). Surface Water Compartment Type
Algal surface area-specific uptake rate constant nmol/[μm 2 -daynmol] 0 2.04E-10 3.60E-10 Assumes radius = 2.5mm, Mason et al. 1995b, Mason et al. 1996; Hg(0) assumed same as Hg(2).

Dow ("overall Kow") L[water]/kg[octan ol] 0

- a

- b Mason et al. 1996.

Solids-water partition coefficient L[water]/kg[solids wet wt] 1,000 100,000 100,000 USEPA 1997.
Vapor dry deposition velocity m/day N/A 2500 USEPA 1997 (Vol. III, App. A).
Demethylation rate 1/day N/A N/A 0.013 Average of range of 1E-3 to 2.5E-2/day from Gilmour and Henry 1991.
Methylation rate 1/day 0 0.001 0 Value used in EPA 1997; range is from 1E-4 to 3E4/day (Gilmour and Henry 1991). Oxidation rate 1/day 0 0 0 Professional judgment.

Reduction rate 1/day 0 0.0075 0 Value used in USEPA 1997; reported values range from less than 5E-3/day for depths greater than 17m, up to 3.5/day (Xiao et al. 1995; Vandal et al. 1995; Mason et al. 1995a; Amyot et al. 1997).

### Exhibit 18. Mercury Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference Hg(0) Hg(2) MHg Sediment Compartment Type
Solids-water partition coefficient L[water]/kg[solids wet wt] 3,000 50,000 3,000 USEPA 1997.

Demethylation rate 1/day N/A N/A 0.5 Value based on Lake Waccamaw, NC in Knightes, et al, 2009.
Methylation rate 1/day 0 0.02 0 Value based on Lake Waccamaw, NC in Knightes, et al, 2009. Oxidation rate 1/day 0 0 0 Professional judgment.

Reduction rate 1/day 0 1.00E-06 0 Inferred value based on presence of Hg(0) in sediment porewater (USEPA 1997; Vandal et al. 1995).

a TRIM.FaTE Formula Property, which varies from 0.025 to 1.625 depending on pH and chloride concentration.

b TRIM.FaTE Formula Property, which varies from 0.075 to 1.7 depending on pH and chloride concentration.

### Exhibit 19. PAH Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference BaP BaA BbF BkF Chr DahA IcdP Air Compartment Type Particle dry deposition velocity m/day 500 500 500 500 500 500 500 McKone et al. 2001.

Half-life day 0.046 0.125 0.596 0.458 0.334 0.178 0.262 Howard et al. 1991 / upper bound measured or estimated value. Washout Ratio 200,000 200,000 200,000 200,000 200,000 200,000 200,000 Mackay et al. 1986. Surface Soil Compartment Type
Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 0.08 0.08 Not used (model set to calculate value).
Use input characteristic depth (boolean) 0 = No, Else = Yes 0 0 0 0 0 0 0 Professional judgment.

Halflife day 530 680 610 2140 1000 940 730 MacKay et al. 2000. Root Zone Soil Compartment Type
Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 0.08 0.08 Not used (model set to calculate value).
Use input characteristic depth 0 = No, Else = Yes 0 0 0 0 0 0 0 Professional judgment.

Half-life day 530 680 610 2140 1000 940 730 MacKay et al. 2000. Vadose Zone Soil Compartment Type
Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 0.08 0.08 Not used (model set to calculate value).
Use input characteristic depth (boolean) 0 = No, Else = Yes 0 0 0 0 0 0 0 Professional judgment.

Half-life day 1060 1360 1220 4280 2000 1880 1460 Howard et al. 1991 / upper bound measured or estimated value for groundwater. Groundwater Compartment Type

Half-life day 1060 1360 1220 4280 2000 1880 1460 Howard et al. 1991 / upper bound measured or estimated value for groundwater.

### Exhibit 19. PAH Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference BaP BaA BbF BkF Chr DahA IcdP Surface Water Compartment Type RatioOfConcInAlgaeToConc DissolvedInWater (g[chem]/kg[algae]) / (g[chem]/L[water]) 3610 3610 3610 3610 3610 3610 3610 BCF data for green algae for BaP from Lu et al. 1977

Half-life day 0.138 0.375 90 62.4 1.626 97.8 750 Howard et al. 1991 / upper bound measured or estimated value. Sediment Compartment Type

Half-life day 2290 2290 2290 2290 2290 2290 2290 Mackay et al. 1992 / PAH values are the mean half-life of the log class that Mackay et al. assigned for sediment, except for BbF and IcdP, which were not on Table 2.3.

### Exhibit 20. Dioxin Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value1,2,3,4,6,7,8,9-OCDD1,2,3,4,6,7,8,9-OCDF1,2,3,4,6,7,8­HpCDD1,2,3,4,6,7,8­HpCDF1,2,3,4,7,8,9­HpCDF1,2,3,4,7,8­HxCDD



### Air Compartment Type Deposition Velocity m/day 500 500 500 500 500 500

Half-life day 162 321 64 137 122 42

Washout Ratio m 3 [air]/m 3 [rain] 91000 22000 64000 32000 32000 9000 

### Surface Soil Compartment Type Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 0.08 Use input characteristic depth (boolean) 0 = No, Else = Yes 0 0 0 0 0 0

Half-life day 3650 3650 3650 3650 3650 3650 

### Root Zone Soil Compartment Type Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 0.08
Use input characteristic depth 0 = No, Else = Yes 0 0 0 0 0 0

Half-life day 3650 3650 3650 3650 3650 3650 

### Vadose Zone Soil Compartment Type Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 0.08 Use input characteristic depth (boolean) 0 = No, Else = Yes 0 0 0 0 0 0

Half-life day 1008 1008 1008 1008 1008 1008 

### Groundwater Compartment Type
Half-life day 1008 1008 1008 1008 1008 1008 

### Surface Water Compartment Type Ratio Of Conc In Algae To Conc Dissolved In Water (g[chem]/g[algae])/ (g[chem]/L[water]) 1.025 1.025 1.025 1.025 1.025 1.025

Half-life day 0.67 0.58 47 0.58 0.58 6.3 

### Sediment Compartment Type Half-life day 1095 1095 1095 1095 1095 1095

### Exhibit 20. Dioxin Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value1,2,3,4,7,8­HxCDF1,2,3,6,7,8­HxCDD1,2,3,6,7,8­HxCDF1,2,3,7,8,9­HxCDD1,2,3,7,8,9­HxCDF1,2,3,7,8­PeCDD



### Air Compartment Type Deposition Velocity m/day 500 500 500 500 500 500

Halflife day 78 28 55 28 51 18

Washout Ratio m 3 [air]/m 3 [rain] 10000 9000 10000 9000 10000 18000 

### Surface Soil Compartment Type Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 0.08 Use input characteristic depth (boolean) 0 = No, Else = Yes 0 0 0 0 0 0

Halflife day 3650 3650 3650 3650 3650 3650 

### Root Zone Soil Compartment Type Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 0.08
Use input characteristic depth 0 = No, Else = Yes 0 0 0 0 0 0

Halflife day 3650 3650 3650 3650 3650 3650 

### Vadose Zone Soil Compartment Type Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 0.08 Use input characteristic depth (boolean) 0 = No, Else = Yes 0 0 0 0 0 0

Halflife day 1008 1008 1008 1008 1008 1008 

### Groundwater Compartment Type
Half-life day 1008 1008 1008 1008 1008 1008 

### Surface Water Compartment Type Ratio Of Conc In Algae To Conc Dissolved In Water (g[chem]/g[algae])/ (g[chem]/L[water]) 1.025 1.025 1.025 1.025 1.025 1.025

Half-life day 0.58 6.3 0.58 6.3 0.58 2.7 

### Sediment Compartment Type Half-life day 1095 1095 1095 1095 1095 1095

### Exhibit 20. Dioxin Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value1,2,3,7,8­PeCDF2,3,4,6,7,8­HxCDF2,3,4,7,8­PeCDF2,3,7,8­TCDD2,3,7,8­TCDF



### Air Compartment Type Deposition Velocity m/day 500 500 500 500 500

Halflife day 31 59 33 12 19

Washout Ratio m 3 [air]/m 3 [rain] 13000 10000 14000 18000 19000 

### Surface Soil Compartment Type Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 Use input characteristic depth (boolean) 0 = No, Else = Yes 0 0 0 0 0

Halflife day 3650 3650 3650 3650 3650 

### Root Zone Soil Compartment Type Input characteristic depth m 0.08 0.08 0.08 0.08 0.08
Use input characteristic depth 0 = No, Else = Yes 0 0 0 0 0

Halflife day 3650 3650 3650 3650 3650 

### Vadose Zone Soil Compartment Type Input characteristic depth m 0.08 0.08 0.08 0.08 0.08 Use input characteristic depth (boolean) 0 = No, Else = Yes 0 0 0 0 0

Halflife day 1008 1008 1008 1008 1008 

### Groundwater Compartment Type
Half-life day 1008 1008 1008 1008 1008 

### Surface Water Compartment Type Ratio Of Conc In Algae To Conc Dissolved In Water (g[chem]/g[algae])/ (g[chem]/L[water]) 1.025 1.025 1.025 1.025 1.025

Half-life day 0.19 0.58 0.19 2.7 0.18 

### Sediment Compartment Type Half-life day 1095 1095 1095 1095 1095

### Exhibit 20. Dioxin Chemical-Specific Properties for Abiotic Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Reference



### Air Compartment Type Deposition Velocity McKone et al. 2001

Halflife Atkinson 1996 as cited in USEPA 2000; vapor phase reaction with hydroxyl radical
Washout Ratio Vulykh et al. 2001 

### Surface Soil Compartment Type Input characteristic depth Not used (model set to calculate value)
Use input characteristic depth (boolean) Professional judgment

Halflife Mackay et al. 2000; the degradation rate was cited by multiple authors, 

### Root Zone Soil Compartment Type Input characteristic depth not used (model set to calculate value)
Use input characteristic depth professional judgment

Halflife Mackay et al. 2000; the degradation rate was cited by multiple authors, 

### Vadose Zone Soil Compartment Type Input characteristic depth Not used (model set to calculate value).
Use input characteristic depth (boolean) Professional judgment.

Halflife Average value of the range presented in Mackay et al. 2000; based on 

### Groundwater Compartment Type
Half-life Average value of the range presented in Mackay et al. 2000; based on 

### Surface Water Compartment Type Ratio Of Conc In Algae To Conc Dissolved In Water BCF data for green algae for 2,3,7,8-TCDD from Isense 1978, at 32 days. Half-life Kim and O’Keefe. 1998, as cited in USEPA. 2000. 

### Sediment Compartment Type Half-life Estimation based on Adriaens and Grbic-Galic 1992,1993 and

### Exhibit 21. Cadmium Chemical-Specific Properties for Plant Compartment s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference 

### Leaf Compartment Type
Transfer factor to leaf particle 1/day 0.002 Professional judgment. 

### Particle on Leaf Compartment Type
Transfer factor to leaf 1/day 0.200 Professional judgment. 

### Root Compartment Type - Grasses and Herbs a
Root to Root Soil Partition- Alpha of Steady State unitless 0.95 Henning et al. 2001.

Root to Root Soil Partition- Partitioning Coefficient m 3 [bulk root soil]/m 3 [root] 0.23 Nriagu 1980; based on average value calculated from various agricultural plant species. Root to Root Soil Partition- Time to Reach Alpha day 28 Henning et al. 2001.



### Stem Compartment Type - Grasses and Herbs a
Transpiration stream concentration factor (TSCF) m 3 [soil pore water]/m 3 [xylem fluid] 0.45 Tsiros et al. 1999.



### Aquatic Plants Macrophyte Compartment Type
Water ColumnDissolved PartitionAlpha of Equilibrium unitless 0.95 Maine et al. 2001; based on assumption that equilibrium was nearly reached during 21 day experiment. Water ColumnDissolved PartitionPartition Coefficient L[water]/kg[macrop hyte wet wt] 100 Maine et al. 2001; based on calculations from an average of four macrophyte species.

Water ColumnDissolved PartitionTime to Reach Equilibrium day 21 Maine et al. 2001.

a Roots and stems are not modeled for deciduous or coniferous forest in the current version of TRIM.FaTE.

### Exhibit 22. Mercury Chemical-Specific Properties for Plant Compartments Documentation for the TRIM.FaT E Screening Scenari o

Parameter Name Units Value Reference Hg(0) Hg(2) MHg 

### Leaf Compartment Type

Transfer factor to leaf particle 1/day 0.002 0.002 0.002 Professional judgment (assumed 1% of transfer factor from leaf particle to leaf).
Demethylation rate 1/day N/A N/A 0.03 Calculated from Bache et al. 1973.

Methylation rate 1/day 0 0 0 Assumed from Gay 1975, Bache et al. 1973.

Oxidation rate 1/day 1.0E+06 0 0 Professional judgment; assumed close to instantaneous

Reduction rate 1/day 0 0 0 Professional judgment. 

### Particle on Leaf Compartment Type

Transfer factor to leaf 1/day 0.2 0.2 0.2 Professional judgment.

Demethylation rate 1/day N/A N/A 0 Professional judgment.

Methylation rate 1/day 0 0 0 Professional judgment.

Oxidation rate 1/day 0 0 0 Professional judgment.

Reduction rate 1/day 0 0 0 Professional judgment. 

### Root Compartment Type - Grasses and Herbs a

Alpha for root-root zone bulk soil unitless 0.95 0.95 0.95 Selected value.

Root/root-zone-soil-water partition coefficient m 3 [bulk root soil]/

m 3 [root] 0 0.18 1.2 Hg2- geometric mean Leonard et al. 1998,John 1972, Hogg et al. 1978; MHgassumed, based on Hogg et al. 1978. t-alpha for root-root zone bulk soil day 21 21 21 Professional judgment.

Demethylation rate 1/day N/A N/A 0 Professional judgment.

Methylation rate 1/day 0 0 0 Professional judgment.

Oxidation rate 1/day 0 0 0 Professional judgment.

Reduction rate 1/day 0 0 0 Professional judgment.

### Exhibit 22. Mercury Chemical-Specific Properties for Plant Compartments Documentation for the TRIM.FaT E Screening Scenari o

Parameter Name Units Value Reference Hg(0) Hg(2) MHg 

### Stem Compartment Type - Grasses and Herbs a
Transpiration stream concentration factor (TSCF) m 3 [soil pore water]/

m 3 [xylem fluid] 0 0.5 0.2 Calculation from Norway spruce, Scots pine, Bishop et al. 1998.

Demethylation rate 1/day N/A N/A 0.03 Calculated from Bache et al. 1973.

Methylation rate 1/day 0 0 0 Professional judgment.

Oxidation rate 1/day 0 0 0 Professional judgment.

Reduction rate 1/day 0 0 0 Professional judgment. 

### Aquatic Plants Macrophyte Compartment Type Water Column Dissolved Partition-Alpha of Equilibrium unitless 0.95 0.95 0.95 Selected value.

Water Column Dissolved PartitionPartition Coefficient L[water]/ kg[macrophyte wet wt] 0.883 0.883 4.4 Elodea densa, Ribeyre and Boudou 1994.

Water Column Dissolved Partition-Time to Reach Equilibrium unitless 0.95 0.95 0.95 Selected value.

Oxidation rate 1/day 1.00E+09 0 0 Professional judgment.

t-alpha day 18 18 18 Experiment duration from Ribeyre and Boudou 1994.

a Roots and stems are not modeled for deciduous or coniferous forest in the current version of TRIM.FaTE.

### Exhibit 23. PAH Chemical-Specific Properties for Plant Compartments Documentation for the TRIM.FaTE Screenin g Scenari o

Parameter Name Units Value Reference BaP BaA BbF BkF Chr DahA IcdP 

### Terrestrial Plants Leaf Compartment Type
Transfer factor to leaf particle 1/day 1.00E-04 1.00E-04 1.00E-04 1.00E-04 1.00E-04 1.00E-04 1.00E-04 Professional judgment.

Half-life day 3.5 3.5 3.5 3.5 3.5 3.5 3.5 Edwards 1988 (as cited in Efroymson 1997)/ calculated from metabolic rate constant. 

### Particle on Leaf Compartment Type

Transfer factor to leaf 1/day 1.00E-04 1.00E-04 1.00E-04 1.00E-04 1.00E-04 1.00E-04 1.00E-04 Professional judgment.

Half-life day 2.31 1.84 3.56 17.8 4.12 17.8 17.8 Edwards 1988 (as cited in Efroymson 1997)/ calculated from metabolic rate constant 

### Root Compartment Type - Grasses and Herbs a

Half-life day 34.6 34.6 34.6 34.6 34.6 34.6 34.6 Edwards 1988 (as cited in Efroymson 1997)/ calculated from metabolic rate constant. 

### Stem Compartment Type - Grasses and Herbs a

Half-life day 3.5 3.5 3.5 3.5 3.5 3.5 3.5 Edwards 1988 (as cited in Efroymson 1997)/ calculated from metabolic rate constant. 

### Aquatic Plants Macrophyte Compartment Type

Half-life days 3.5 3.5 3.5 3.5 3.5 3.5 3.5 Edwards 1988 (as cited in Efroymson 1997)/ calculated from metabolic rate constant.

a Roots and stems are not modeled for deciduous or coniferous forest in the current version of TRIM.FaTE.

### Exhibit 24. Doixin Chemical-Specific Properties for Plant Compartments Documentation for th e TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference All Dioxins 

### Terrestrial Plants Leaf Compartment Type

Transfer factor to leaf particle 1/day 0.003 Calculated as 1 percent of transfer factor to leaf; highly uncertain.

Half-life day 70 Arjmand and Sandermann 1985, as cited in Komoba et al. 1995; soybean root cell culture metabolism test data for DDE. 

### Particle on Leaf Compartment Type

Transfer factor to leaf 1/day 0.3 Professional judgment based on USEPA 2000c (an estimate for mercury) and Trapp 1995; highly uncertain.

Half-life day 4.4 McCrady and Maggard 1993; photodegradation sorbed to grass foliage in sunlight; assumed 10 sunlight per day. 

### Root Compartment Type - Grasses and Herbs a

Half-life day 70 Arjmand and Sandermann 1985, as cited in Komoba, et al. 1995; soybean root cell culture metabolism test data for DDE.

Root Soil Water Interaction - Alpha unitless 0.95 Professional judgment.


### Stem Compartment Type - Grasses and Herbs a

Half-life day 70 Arjmand and Sandermann 1985, as cited in Komoba, et al. 1995; soybean root cell culture metabolism test data for DDE. 

### Aquatic Plants Macrophyte Compartment Type

Half-life days 70 Arjmand and Sandermann 1985, as cited in Komoba et al. 1995; soybean root cell culture metabolism test data for DDE.

a Roots and stems are not modeled for deciduous or coniferous forest in the current version of TRIM.FaTE.

### Exhibit 25. Cadmium Chemical-Specific Properties for Aquatic Specie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference 

### Zooplankton Compartment Type Assimilation efficiency from food unitless 0.5 Goulet et al, 2007 Absorption Rate Constant L/kg(ww)-day 1500 Goulet et al, 2007 Elimination Rate Constant /day 0.03 Mean of reported range from Goulet et al, 2007 

### Benthic Invertebrate Compartment Type Sediment Partitioning - Alpha of Equilibrium unitless 0.95 Professional judgment

Sediment Partitioning - Partition Coefficient kg[bulk sed/kg[inverteb

rate wet wt] 0.27 Professional judgment

Sediment Partitioning - Time to Reach Alpha of Equilibrium day 21 Hare et al. 2001

Absorption Rate Constant unitless 1.23 Calculated based on body weight from regression in Hendriks & Heikens 2000 Elimination Rate Constant unitless 2.82E-03 Professional judgment 

### Benthic Omnivore Compartment Type
Assimilation efficiency from food unitless 0.1 Professional judgment based on Yan and Wang 2002.

Absorption Rate Constant unitless 1.23E+00 Calculated based on body weight from regression in Hendriks & Heikens 2000 Elimination Rate Constant unitless 2.82E-03 Professional judgment 

### Benthic Carnivore Compartment Type
Assimilation efficiency from food unitless 0.1 Professional judgment based on Yan and Wang 2002.

Absorption Rate Constant unitless 6.60E-01 Calculated based on body weight from regression in Hendriks & Heikens 2000 Elimination Rate Constant unitless 1.68E-03 Professional judgment 

### Water-column Herbivore Compartment Type Assimilation efficiency from food unitless 0.1 Professional judgment based on Yan and Wang 2002. Assimilation efficiency from plants unitless 0.1 Professional judgment based on Yan and Wang 2002.

Absorption Rate Constant unitless 2.46 Calculated based on body weight from regression in Hendriks & Heikens 2000 Elimination Rate Constant unitless 5.02E-03 Professional judgment 

### Water-column Omnivore Compartment Type
Assimilation efficiency from food unitless 0.1 Professional judgment based on Yan and Wang 2002. Assimilation efficiency from plants unitless 0.1 Professional judgment based on Yan and Wang 2002.

Absorption Rate Constant unitless 1.2320207 Calculated based on body weight from regression in Hendriks & Heikens 2000 Elimination Rate Constant unitless 2.82E-03 Professional judgment 

### Water-column Carnivore Compartment Type
Assimilation efficiency from food unitless 0.1 Professional judgment based on Yan and Wang 2002.

Absorption Rate Constant unitless 0.6602235 Calculated based on body weight from regression in Hendriks & Heikens 2000 Elimination Rate Constant unitless 1.68E-03 Professional judgment

### Exhibit 26. Mercury Chemical-Specific Properties for Aquatic Specie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference Hg(0) Hg(2) MHg 

### Benthic Invertebrate Compartment Type Alpha of equilibrium for sediment partitioning unitless 0.95 0.95 0.95 Selected value.

Benthic invertebrate-bulk sediment partition coefficient kg[bulk sediment]/ kg [invertebrate wet wt] 0.0824 0.0824 5.04 Hg(0) - assumed based on Hg(2) value; Hg(2) and MHg - Saouter et al. 1991.

t-alpha for equilibrium for sediment partitioning day 14 14 14 Experiment duration from Saouter et al. 1991.
All Fish Compartments Types a

Elimination adjustment factor unitless 3 3 1 Trudel and Rasmussen 1997.

Assimilation efficiency from food unitless 0.06 0.06 b 0.5 c Professional judgment based on Trudel and Rasmussen 2001 & Muir, 1986. Demethylation rate 1/day N/A N/A 0 Professional judgment.
Methylation rate 1/day 0 0 0 Professional judgment.

Oxidation rate 1/day 1.0E+06 0 0 Professional judgment.

Reduction rate 1/day 0 0 0 Professional judgment. Water-column Herbivore Compartment Type Assimilation efficiency from plants unitless 1 1 1 Phillips and Gregory 1979. Water-column Omnivore Compartment Type

Assimilation efficiency from food unitless 1 1 1 Phillips and Gregory 1979.

a Screening scenario includes Algae, Macrophyte, Zooplankton, Benthic Invertebrates, Water-column Herbivore, Benthic Omnivore, Water-column Omnivore

, Benthic Carnivore, and Water-column Carnivor e b Zooplankton were assigned an assimilation efficiency of 0.2 for divalent mercury to compensate for the absence of naturally occurring direct diffusion processe s in the model

. c Water Column Carnivores were assigned an assimilation efficiency of 0.2 for methyl mercury to compensate absence of naturally occurring death , growth

, reproduction and predation processes in the scenario/model

.

### Exhibit 27. PAH Chemical-Specific Properties for Aquatic Specie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value Reference BaP BaA BbF BkF Chr DahA IcdP Zooplankton Compartment Type Assimilation efficiency from food unitless 0.43 0.43 0.43 0.43 0.43 0.43 0.43 Estimated from Arnot & Gobas, 2004

Absorption Rate Constant L/kg(ww)­ day 4.8E+05 4.8E+05 4.8E+05 4.8E+05 4.8E+05 4.8E+05 4.8E+05 Estimated from Muir, D.C.G., A.L. Yarechewski, A. Knoll, et al. 1986a Elimination Rate Constant /day 5.2E-01 5.2E-01 5.2E-01 5.2E-01 5.2E-01 5.2E-01 5.2E-01 Estimated from Kow Half Life day 16.5 16.5 16.5 16.5 16.5 16.5 16.5 Moermond, 2007. 

### Benthic Invertebrate Compartment Type

Clearance constant unitless 157.6 157.6 157.6 157.6 157.6 157.6 157.6 Stehly et al. 1990 / estimated for mayfly, 120-day-old nymphs. alpha of equilibrium for sediment partitioning unitless 0.95 0.95 0.95 0.95 0.95 0.95 0.95 Professional judgment.
talpha for equilibrium for sediment partitioning days 14 14 14 14 14 14 14 Professional judgment.

V d (ratio of concentration
in benthic invertebrates to concentration in water) ml/g 7235.0 7235.0 7235.0 7235.0 7235 7235 7235 Stehly et al. 1990 / estimated for mayfly, 120-day-old nymphs.

Half-life day 1.5 1.5 1.5 1.5 1.5 1.5 1.5 Stehly et al. 1990 / calculated from estimated elimination/depuration rateconstant estimated for mayfly, 120-dayold nymphs. 

### All Fish Compartment Types a Gamma_fish unitless 0.2 0.2 0.2 0.2 0.2 0.2 0.2 Thomann 1989. Assimilation efficiency from
food b unitless 1.0 1.0 1.0 1.0 1.0 1.0 1.0 Professional judgment.

Half-life day 2.8 2.8 2.8 2.8 2.8 2.8 2.8 Spacie et al. 1983, as cited in MacKay et al. 1992 (bluegill sunfish) for benzo(a)pyrene. 

### Benthic Omnivore Compartment Type Assimilation efficiency from plants b unitless 1.0 1.0 1.0 1.0 1.0 1.0 1.0 Professional judgment. 

### Water Column Omnivore Compartment Type Assimilation efficiency from plants b unitless 1.0 1.0 1.0 1.0 1.0 1.0 1.0 Professional judgment.

a Screening scenario includes: Benthic Omnivore, Benthic Carnivore, Water-column Herbivore, Water-column Omnivore, and Water-column Carnivore.

b All ingestion assimilation efficiencies set to 1 to be consistent with excretion rate calculations.

### Exhibit 28. Dioxin Chemical-Specific Properties for Aquatic Specie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value1,2,3,4,6,7,8,9-OCDD1,2,3,4,6,7,8,9-OCDF1,2,3,4,6,7,8­HpCDD1,2,3,4,6,7,8­HpCDF1,2,3,4,7,8,9­HpCDF1,2,3,4,7,8­HxCDD1,2,3,4,7,8­HxCDF1,2,3,6,7,8­HxCDD1,2,3,6,7,8­HxCDF



### Zooplankton Compartment Type

Assimilation efficiency from food unitless 0.41 0.41 0.41 0.41 0.41 0.41 0.41 0.41 0.41 Absorption Rate Constant L/kg(ww)/day 380 380 380 380 380 380 380 380 380

Elimination Rate Constant /day 5.5E-04 5.5E-04 5.5E-04 5.5E-04 5.5E-04 5.5E-04 5.5E-04 5.5E-04 5.5E-04
Half Life day 1.0E+09 1.0E+09 1.0E+09 1.0E+09 1.0E+09 1.0E+09 1.0E+09 1.0E+09 1.0E+09



### Benthic Invertebrate Compartment

Clearance constant unitless 0 0 0 0 0 0 0 0 0 Sediment Partitioning Partition Coefficient kg/kg 0.0013 0.0017 0.0055 0.0012 0.042 0.033 0.0081 0.013 0.02
Sediment Partitioning Alpha of Equilibrium unitless 0.95 0.95 0.95 0.95 0.95 0.95 0.95 0.95 0.95
Sediment Partitioning Time to Reach Alpha of Equilibrium days 120 42 120 42 42 120 42 120 42

V d (ratio of concentration
in benthic invertebrates to concentration in water) ml/g 0 0 0 0 0 0 0 0 0

Half-life day 5776.23 5776.23 5776.2 5776.23 5776.23 5776.23 5776.23 5776.23 5776.23 

### All Fish Compartments a

Assimilation efficiency from food unitless 0.03 0.03 0.5 0.5 0.5 0.5 0.5 0.5 0.5

Chemical Uptake Rate Via Gill L[water]/kg[fish wet wt]-day 142 N/A b 14 N/A b N/A b 127 N/A b 127 N/A b

Gamma_fish unitless N/A b 0.2 N/A b 0.2 0.2 N/A b 0.2 N/A b 0.2

Half-life day 693.147 346.574 346.57 346.574 346.574 495.105 495.105 495.105 495.105

### Exhibit 28. Dioxin Chemical-Specific Properties for Aquatic Specie s Documentation for the TRIM.FaTE Screening Scenari o
Parameter Name Units Value1,2,3,4,6,7,8,9-OCDD1,2,3,4,6,7,8,9-OCDF1,2,3,4,6,7,8-HpCDD1,2,3,4,6,7,8-HpCDF1,2,3,4,7,8,9-HpCDF1,2,3,4,7,8­HxCDD1,2,3,4,7,8­HxCDF1,2,3,6,7,8­HxCDD1,2,3,6,7,8­HxCDF



### Water Column Herbivore Compartment

Assimilation efficiency from plants unitless 0.03 0.03 0.5 0.5 0.5 0.5 0.5 0.5 0.5



### Water Column Omnivore Compartment

Assimilation efficiency from plants unitless 0.03 0.03 0.5 0.5 0.5 0.5 0.5 0.5 0.5

a Screening scenario includes: Benthic Omnivore, Benthic Carnivore, Water-column Herbivore, Water-column Omnivore, and Water-column Carnivore.

b N/A = not applicable. This parameter is used in calculating the uptake when measured data are unavailable.

### Exhibit 28. Dioxin Chemical-Specific Properties for Aquatic Specie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Value1,2,3,7,8,9­HxCDD1,2,3,7,8,9­HxCDF1,2,3,7,8­PeCDD1,2,3,7,8­PeCDF2,3,4,6,7,8­HxCDF2,3,4,7,8­PeCDF2,3,7,8­TCDD2,3,7,8­TCDF



### Zooplankton Compartment Type

Assimilation efficiency from food unitless 0.41 0.41 0.41 0.41 0.41 0.41 0.41 0.41

Absorption Rate Constant L/kg(ww)/day 380 380 380 380 380 380 380 380

Elimination Rate Constant /day 5.5E-04 5.5E-04 5.5E-04 5.5E-04 5.5E-04 5.5E-04 5.5E-04 5.5E-04

Half Life day 1.0E+09 1.0E+09 1.0E+09 1.0E+09 1.0E+09 1.0E+09 1.0E+09 1.0E+09



### Benthic Invertebrate Compartment

Clearance constant unitless 0 0 0 0 0 0 0 0 Sediment Partitioning Partition Coefficient kg/kg 0.015 0.067 0.098 0.024 0.072 0.17 0.205 0.056
Sediment Partitioning Alpha of Equilibrium unitless 0.95 0.95 0.95 0.95 0.95 0.95 0.95 0.95
Sediment Partitioning Time to Reach Alpha of Equilibrium days 120 42 120 42 42 42 120 42

V_d (ratio of concentration in benthic invertebrates to concentration in water) ml/g 0 0 0 0 0 0 0 0

Half-life day 5776.23 5776.23 5776.23 5776.23 5776.23 5776.23 5776.23 5776.23 

### All Fish Compartments a

Assimilation efficiency from food unitless 0.5 0.5 0.5 0.5 0.5 0.5 0.5 0.5

Chemical Uptake Rate Via Gill L[water]/kg[fish wet wt]-day 127 N/A b 700 N/A b N/A b N/A b 380 N/A b

Gamma_fish unitless N/A b 0.2 N/A b 0.2 0.2 0.2 N/A b 0.2

Half-life day 495.105 495.105 420.089 420.089 495.105 420.089 5251.12 5251.12

### Exhibit 28. Dioxin Chemical-Specific Properties for Aquatic Specie s Documentation for the TRIM.FaTE Screening Scenari o
Parameter Name Units Value1,2,3,4,6,7,8,9-OCDD1,2,3,4,6,7,8,9-OCDF1,2,3,4,6,7,8-HpCDD1,2,3,4,6,7,8-HpCDF1,2,3,4,7,8,9-HpCDF1,2,3,4,7,8­HxCDD1,2,3,4,7,8­HxCDF1,2,3,6,7,8­HxCDD



### Water Column Herbivore Compartment

Assimilation efficiency from plants unitless 0.5 0.5 0.5 0.5 0.5 0.5 0.5 0.5



### Water Column Omnivore Compartment

Assimilation efficiency from plants unitless 0.5 0.5 0.5 0.5 0.5 0.5 0.5 0.5

a Screening scenario includes: Benthic Omnivore, Benthic Carnivore, Water-column Herbivore, Water-column Omnivore, and Water-column Carnivore. b N/A

b N/A = not applicable. This parameter is used in calculating the uptake when measured data are unavailable.

### Exhibit 28. Dioxin Chemical-Specific Properties for Aquatic Specie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Reference



### Zooplankton Compartment Type

Assimilation efficiency from food unitless Morrison, 1999.

Absorption Rate Constant L/kg(ww)-day Based on fish value in Muir, D.C.G., A.L. Yarechewski, A. Knoll, et al. 1986a

Elimination Rate Constant /day Professional judgment based on water column herbivore value.

Half Life day Professional judgment.



### Benthic Invertebrate Compartment

Clearance constant unitless Professional judgment. Sediment Partitioning Partition Coefficient kg/kg TCDD data for sandworm in Rubenstein et al. 1990; dry weight sediment.PeCDF: multiplied TCDD partition coefficient for sandworm by congenerSediment Partitioning Alpha of Equilibrium unitless Professional judgment.
Sediment Partitioning Time to Reach Alpha of Equilibrium days TCDD: professional judgment; PeCDF: Rubinstein et al. 1990; data for TCDF in sandworm. V_d (ratio of concentration in benthic invertebrates to concentration in water) ml/g Professional judgment.

Half-life day Change source to f-pass 

### All Fish Compartments a

Assimilation efficiency from food unitless TCDD: calculated from data in Kleeman et al. 1986b trout data as cited in USEPA 1993; PeCDF: used assimilation efficiency for TCDD in trout.

Chemical Uptake Rate Via Gill L[water]/kg[fish wet wt]-day Muir et al. 1986.

Gamma_fish unitless Thomann 1989

Half-life day Change source to f-pass

### Exhibit 28. Dioxin Chemical-Specific Properties for Aquatic Specie s Documentation for the TRIM.FaTE Screening Scenari o

Parameter Name Units Reference



### Water Column Herbivore Compartment

Assimilation efficiency from plants unitless TCDD: calculated from data in Kleeman et al. 1986b trout data as cited in USEPA 1993; PeCDF: used assimilation efficiency for TCDD in trout.



### Water Column Omnivore Compartment

Assimilation efficiency from plants unitless TCDD: calculated from data in Kleeman et al. 1986b trout data as cited in USEPA 1993; PeCDF: used assimilation efficiency for TCDD in trout.

a Screening scenario includes: Benthic Omnivore, Benthic Carnivore, Water-column Herbivore, Water-column Omnivore, and Water-column Carnivore.

b N/A = not applicable. This parameter is used in calculating the uptake when measured data are unavailable.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 

### [This page intentionally left blank.]

### Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR: Summary of Approach and Evaluation



# ATTACHMENT 2: Description of Multimedia Ingestion Risk Calculator (MIRC) Used for RTR Exposure and Risk Estimat esAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-i 

### [This page intentionally left blank.]Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- ii 

### TABLE OF CONTENTS

1 Introduction

......................................................................................................................................... 1

1.1 Purpose and Overview

................................................................................................................ 1

1.2 Scope of MIRC

............................................................................................................................ 1

1.3 Use in EPA’s Air Toxics Program

................................................................................................ 2

1.4 MIRC Highlights

........................................................................................................................... 3

1.5 Organization of This Document

................................................................................................... 3

2 MIRC Overview

................................................................................................................................... 5

2.1 Software

....................................................................................................................................... 5

2.2 Exposure Pathways

..................................................................................................................... 7

2.3 Receptor Groups

......................................................................................................................... 8

3 Exposure Algorithms

....................................................................................................................... 11

3.1 Farm Food Chain Algorithms

..................................................................................................... 11

3.1.1 Estimating Chemical Concentrations in Produce

................................................................ 11 3.1.2 Estimating Chemical Concentrations in Animal Products

................................................... 18

3.2 Chemical Intake Calculations for Adults and Non-Infant Children

............................................ 22

3.2.1 Chemical Intake from Soil Ingestion

.................................................................................... 24 3.2.2 Chemical Intake from Fish Ingestion

................................................................................... 24 3.2.3 Chemical Intake from Fruit Ingestion

.................................................................................. 26 3.2.4 Chemical Intake from Vegetable Ingestion

......................................................................... 26 3.2 .5 Chemical Intake from Animal Product Ingestion

................................................................ . 28 3.2.6 Chemical Intake from Drinking Water Ingestion

.................................................................. 30

3.3 Total Chemical Intake

................................................................................................................ 30

3.4 Chemical Intake Calculations for Nursing Infants

...................................................................... 32

3.4.1 Infant Average Daily Absorbed Dose

.................................................................................. 32 3.4.2 Chemical Concentration in Breast Milk Fat

......................................................................... 33 3.4.3 Chemical Concentration in Aqueous Phase of Breast Milk

................................................ 37 3.4.4 Alternative Model for Infant Intake of Methyl Mercury

......................................................... 39

4 Dose-Response Values Used for Assessment

.............................................................................. 41

5 Risk Estimation

................................................................................................................................ . 46

5.1 Cancer Risks

............................................................................................................................. 46

5.2 Non-cancer Hazard Quotients

................................................................................................... 48

5.2.1 Hazard Quotients for Chemicals with a Chronic RfD

.......................................................... 48 5.2.2 Hazard Quotients for Chemicals with RfD Based on Developmental Effects

..................... 48 5.2.3 Hazard Index for Chemicals with RfDs

............................................................................... 48

6 Model Input Options

......................................................................................................................... 50

6.1 Environmental Concentrations

................................................................................................... 50

6.2 Farm-Food-Chain Parameter Values

........................................................................................ 51

6.2.1 List of Farm-Food-Chain (FFC) Parameters

....................................................................... 51 6.2.2 Produce Parameter Values

................................................................................................ . 52Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- iii 6.2.3 Animal Product Parameter Values

...................................................................................... 59

6.3 Adult and Non-Infant Exposure Parameter Values

................................................................... 61

6.3.1 Body Weights

...................................................................................................................... 61 6.3.2 Water Ingestion Rates

......................................................................................................... 62 6.3.3 Local Food Ingestion Rates

................................................................................................ 63 6.3.4 Local Fish Ingestion Rates

.................................................................................................. 67 6.3.5 Soil Ingestion Rates

............................................................................................................ 72 6.3.6 Total Food Ingestion Rates

................................................................................................ . 73

6.4 Other Exposure Factor Values

.................................................................................................. 74

6.4.1 Exposure Frequency

........................................................................................................... 74 6.4.2 Fraction Contaminated

........................................................................................................ 75 6.4.3 Preparation and Cooking Losses

........................................................................................ 75

6.5 Breast-Milk Infant Exposure Pathway Parameter Values

.......................................................... 77

6.5.1 Receptor-specific Parameters

............................................................................................. 77 6.5.2 Chemical-Specific Parameter Values

.................................................................................. 82

7 Summary of MIRC Default Exposure Parameter Settings

............................................................ 85

7.1 Default Ingestion Rates

............................................................................................................. 85

7.2 Default Screening-Level Population-Specific Parameter Values

.............................................. 87

7.3 Default Chemical-Specific Parameter Values for Screening Analysis

....................................... 87

7.4 Screening-Level Parameter Values for Nursing Infant Exposure

.............................................. 89

7.4.1 Dioxins

................................................................................................................................ . 89 7.4.2 Methyl Mercury

.................................................................................................................... 90

8 REFERENCES

................................................................................................................................... 91Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- iv 

### LIST OF EXHIBITS

Exhibit 2-1. Overview of Access-based MIRC Software Application for Performing Farm-Food-Chain

Ingestion Exposure and Risk Calculations

......................................................................... 6
Exhibit 2-2. Transfer Pathways for Modeled Farm Food Chain (FFC) Media

............................................. 8
Exhibit 3-1. Chemical Transfer Pathways for Produce

.............................................................................. 12
Exhibit 3-2. Estimating Chemical Concentration in Aboveground Produce

............................................... 12
Exhibit 3-3. Chemical Transfer Pathways for Animal Products

................................................................ . 19

Exhibit 4-1. Oral Dose- re sponse Values for PB-HAP Chemicals Used to Calculate RTR Screening

Threshold Emission Rates

................................................................................................ 41
Exhibit 4-2. WHO 2005 Toxic Equivalency Factors (TEFs) for Dioxins

..................................................... 43
Exhibit 4-3. Oral Dose-response Values for Polycyclic Organic Matter (POM) Groups

............................ 44

Exhibit 6-1. MIRC Parameters Used to Estimate Chemical Concentrations in Farm Foods

..................... 51
Exhibit 6-2. Chemical-Specific Inputs for Produce Parameters

................................................................ . 53
Exhibit 6-3. Chemical-Specific Inputs by Plant Type for Chemicals in MIRC

............................................ 54
Exhibit 6-4. Non-Chemical-Specific Produce Inputs

.................................................................................. 58
Exhibit 6-5. Animal Product Chemical-specific Inputs for Chemicals Included in MIRC

........................... 59
Exhibit 6-6. Soil and Plant Ingestion Rates for Animals

............................................................................. 60
Exhibit 6-7. Mean and Percentile Body Weight Estimates for Adults and Children

.................................. 62
Exhibit 6-8. Estimated Daily Per Capita Mean and Percentile Water Ingestion Rates for Children and

Adults a

............................................................................................................................. 63
Exhibit 6-9. Summary of Age-Group-Specific Food Ingestion Rates for Farm Food Items

....................... 64
Exhibit 6-10. Daily Mean and Percentile Consumer-Only Fish Ingestion Rates

........................................ 70
Exhibit 6-11. Fraction of Population Consuming Freshwater/Estuarine Fish on a Single Day (FPC,y)

.... 70
Exhibit 6-12. Calculated Long-term Mean and Percentile Per capita Fish Ingestion Rates for Children and

Adults (IRPC,y)

................................................................................................................. 71
Exhibit 6-13. Calculated Mean and 90th Percentile Per capita Fish Ingestion Rates for Populations of

Recreational Fishers (IRPC,y)

......................................................................................... 71
Exhibit 6-14. Daily Mean and Percentile Soil Ingestion Rates for Children and Adults

............................. 73
Exhibit 6-15. Daily Mean and Percentile Per Capita Total Food Intake for Children and Adults

............... 74
Exhibit 6-16. Fraction Weight Losses from Preparation of Various Foo ds

................................................ 76
Exhibit 6-17. Scenario- and Receptor-Specific Input Parameter Values Used to Estimate Infant

Exposures via Breast Milk

................................................................................................ . 78
Exhibit 6-18. Average Body Weight for Infants

.......................................................................................... 78
Exhibit 6-19. Time-weighted Average Body Weight for Mothers

................................................................ 79

Exhibit 6- 20. Infant Breast Milk Intake Rates

............................................................................................. 81
Exhibit 6-21. Chemical-specific Input Parameter Values for Breast Milk Exposure Pathway

.................... 82
Exhibit 7-1. Farm Food Category Ingestion Rates for Conservative Screening Scenario for Farming

Households

....................................................................................................................... 86Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-v Exhibit 7-2. Mean Body Weight Estimates for Adults and Children a

........................................................ 87
Exhibit 7-3. Chemical-Specific Parameter Values for Input to MIRC a

...................................................... 88
Exhibit 7-4. Chemical and Animal-Type Specific Biotransfer Factor (Ba) values for Input to MIRC

......... 89Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- vi 

### LIST OF EQUATIONS

Equation 3-1. Chemical Concentration in Aboveground Produce

............................................................. 13
Equation 3-2. Chemical Concentration in Aboveground Produce Due to Root Uptake

............................ 13
Equation 3-3. Chemical Concentration in Aboveground Produce Due to Deposition of Particle- ph ase

Chemical

........................................................................................................................... 14
Equation 3-4. Chemical Concentration in Aboveground Produce Due to

.................................................. 15
Equation 3-5. Conversion of Aboveground Produce Chemical Concentration from

.................................. 16
Equation 3-6. Chemical Concentration in Belowground Produce: Nonionic Organic Chemicals

............. 17
Equation 3-7. Chemical Concentration in Belowground Produce: Inorganic Chemicals

.......................... 18
Equation 3-8. Conversion of Belowground Produce Chemical Concentration from

.................................. 18
Equation 3-9. Chemical Concentration in Beef, Pork, or Total Dairy

......................................................... 19
Equation 3-10. Chemical Concentration in Poultry or Eggs

....................................................................... 20
Equation 3- 11. Incidental Ingestion of Chemical in Soil by Livestock

........................................................ 20
Equation 3- 12. Ingestion of Chemical in Feed by Livestock

...................................................................... 21
Equation 3-13. Chemical Concentration in Lifestock Feed (All Aboveground)

.......................................... 21
Equation 3-14. Chemical Concentration in Livestock Feed Due to Root Uptake

...................................... 22
Equation 3- 15. Average Daily Dose for Specified Age Group and Food Type

.......................................... 22
Equation 3-16. Chemical Intake from Soil Ingestion

.................................................................................. 24
Equation 3-17. Chemical Intake from Fish Ingestion

................................................................................. 25
Equation 3-18. Consumption-weighted Chemical Concentration in Fish

.................................................. 25
Equation 3-19. Chemical Intake from Consumption of Exposed Fruits

..................................................... 26
Equation 3-20. Chemical Intake from Consumption of Protected Fruits

.................................................... 26
Equation 3-21. Chemical Intake from Exposed Vegetables

...................................................................... 27
Equation 3-22. Chemical Intake from Protected Vegetables

..................................................................... 27
Equation 3-23. Chemical Intake from Root Vegetables

............................................................................. 27
Equation 3-24. Chemical Intake from Ingestion of Beef

............................................................................ 28
Equation 3-25. Chemical Intake from Dairy Ingestion

............................................................................... 28
Equation 3- 26. Chemical Intake from Pork Ingestion

................................................................................ 29
Equation 3- 27. Chemical Intake from Poultry Ingestion

............................................................................. 29
Equation 3-28. Chemical Intake from Egg Ingestion

................................................................................. 30
Equation 3-29. Chemical Intake from Drinking Water Ingestion

................................................................ 30
Equations 3-30 to 3-35. Total Average Daily Dose of a Chemical for Different Age Gro ups

.................... 31
Equation 3- 36. Lifetime Average Daily Dose (LADD)

................................................................................ 31
Equation 3-37. Average Daily Dose of Chemical to the Nursing Infant

..................................................... 33
Equation 3-38. Chemical Concentration in Breast Milk Fat

....................................................................... 34
Equation 3-39. Daily Maternal Absorbed Intake

........................................................................................ 35Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-vii Equation 3-40. Biological Elimination Rate Constant for Chemicals for Non-lactating Women

................ 36
Equation 3-41. Biological Elimination Constant for Lipophilic Chemicals for Lactating Women

............... 36
Equation 3-42. Chemical Concentration in Aqueous Phase of Breast Milk

............................................... 37
Equation 3-43. Fraction of Total Chemical in Body in the Blood Plasma Compartment

........................... 38
Equation 3-44. Biological Elimination Rate Constant for Hydrophilic Chemicals

...................................... 39
Equation 3-45. Calculation of Infant Average Daily Absorbed Dose of Methyl Mercury

............................ 40
Equation 5- 1. Calculation of Excess Lifetime Cancer Risk

........................................................................ 46
Equations 5-2 to 5-8. Lifetime Cancer Risk: Chemicals with a Mutagenic MOA for Cancer

..................... 47
Equation 5- 9. Hazard Quotient for Chemicals with a Chronic RfD

............................................................ 48
Equation 5-10. Hazard Index Calculation

.................................................................................................. 49
Equation 6-1. Calculation of Age-Group-Specific and Food-Specific Ingestion Rates

.............................. 67
Equation 6-2. Calculation of Alternative Age-Group-Specific Fish Ingestion Rates

.................................. 69Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-1 

## 1 Introduction

1.1 Purpose and Overview
This document provides a detailed description of the Multimedia Ingestion Risk Calculator (MIRC), an Access-based tool and database designed to assist in estimating risks via multiple ingestion pathways, particularly for food products grown or raised at home or on a farm. MIRC was designed to estimate risks to humans from ingestion of produce or animal products, fish, and water in the vicinity of a source of chemical emissions to air. The user can evaluate either generalized (e.g., conservative default) or more site-specific scenarios using the same tool. MIRC includes a database of exposure parameter values, offering the user the option of selecting mean, median, and upper percentile values for many parameters, data permitting. Generally conservative default values were assigned to each parameter in the tool and the default configuration is used for initial risk screening efforts by EPA’s Office of Air Quality Planning and Standards’ (OAQPS) for Risk and Technology Review (RTR) multimedia risk assessments. MIRC also allows the user to define the farm food chain (FFC) parameter values and receptor characteristics to better represent a site-specific scenario.

With user-input concentrations for one or more chemicals in air and soil and air- to -surface deposition rates, MIRC calculates the chemical’s concentrations in home- or farm-grown produce and animal food products using FFC algorithms adapted from EPA’s Human Health Risk Assessment Protocol for Hazardous Waste Combustion Facilities (hereafter referred to as HHRAP ; EPA 2005a ). MIRC uses these calculated concentrations, along with user-input chemical concentrations for fish and drinking water, to estimate chemical intake rates, as average daily doses (ADDs), for adults, children, and nursing infants. Users can obtain chemical input concentrations and deposition rates from measurements at an actual site or from a transport and fate model, such as TRIM.FaTE, as is done for RTR risk assessment.

For a specified set of chemical concentrations and MIRC parameter options, MIRC calculates ADDs separately for adults, four age groups of children, and infants to reflect differences in food ingestion rates and diet at different lifestages. MIRC estimates age-specific hazard quotients (HQs) as the ratio of age-specific ADDs to the reference dose (RfD) for a chemical. The most appropriate HQ for a chemical depends on its toxic mode of action and the duration of exposure required to produce an effect. MIRC also estimates average lifetime ADDs and compares those to cancer slope factors (CSFs) to estimate cancer risks. A breast milk ingestion pathway is included to estimate exposure and risks to nursing infants.

MIRC was developed to be a flexible, transparent application using Microsoft Access software. The tool includes chemical transfer and ingestion exposure algorithms and a database of parameter values, many with several options, used by these equations

. The MIRC database includes values for the relevant physiochemical properties and toxicity reference values for more than 500 chemicals, including approximately 60 inorganics taken primarily from a database developed for HHRAP (EPA 2005a). Although designed for OAQPS ’ RTR assessments for sources of hazardous air pollutants (HAPs), the tool is flexible in its design and can be used to assess risks in many other contexts where soil and air concentrations are predicted or measured.



### 1.2 Scope of MIRC
For persistent and bioaccumulative (PB) chemicals, risks from direct inhalation of the chemical can be much less than risks from ingestion of the chemical in water, fish, and food products grown in an area of chemical deposition. Vegetables and fruits in such areas can becomeAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-2 

### contaminated directly by deposition of the airborne chemical to foliage, fruits, and vegetables or indirectly by root uptake of the chemical deposited to soils. Livestock can be exposed to the PB chemicals via ingestion of contaminated forage and incidental ingestion of contaminated soils.

For PB chemicals, evaluation of the inhalation pathway for air pollutants may reveal only a portion of the risk to individuals in such populations. Households that consume high quantities of self-caught fish or locally grown produce and animal products may be particularly susceptible to ingestion of chemicals transferred from air in the vicinity of an air emissions source. For PB chemicals in particular, therefore, EPA developed methods of estimating risk from indirect exposure pathways associated with the deposition of airborne chemicals to gardens and farms

, as described in HHRAP ( EPA 2005 a).

MIRC is an Access-based tool that facilitates calculation of risks associated with the indirect ingestion exposure pathways for persons consuming produce and animal products grown in an air depositional area of concern. The tool uses algorithms described in or adapted from HHRAP to calculate exposures from the ingestion of produce and animal products. Included with MIRC is a fish ingestion pathway and drinking water ingestion pathway for scenarios in which those pathways may be important. MIRC also includes a breast milk ingestion pathway for nursing infants based primarily on EPA’s Methodology for Assessing Health Risks Associated with Multiple Pathways of Exposure to Combustor Emissions (hereafter MPE; EPA 1998)

. 

### 1.3 Use in EPA’s Air Toxics Program
MIRC was designed to help predict human health risks from PB HAPs for EPA’s RTR assessments. EPA

evaluates the fate of HAP releases to air from source categories after implementation of technology-based Maximum Achievable Control Technology (MACT) standards. For volatile chemicals that do not partition to other environmental media and for

non -persistent chemicals that degrade relatively quickly in the environment, evaluation of health risks from direct inhalation of the chemical in air can provide reasonable estimates of total risk.

For PB-HAPs, however, indirect exposure pathways, such as ingestion, might contribute more to total risk than the inhalation pathway

. EPA therefore developed several computer software tools to assist in evaluating exposure and risk from non-inhalation pathways

. EPA developed the Total Risk Integrated Methodology (TRIM) Environmental Fate, Transport, and Ecological Exposure (TRIM.FaTE) computer program to simulate the release, transport, and fate of HAPs from a specific s ource through out the area in which local (non

- source) chemical deposition is likely to be a concern

. TRIM.FaTE models the transport of individual chemicals from the source through air by advection (wind) of particle

- and vapor

- phase chemical and depositio n of the chemical from air to terrestrial and aquatic ecosystems by wet and dry deposition

. Movement of the chemical through a watershed via erosion and runoff, uptake by plants, and other abiotic and biotic transfer processes also are simulated

. For the chemical that reaches surface waters, TRIM.FaTE models uptake and bioaccumulation to trophic level (TL) 3 and 4 fish (i.e., pan fish and game fish, respectively)

. MIRC was developed to process TRIM.FaTE results, in particular, air deposition rates and the concentrations of a chemical, after a specified duration of emissions, in several spatially explicit environmental compartments, including air, surface and root-zone soils, surface and ground waters, and fish

. MIRC uses those results to calculate exposure to the chemical through ingestion of locally grown foods, including various types of fruits and vegetables, poultry, swine, and dairy (and beef) cattle. MIRC also calculates the associated risks for individuals who consume those foods. MIRC was designed to use specific TRIM.FaTE results to estimate FFC concentrations, ingestion exposures, and human health risks for OAQPS’ RTR assessments. ItAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-3 

### uses the same approach that OAQPS intends to implement directly in its TRIM system via three modules beyond TRIM.FaTE: TRIM Farm Food Chain, TRIM.Expo Ingestion 

### , and TRIM.Risk

. 1



### 1.4 MIRC Highlights
Although designed to assist EPA OAQPS in its RTR assessments, MIRC is a stand-alone software application that can be used in other contexts. A user can supply either measured or estimated chemical concentrations for soil, air, water, and fish and air deposition rates likely for the location(s) of interest based on local meteorology. The user can accept the default values for many exposure parameters and screen for small possibilities of risk, or the user can select other options or overwrite parameter values to tailor the estimates to a specific scenario or location.

MIRC complies with EPA’s latest guidelines for exposure and risk assessment, including HHRAP ; the Agency’s 2005 Guidelines for Carcinogen Risk Assessment (Cancer Guidelines)

, Supplemental Guidance for Assessing Susceptibility from Early-Life Exposure to Carcinogens (Supplemental Guidance), and Guidance on Selecting Age Groups for Monitoring and Assessing Childhood Exposures to Environmental Contaminants ( EPA 2005 b, c,d); and its 2008 Child-Specific Exposure Factors Handbook ( EPA 2008a) . In particular, MIRC provides several important capabilities:

When provided air and soil concentrations, the MIRC software package allows rapid calculation of screening-level exposures and risks associated with household consumption of locally grown/raised foods.

MIRC can calculate exposures and risks associated with incidental ingestion of surface soils, fish consumption, and drinking water.

The tool calculates ADDs (i.e., chemical intake rates) for six “built

- in ” age groups to allow use of age-group-specific body weights, ingestion rates, food preferences, and susceptibility to toxic effects.

Its database of chemical information covers plant- and animal-specific transfer factors and other inputs that determine concentrations in farm food stuffs.

Value options for receptor characteristics in the database include the mean and 50th, 90th, 95th, and 99th percentile values where data permit.

For carcinogens with a mutagenic mode of action, MIRC estimates a lifetime ADD using the three lifestages and potency adjustment factors recommended in EPA’s 2005 Cancer Guidelines and Supplemental Guidance.

The data for exposure parameters in the tool have been updated to include the latest recommended values for children issued September 30, 2008, in the Agency’s Child

Specific Exposure Factors Handbook (CSEFH) ( EPA 2008 a ).



### 1.5 Organization of This Document
Sections 2 through 5 of this document descri be the exposure and risk models implemented in MIRC

. Section 2 provides an overview of the FFC exposure scenario and indicates options available to a user to tailor the scenario to specific applications. Section 3 describes the

1 General information about the TRIM system is available at http://www.epa.gov/ttn/fera/trim_gen.html

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-4 

### exposure algorithms used in MIRC, including how ADDs are calculated. Section 4 presents the toxicity reference values included in MIRC to calculate risks. Section 5 describes the risk characterization algorithms in MIRC

. Section 6 of this document describes data input options fo r the model

. Section 7 describes the default parameterization of MIRC for application to conservative risk screening assessments, and Section 8 provides the references. Appendix A provides guidance to users on how to set up and run MIRC for their own applications.

Note that the default parameterization described in Section 7 was used to estimate screening threshold releases of PB -HAPs from facilities assumed to pose negligible risk to subsistence communities in the vicinity of a facility emitting the HAPs to air

. Users of MIRC can modify the default values for many of the parameters to better represent a specific exposure scenario.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-5 

## 2 MIRC Overview

The Multimedia Ingestion Risk Calculator (MIRC) software package is designed to allow rapid calculation of screening-level exposures and risks associated with subsistence and recreational farmer/fisher populations in the vicinity of a source of chemical emissions to air. The tool allows a user to assess human exposures via ingestion pathways, including drinking water consumption, incidental soil ingestion, fish ingestion, and ingestion of ten types of farm food chain (FFC) products : exposed fruits, protected fruits, exposed vegetables, protected vegetables

, root vegetables, beef, total dairy, pork, poultry, and eggs

. The tool also includes a breast milk ingestion and risk module for nursing infants. For fruits and vegetables, the terms “exposed” and “protected” refer to whether the edible portion of the plant is exposed to the atmosphere.

The remainder of this overview consists of three sections. The first (Section 2.1) provides an overview of the MIRC software package. The second and third sections summarize the ingestion exposure pathways included in the tool and the “built

- in” receptor age categories

, re spectively (Sections 2.2 and 2.3).



### 2.1 Software
The MIRC application includes the following components:

A graphical user interface through which the user locates and accesses various input and output tables.

Input tables in which the user can enter environmental concentrations of a chemical estimated for air, soil, drinking water, and fish tissue.

Internal chemical transfer and exposure algorithms and database of options for FFC algorithm parameter value, chemical-specific inputs, and exposure factors.

Tabulated outputs of calculated chemical concentrations in the various farm food products (e.g., fruits, vegetables, beef, eggs) and ADDs for those foods and for water and fish ingestion for each receptor category.

Output tables with estimated cancer risks and n on -cancer hazard estimates associated with total ingestion exposure to each chemical for each receptor category.

Exhibit 2-1 provides a flowchart displaying the types of inputs required or optional and general flow of calculations carried out by the tool.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-6 

### Exhibit 2

- 1

. Overview of Access

- based MIRC Software Application for Performing Farm

- Food

- Chain Ingestion Exposure and Risk CalculationsAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-7 

### An Access form within the graphical user interface enables the user to construct specific scenarios by choosing ingestion sources, receptor ages, and other input choices (e.g., diet composition, body weight percentiles). This feature facilitates the analysis of various exposure scenarios. To begin an analysis, the user must supply values for the following chemical-specific
pa rameters for the scenario being evaluated:

Air concentration of total chemical, Fraction chemical in air in vapor-phase, Wet and dry deposition rates for particle-phase chemical, Drinking water concentration, Chemical concentration in surface soils (two locations; can be tilled and untilled), Chemical concentration in root-zone soils (two locations; can be tilled and untilled), and Chemical concentrations in pan fish and in game fish.

Users can input measured values or values estimated by TRIM.FaTE or other models for these parameters

. The MIRC application uses the input data and a variety of empirical transfer factor values (included in its database) to estimate chemical concentrations in nine categories of FFC food types (Section 2.2). The FFC algorithms and transfer factor values included in MIRC are based on those presented in Chapter 5 of EPA’s Human Health Risk Assessment Protocol for Hazardous Waste Combustion Facilities, hereafter referred to as HHRAP ( EPA 2005 a).

For outputs, MIRC is designed to calculate individual cancer risk and non -cancer hazard quotients for one chemical at a time. It is up to the risk assessor to determine if cancer risks or hazard quotients may be additive across two or more chemicals (i.e., if they cause toxic effects in the same target organ by the same mode of action, such as multiple PAHs that are carcinogenic by a mutagenic mode of action).

The tool assumes that the same individuals (farming family or household that gardens and raises animals) are exposed via all of the pathways specified (i.e., pathways with non-zero ingestion rates). The tool therefore is useful in estimating risk to the maximally exposed individuals (MEI) in a risk assessment. To evaluate multiple populations, the user must specify the full exposure scenario for each population separately.



### 2.2 Exposure Pathways

MIRC estimates the concentrations of chemicals i n FFC food categories grown in an area of airborne chemical deposition using algorithms and parameter values provided in HHRAP ( EPA 2005a) . FFC foods are evaluated in ten categories: exposed fruit, protected fruit, exposed vegetables, protected vegetables, root vegetables, beef, total dairy, pork, poultry, and eggs. Exhibit 2-2 summarizes the pathways by which chemicals are transferred to these food media. Note that for a general screening-level assessment, all of the pathways can be modeled, as is the case for EPA’s Risk and Technology Review (RTR) calculation of screening threshold emission rates for persistent and bioaccumulative hazardous air pollutants (PB-HAPs) ( EPA 2008 b ).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-8 

### Exhibit 2

- 2

. Transfer Pathways for Modeled Farm Food Chain (FFC) Media

Farm Food Media Chemical Transfer Pathways Exposed fruit and vegetables Direct deposition from air of particle

- bound chemical Air

- to

- plant transfer of vapor phase chemical Root uptake from soil Protected fruit and vegetables (includin g root vegetables) Root uptake from soil

Beef and total dairy (including milk) Ingestion of forage, silage, and grain a Soil ingestion

Pork Ingestion of silage and grain a Soil ingestion Poultry and eggs Ingestion of grain a Soil ingestion

a Chemical concentrations in forage, silage, and grain are estimated via intermediate calculation s analogous to those used for aboveground produce

.


### Produce types included in the FFC can accumulate a chemical directly from air and/or soil

. For exposed produce, chemical mass is assumed to be transferred to plants from the air in two
ways

. First, particle-bound chemical can deposit directly on the plant surface. Second, the uptake of vapor-phase chemicals by plants through their foliage can occur. For both exposed and protected produce, the concentration in the plant derived from exposure to the chemical in soil is estimated using an empirical bioconcentration factor (BCF) that relates the concentration in the plant to the concentration present in the soil

. For belowground root vegetables, a root concentration factor is applied

. The algorithms used to estimate produce concentrations are presented in Section 3.1.1

. Chemical concentrations in animal products are estimated based on the amount of chemical consumed through the diet, including incidental ingestion of soil while grazing. The diet options for farm animals in MIRC include forage (plants grown on-site for animal grazing, such as grass), silage (wet forage grasses, fresh-cut hay, or other fresh plant material that has been stored and fermented), and feed grain products grown on the farm (e.g., corn, soybeans). All three animal feed products are assumed to accumulate chemical via root uptake from the soil. Forage and silage also can accumulate chemical via direct deposition of particle-bound chemical and vapor transfer.

The algorithms in MIRC are based on the assumptions that beef and dairy cattle consume all three feed products, while pigs consume only silage and grain and chickens consume only grain. The incidental ingestion of the chemical in soils during grazing or consumption of foods placed on the ground is estimated using empirical soil ingestion values

. For secondary animal products (dairy products and eggs), chemical concentrations are estimated by applying a biotransfer factor to the estimated concentration in the “source” animal (cows and chickens, respectively)

. The algorithms used to estimate animal product concentrations are described in Section 3.1.2

. 

### 2.3 Receptor Groups

As noted in EPA risk assessment guidelines (EPA 2005b,c,d, 2008 a), exposures of children are expected to differ from exposures of adults due to differences in body weights, ingestion rates, dietary preferences, and other factors. It is important, therefore, to evaluate the contribution of exposures during childhood to total lifetime risk using appropriate exposure factor values

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2-9 

### EPA’s HHRAP (Chapter 4, EPA 2005a) recommends assessing exposures for children and adults separately, but considers all non -infant children in one category. Specifically, HHRAP recommends eight categories of receptor: farmer, child f ar mer, resident, child resident, fisher, child fish er , acute receptor, and nursing infant. Over time, different EPA programs have used different child age groupings to evaluate body weights, ingestion rates, and other parameter values needed to estimate chemical exposures and risks to children.

To improve the match between age groups used to estimate values across exposure parameters, in 2005, EPA recommend ed a standard set of child age categories for exposure and risk assessments ( EPA 2005b) . EPA recommended four age groups for infants: birth to < 1 month; 1 to < 3 months; 3 to < 6 months; and 6 to < 12 months. For young children, EPA recommended an additional four age groups: 1 to < 2 years; 2 to < 3 years; 3 to < 6 years; and 6 to < 11 years. Two age groupings were recommended for teenagers and young adults: 11 to < 16 years; and 16 to < 21 years. These age groupings correspond to different developmental stages and reflect different food ingestion rates per unit body weight, with the highest ingestion rates occurring for the youngest, most rapidly growing, age groups.

For assessment of cancer risks from early-life exposure, EPA recognizes that infants and children may be more sensitive to a carcinogenic chemical than adults, with cancers appearing earlier in life or with lower doses experienced during childhood ( EPA 2005c, d). Thus, the “potency” of a carcinogen m ight be higher for infants and children than for adults. To date, however, data by which to evaluate the relative sensitivity of children and adults to the same daily dose of a carcinogen remain limited

. Based on analyses of radioactive and other carcinogenic chemicals, EPA recommends evaluating two lifestages for children separately from adults for chemicals that cause cancer by a mutagenic mode of action (MOA): from birth to < 2 years and from 2 to < 16 years ( EPA 2005c,d). EPA also suggests that, as data become available regarding carcinogens with a mutagenic MOA, further refinements of these age groupings may be considered.

For purposes of RTR assessment using MIRC, the selection of age categories is limited by the categories for which most of the F FC food ingestion rates have been calculated. In Chapter 13 of both its Exposure Factors Handbook (EFH; EPA 1997 a ) and its Child-Specific Exposure Factors Handbook

(CSEFH ; EPA 2008a) , EPA summarized home-grown/raised food ingestion rates for four children ’s age groups: 1 to < 3 years; 3 to < 6 years; 6 to < 12 years; and 12 to < 20 years. Intake rates were not calculated for children younger than 1 year because infants are unlikely to consume those foods. They are more likely to be nursing or to be fed formula and other commercial baby-food products

. Although the age groupings used to estimate FFC ingestion rates do not match precisely the groupings that EPA recommended in 2005 for Agency exposure assessments ( EPA 2005b), they are the only age-groupings for which such data are available

. T he U.S

. Department of Agriculture’ s (USDA’s) 1987- 1988 Nationwide Food Consumption Survey (USDA 1992, 1993, 1994) remains the most recent survey of ingestion rates for home-grown foods , and EPA’s analysis of those data, published in its 1997 EFH, remains the most recently published major analysis of those data. Because ingestion of home-grown produce and animal products are the primary exposure pathways for which MIRC was developed, those are the age groupings used fo r all child parameter values used to estimate exposure and risk in MIRC

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 10 

### Thus, i n MIRC , v alues for each exposure parameter were estimated for adults (20 to 70 years) and five children’s age groups:

infants under 1 year (i.e., 0 to < 1 year) ; children ages 1 through 2 years (i.e., 1 to < 3 years) ; children ages 3 through 5 years (i.e., 3 to < 6 years) ;

c hildren ages 6 through 11 years(i.e., 6 to < 12 years) and children ages 12 through 19 years (i.e., 12 to < 20 years).

Exposure and risks to infants under 1 year of age are estimated only for the breast-milkingestion pathway

. For assessing risks from exposures to carcinogenic chemicals that act via a mutagenic MOA

, the two early lifestages recommended by EPA (EPA 2005c,d) also are included in MIRC:

children under the age of 2 years (i.e., 0 to < 2 years); and children from 2 through 15 years (i.e., 2 to < 16 years).

Different age groupings are needed for the assessment of risks from carcinogenic chemicals with a mutagenic MOA and other carcinogens with other or unknown MOAs. Currently in MIRC, the only PB

- HAPs with a mutagenic mode of carcinogenesis are some of the PAHs.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 11 

## 3 Exposure Algorithms

The exposure algorithms in MIRC are described below in four sections. Section 3.1 presents the algorithms used to estimate chemical concentrations in FFC foods from chemical concentrations in soil and air. Pathway-specific algorithms used to estimate chemical intakes by adults and non-infant children are described in Section 3.2, and total chemical intake calculations are described in Section 3.3. Finally, the sets of algorithms used to estimate chemical intake via consumption of breast milk by nursing infants are described in Section 3.4. As noted previously, the exposure algorithms used in MIRC are based on those presented in HHRAP (EPA 2005b). Any differences between MIRC and HHRAP are explained in this section.



### 3.1 Farm Food Chain Algorithms
The algorithms and parameters used to estimate chemical concentrations in produce and animal products are described in Sections 3.1.1 and 3.1.2, respectively

. Discussions of the parameter value options and the values selected as defaults in MIRC for RTR risk assessment are provided in Section 6. 2. The use of TRIM.FaTE to model chemical fate and transport in the environment prior to FFC calculations drives the most significant difference between the FFC algorithms included in HHRAP and the equations used for RTR. The approach in HHRAP uses estimated ambient air concentrations and deposition rates from dispersion model simulations that use unitized emission rates. Chemical-specific emission rates (adjusted for vapor and particle-bound fractions) are then incorporated into some of the HHRAP FFC algorithms to calculate concentrations in FFC media. Soil concentrations are calculated using a similar approach in HHRAP. For assessment of multipathway exposures for RTR, TRIM.FaTE is used to estimate air concentrations, air- to -surface deposition rates, and soil concentrations, and these outputs are used in the FFC algorithms.

3.1.1 Estimating Chemical Concentrations in Produce Produce (vegetables and fruits) can become contaminated directly by deposition of airborne chemicals to foliage and fruits or indirectly by uptake of chemicals depo sited to the soil. Given these two contamination processes, produce is divided into two main groups: abov eground and belowground produce. Aboveground produce is divided into fruits and vegetables. These groups are further subdivided into “ exposed ” and “ protected ” depending on whether the edible portion of the plant is exposed to the atmosphere or is protected by a husk, hull, or other outer covering.

Exhibit 3-1 lists the pathways by which chemicals are transferred to the FFC pr oduce categories. Note that for a general screening-level assessment, all of the pathways can be modeled, as was done for EPA’s calculation of screening threshold emission rates for PB -HAPs in its RTR assessments (EPA 2008b) , and as described in the “ Technical Support Document for
TRIM- Based Multipathway Screening Scenario for RTR” 

### . Sections 3.1 .1 .1 and 3.1.1.2 describe the transfer pathways and algorithms for aboveground and belowground produce, respectively.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 12 

### Exhibit 3

- 1

. Chemical Transfer Pathways for Produce

Farm Food Media Chemical Transfer Pathways

Aboveground Produce Exposed fruits and

vegetables Direct deposition from air of particle

- bound chemical Air

- to

- plant transf er of vapor phase chemical Root uptake from soil
Protected fruits and vegetables Root uptake from soil

Belowground Produce Root vegetables Root uptake from soil



### 3.1.1.1 Aboveground Produce For aboveground exposed produce, chemical mass is assumed to be transferred to plants from the air in three ways, as illustrated in Exhibit 3-2 . First, particlebound chemical can deposit directly on the plant surface via deposition ( Pd ). The amount of chemical accumulated is estimated based on the areal fraction of chemical deposition intercepted by the plant surface, minus a loss factor that is intended to account for removal of deposited chemical by wind and rain and changes in concentration due to growth dilution

. Second, for chemical present in air in the vapor phase, the concentration of chemical accumulated by the plant’s foliage is estimated using an empirical air- to -plant biotransfer factor ( Pv

). Third, the chemical concentration in the plant due to root uptake from the soil ( Pr AG -produce 

### ) is estimated using an empirical bioconcentration factor ( Br AG -produce 

### ) that relates the chemical concentration in the plant to the average chemical concentration in the soil at the root-zone depth in the produce-growing area ( Cs root -zone_produce 

### )

. The edible portions of aboveground protected produce are not subject to contamination via particle de position ( Pd

) or vapor transfer (

Pv )

. Therefore, root uptake of chemicals is the primary mechanism through which aboveground protected produce becomes contaminated

. The chemical concentration in the aboveground plant due to root uptake from soil ( Pr AG -produceDW 

### ) is estimated using an empirical bioconcentration factor ( Br AG -produce- DW



### ) that relates thechemical concentration in the plant to the average chemical concentration in the soil at the rootzone depth in the produce-growing area ( Cs root -zone_produce 

### )

. Exhibit 3

- 2

. Estima ting Chemical Concentration in Aboveground ProduceAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 13 

### Equation 3-1

. Chemical Concentration in Aboveground Produce

where:

C AG

- p roduce

- DW

(i) = Conc entration of chemical in edible portion of abovegro und produce type i

, exposed or protected, on a dry

- weight (DW) basis (mg/kg produce DW )

Pd (i) = Chemical c oncentration in edible portion of aboveground produce type i due to deposition of particles (mg/kg produce DW ) ; for protected aboveground produce, Pd equals zero

Pr AG

- p roduce

- DW

(i) = C hemical c oncentration in ed ible portion of aboveground produce type i

, exposed or protected, due to root uptake from soil at the root

- zone depth of the produce growing area (mg/kg produce DW )

Pv (i) = Chemical c oncentration in edible portion of aboveground produce type i due to air

- to

- plant transfer (μg/g [ or mg/kg ] produce DW ) ; for protected aboveground produce, Pv equals zero



### Equation 3-2

. Chemical Concentration in Aboveground Produce Due to Root Uptake

where:

Pr AG

- produce

- DW

(i) = Concentration of chemical in edible portion of aboveground produce type i

, exposed or protected

, due to root uptake from soil at root

- zone depth in the produce

- growing area , on a dry

- weight (DW) basis (mg/kg produce DW )

Cs root

- zone

_ produce = Average chemical concentration in soil at root

- zone depth in produce

- growing

area (mg/kg soil DW )

Br AG

- produce

- DW

(i) = Chemical

- specific plant/ soil chemical bioconcentration factor for edible portion of aboveground produce type i

, exposed o r protected ( g soil DW / g produce DW )Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 14 

### Equation 3-3

. Chemical Concentration in Aboveground Produce Due to Deposition of Particle-phase Chemical

where:

Pd (i) = Chemical concentrati on in aboveground produce type i on a dry

- weight (DW)

basis due to particle deposition (mg/kg produce DW) ; set equal to zero for protected aboveground produce
Drdp = Average annual dry deposition of particle

- phase chemical (g/m 2

- yr)

Fw = Fraction of wet deposition that adheres to plant surfaces; 0.2 for anions, 0.6 for

cations and most organics (unitless)
Drwp = Average annual wet deposition of particle

- phase chemical (g/m 2

- yr)
Rp (i) = Interception fraction of the edible portion of plant type i (unitles s)

k p (i) = Plant surface loss coefficient for plant type i (yr - 1 )

Tp (i) = Length of exposure to deposition in the field per harvest of the edible portion of

plant type i (yr)

Yp (i) = Yield or standing crop biomass of the edible portion of plant type i (kg produce

DW /m 2 )



### Note that Equation 3-3 differs from Equation 5-14 in HHRAP, from which it is derived

. In HHRAP, Equation 5-14 includes the term Q x ( 1

– Fv ) to indicate the emissions rate, in g/sec, of chemical from the source and the proportion of the chemical that remains in, or partitions to, the particle-phase in the air. Also in HHRAP

, the dry and wet particle phase deposition rates, Dydp and Dywp, respectively, are normalized to the emission rate and are expressed in units of sec/m 2



### - yr

. With MIRC, the user inputs both the dry and wet particle-phase deposition rates, Drdp and Drwp , respectively, in units of g/m 2 

### -yr for a specific location relative to an emissions source. Those deposition rates might be values measured near that location or es timated using a fate and transport model, such as TRIM.FaTE, in conjunction with local meteorological information and emissions rate data. The chemical emissions term used in HHRAP

, Q

, therefore, is not used in MIRC ’s Equation 3-3. In addition, in MIRC, Dr dp and Dr wp
, the average annual dryand wet-particle-phase deposition rates, respectively, are in units of g/m 2



### - yr . Users of TRIM.FaTE should note that the dry- and wet-particle-deposition rates output from TRIM.FaTE are in units of

g/m 2 

### -d ay ; therefore

, user s must adjust the TRIM.FaTE output values to units of g/m 2 

### -yr (i.e., multiply by 365 days/yr) before inputting values for Drdp and Drwp into MIRC.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 15 

### Equation 3-4

. Chemical Concentration in Aboveground Produce Due to

Air- to -Plant Transfer of Vapor-phase Chemical

where:

Pv (i) = Concentration of chemical in edible portion of a boveground produce type i from air

- to

- plant transfer of vapor

- phase chemical on a dry

- weight (DW) basis ( μg/g produce DW ) ; set equal to zero for protected aboveground produce

Ca = Average annual total chemical concentration in air (g/m 3 )

Fv = Fraction of airborne chemical in vapor phase (unitless)

Bv AG (i) = A ir

- to

- plant biotransfer factor for aboveground produce type i for vapor

- phase

chemical in air ([mg/g produce DW ] / [ mg/g air ] , i.e., g air/ g produce DW )

VG AG (i) = Empirical correction factor for aboveground exposed produce type i to address

possible overestim ate of the diffusive transfer of chemical from the outside to the inside of bulky produce, such as fruit (unitless)

ρ a = Density of air (g/m 3 )



### Note that Equation 3-4 differs from Equation 5-18 in HHRAP, from which it is derived

. In HHRAP, Equation 5-18 includes the term Q x Fv to indicate the emissions rate, in g/sec, of chemical from the source and the fraction of the chemical in vapor phase in the air. HHRAP also includes the parameter Cyv , or the unitized

yearly average air concentration of vaporphase chemical in units of μg -sec/g-m 3 

### . For MIRC, the user inputs the average annual total air concentration of the chemical, Ca

, for a specific location relative to the source in units of g /m 3 

### ; MIRC includes a chemical-specific default value for Fv for chemicals included in its database. Th e air concentration might be a value measured near that location or a value estimated by a fate and transport model such as TRIM.FaTE

. Users of TRIM.FaTE should note that the average annual concentration of the total chemical in air (i.e., total of both vapor and particulate phases)

, Ca , output from TRIM.FaTE is in units μg/m 3 

### ; therefore, the user must adjust the value to units of g/m 3 

### (i.e., divide by 1,000 μg/g) b efore entering it in MIRC.

The calculations of chemical concentration in aboveground produce, ( C AG -produce- DW



### ), shown above, are on a dry-weight (DW) basis. The family FFC food ingestion rates, on the other hand, are on a fresh- or wet-weight (WW) basis. MIRC therefore calculates the concentration in aboveground produce on a wet-weight basis, C AG -produce- WW



### , using Equation 3-5 and the moisture content ( MAF

) of the FFC food category.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 16 

### Equation 3-5

. Conversion of Aboveground Produce Chemical Concentration from D ry - to W et -Weight Basis

where:

C AG

- produce

- WW

(i) = Chemical concentration in edible portion o f aboveground produce type i on a

we t

- weight (WW) basis (mg/kg produce WW)



### C AG

- produce

- D W

(i) = Chemical concentration in edible portion of aboveground produce type i on a dry

- weight ( D W) basis (mg/kg produce DW)

MAF (i) = Moisture adj ustment factor for ab oveground produce type i to convert the chemical concentration estimated for dry

- weight produce to the corresponding chemical concentration for full

- weight fresh produce (percent water)



### 3.1.1.2 Belowground Produce The equations by which chemical concentrations are estimated in belowground produce are different for nonionic organic chemicals than for inorganic chemicals and ionic organic chemicals.

3.1.1.2.1 Nonionic Organic Chemicals For belowground produce, the nonionic organic chemical concentration in the tuber or root vegetable is derived from exposure to the chemical in soil and is estimated using an empirical root concentration factor ( RCF) and the average chemical concentration in the soil at the rootzone depth in the produce-growing area ( Cs root -zone_produce 

### ), as shown in Equation 3-6. The RCF relates the chemical concentration in the plant on a wet-weight basis to the average chemical concentration in the root-zone soil ( Cs root -zone_produce 

### ) on a dry-weight basis. Belowground produce (i.e., tubers or root vegetables) are protected from the deposition and vapor transfer by being covered by soil

. Therefore, root uptake of chemicals is the primary mechanism through which belowground produce becomes contaminated.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 17 

### Equation 3-6

. Chemical Concentration in Belowground Produce: Nonionic Organic Chemicals

where:

C BG

- produce

- WW = Concentration of chemical in belowground (BG) produce (i.e., tuber or root

vegetable) on a wet

- weight (WW) basis (mg chem ical /kg produce WW) *

Cs root

- zone_produce = Average chemical concentration in soil at root

- zone depth in produce

- growing

area , on a dry

- weight (DW) basis (mg chemical /kg soil DW )

RCF = Chemical

- specific root concentration factor for tubers and root prod uce (L soil

pore water/kg root WW) *

VG rootveg = Empirical correction factor for belowground produce ( i.e., tuber or root

vegetable ) to account for p ossible overestimate of the diffusive transfer of chemicals fr om the outside to the inside of bulky tubers or roots (based on carrots and potatoes) (unitless) *

Kds = Chemical

- specific soil/water partition coefficient (L soil pore water/kg soil DW)

UCF = Units conversion factor of 1 kg/L
* Note that there is only one type of BG produce; hence there are no p lant

- type

- specific subscripts



### The RCF, as developed by Briggs et al

. (1982), is the ratio of the chemical concentration in the edible root on a wet-weight basis to its concentration in the soil pore water. RCFs are based on experiments with growth solutions (hydroponic) instead of soils; therefore, it is necessary to divide the soil concentration by the chemical-specific soil/water partition coefficient ( Kd s ). There is no conversion of chemical concentrations in belowground produce from DW to WW because the values are already on a WW basis.

For nonionic organic chemicals, it is possible to predict RCF values and Kds values (for a specified soil organic carbon content) from a n estimate of the chemical’s Kow from empirically derived regression models

. Those models are shown in HHRAP Appendix A-2, Equations A-2- 14 and A-2-15 ( RCF

) and in Equations A-29 and A-2-10 ( Kds ). The RCF and Kds values so calculated for many of the chemicals in HHRAP are included in the MIRC database (including the values for PAHs and dioxins).

3.1.1.2.2 Inorganic and Ionic Organic Chemicals For inorganic chemicals and ionized organic chemicals, it is not possible to predict RCF or Kds values from Kow

. For inorganic chemicals, one must use empirical values for the root/soil bioconcentration factor measured for specific chemicals. The root/soil bioconcentration factor, now specified as Br BG -produce- DW 

### , must be obtained from the literature for each inorganic chemical on a DW basis. For inorganic chemicals, therefore, Equation 3-7 is used instead of Equation 3-6.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 18 

### Equation 3-7

. Chemical Concentration in Belowground Produce: Inorganic Chemicals

where:

C

BG

- produce

- DW = Concentration of chemical in edible portion of aboveg round produce, due to

root uptake from soil at root

- zone depth in the produce

- growing area, on a dry

weight (DW) basis (mg/kg produce DW )

Cs root

- zone_produce = Average chemical concentration in soil at root

- zone depth in produce

- growing

area (mg/kg soil D W )

Br BG

- produce

- DW = Chemical

- specific root/ soil chemical bioconcentration factor for edible portion

of belowground produce ( g soil DW / g produce DW )

VG rootveg = Empirical correction factor for belowground produce (as in Equation 3

- 6 )

(unitless)



### As fo r the aboveground produce, the DW estimate of concentration of chemical in the root vegetables must be transformed to a WW estimate, as shown in Equation 3-8.

Equation 3-8

. Conversion of Belowground Produ ce Chemical Concentration from D ry - to W et -Weight Basis

where:

C B G

- produce

- WW = Chemical concentration in edible portion of belowground produce on a weight

weight (WW) basis (mg/kg produce WW)

C BG

- produce

- DW = Concentration of che mical in edible portion of aboveground produce, due to root

uptake from soil at root

- zone depth in the produce

- growing area, on a dry

weight (DW) basis (mg/kg produce DW )

MAF (BG) = Moisture adj ustment factor (as in Equation 3

- 5, but single value for below ground produce) (percent water)



### 3.1.2 Estimating Chemical Concentrations in Animal Products Chemical concentrations in animal products are estimated based on the amount of chemical consumed by each animal group m through each plant feed type i ( Plant

Ch -Intake(i,m) 

### ) and incidental ingestion of soil for ground-foraging animals ( Soil Ch -Intake(m) 

### )

. Exhibit 3-3 summarizes the pathways by which chemicals are transferred to these home- or farm-raised animal food products. Note that for a general screening-level assessment, all of the pathways can be modeled, as is done for EPA’s RTR calculation of screening threshold emission rates for PB

HAPs (EPA 2008b).

The feed options for farm animals in MIRC include forage (plants grown on-site for animal grazing, such as grass), silage (wet forage grasses, fresh-cut hay, or other fresh plant material that has been stored and fermented), and grain products grown on the farm. As seen in Exhibit 3-3 , the algorithms in MIRC for chemical intake with plant feeds ( Plant Ch -Intake(i,m) 

### ) are based on the assumptions that beef and dairy cattle consume all three plant feed products, while pigs consume only silage and grain, and chickens consume only grain.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 19 

### Exhibit 3

- 3

. Chemical Transfer Pathways for Animal Products

Farm Food Media Chemical Transfer Pathways

Animal Products Beef and total dairy (including milk) Ingestion of forage, silage, and grain a Incidental s oil ingestion

Pork I ngestion of silage and grain a Incidental s oil ingestion Poultry and eggs Ingestion of grain a Incidental s oil ingestion

a Chemical concentrations in plant feed (i.e., forage, silage, and grain ) are estimated via intermediate calculatio ns (see Equations 3

- 13, 3

- 14, 3

- 3, and 3

- 4 )

.


### Forage and silage are exposed to the air and can accumulate chemicals via direct deposition of particle-bound chemical and transfer of vapor-phase chemical, while all animal feed grains are assumed to be protected from the air by a husk or pod (e.g., corn, soybeans). All three animal feed products are assumed to accumulate chemical via root uptake.

Chemical concentrations are estimated for animal feeds using algorithms analogous to those for aboveground farm produce described above. MIRC uses Equation 3-9 to calculate the concentration of chemical in beef, pork, or total dairy and Equation 3- 10 to calculate the concentration of chemical in poultry or eggs

. The chemical concentration in mammalian farm animals (i.e., beef and pigs) is adjusted using a metabolism factor ( MF ) that accounts for endogenous degradation of the chemical (see Equation 3-9). MF is set to 1.0 for chemicals that are not metabolized and for chemicals for which the metabolic degradation rate is unknown. Although other vertebrates, including birds, are likely to have similar metabolic pathways for most chemicals, the conservative assumption is that birds do not metabolize any chemicals; therefore, the MF

is omitted from Equation 3- 10 for poultry and eggs.

Equation 3-9

. Chemical Concentration in Beef, Pork, or Total Dairy

where:

C

mammal (

m ) = Concentration of chemical in mammalian animal product m , where m = beef, pork, or total dair y (mg chemical /kg animal product WW )

Ba (m) = Chemical

- specific biotransfer fa ctor for chemical in diet to chemical in animal

food product m , where m = beef, pork, or total dairy ( [mg chemical/kg animal product WW] / [mg chemical intake/day] or day/kg W W )

MF = Chemical

- specific m ammalian m etabolism factor that accounts for endogenous

degradation of the chemical (unitless)

Soil Ch

- Intake (m) = Incidental ingestion of chemical in surface soils by livestock type m during

grazing or consumption of foods place d on the g round (mg/day); see Equation 3

- 11 below

Plant Ch

- Intake(

i,m ) = For livestock (animal product) type m , i ngestion of chemical from plant feed type i (mg chemical /kg livestock WW ) ; see Equation 3

- 12 below (I f m = beef or total dairy, then n = 3 an d i = fo rage, silage, and grain;

m = pork, then n = 2 and i = silage and grain ;

m = poultry, then n = 1 and I = grain.)Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 20 

### Equation 3- 10

. Chemical Concentration in Poultry or Eggs

where:

C

poultry( m ) = Concentration of chemical in food product m , where m = poultry or eggs (mg chemical /kg animal product WW)

Ba (m) = Chemical

- specific biotransfer factor for food product m , where m = poultry or

eggs (day/kg animal p roduct WW)

Soil Ch

- Intake (m) = Incidental ingestion of chemical in surface soil s by consumption of food on the

ground (mg chemical /day) where m = poultry ; see Equation 3

- 11

Plant Ch

- Intake (

i,m ) = For poultry (and eggs), animal m , i ngestion of the chemica l in plant feed type i (mg chemical /day), which for poultry is limited to grain ; see Equation 3

- 1 2



### In MIRC, the incidental ingestion of the chemical in soils by livestock during grazing or consumption of feed placed on the ground ( Soil Ch -Intake(m) 

### ) is estimated using empirical soil ingestion rates ( Qs ) and a soil bioavailability factor for livestock ( Bs ), as shown in Equation 3- 11 . At this time, the default value for Bs in MIRC for all chemicals is 1.0 (i.e., t he chemical in soil is assumed to be 100 percent bioavailable to the animal). This assumption may be reasonably accurate for the soil surface to which airborne chemical is deposited. MIRC allows the user to enter a surface soil concentration for areas where livestock forage, Cs S-livestock 

### , that is distinct from the surface soil concentration input for areas where produce may be grown and where humans might incidentally ingest soils (see Section 6.1).

Equation 3- 11

. Incidental Ingestion of Chemical in Soil by Livestock

where:

Soil

Ch

- Intake (m) = Incidental ingestion of the chemical in surface soils by livestock type m during

grazing or consumption of foods placed on the ground (mg chemical /day)

Qs (m) = Quantity of soil eaten by animal type m each day (kg soil DW /day)

Cs s

- livestock = Chemical c oncentration in surface soi l in contaminated area where livestock

feed ( mg chemical /kg soil DW)

Bs = Soil bioavailability factor for livestock (unitless) (assumed to be the same for

birds and mammals)



### Animal ingestion of the chemical in feed is calculated for each type of livestock based on their assumed diets. For m = beef and dairy cattle, chemical intake is estimated for all three feed types: i =

forage, silage, and grain. For pork, chemical intake is estimated only for silage and grain. The chemical intake for poultry is based on grain consumption only. The intake of chemical with each feed type

, i

, Plant

Ch -Intake(i,m) 

### , is calculated separately according to Equation 3- 12

. No te that the animal feed ingestion rates are on a dry-weight (DW) basis; hence, no DW to wet weight (WW) conversion is needed.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 21 

### Equation 3- 12

. Ingestion of Chemical in Feed by Livestock

where:

Plant Ch

- Intake(

i,m ) = Ingestion of chemical in plant feed type i (mg chemical /day) , where i = forage, silage, or grain , for livestock type m

F ( i,m ) = Fraction of plant feed type i obtained from contaminated area used to grow animal feed , where I = forage, silage, or grain (unitless) for livestock type m

Qp ( i,m ) = Q uantity of plant feed type i consumed per animal per day (kg plant feed DW/day) , where i = forage, silage, or grain , for livestock type m



### C feed(i) = Concentration of chemical in inges ted plant feed type i (mg chemical/kg plant

feed DW ) , where i = forage, silage, or grain



### The concentrations of chemical in the three different types of plant feeds for livestock are calculated according to Equation 3-13. The equation is the same as that for aboveground produce in Equation 3-1, with the exception that the concentrations are for plants used as animal feeds (not produce consumed by humans) and all types of plant feed (i.e., forage, silage, and grain) are aboveground.

Equation 3- 13

. Chemical Concentration in Livestock Feed (All Aboveground)

where:

C feed(i) = Concentration of chemical in plant feed type i on a dry

- weight (DW) basis (mg

chemical /kg plant feed DW )

, wher e i = forage, silage, or grain

Pr feed(i) = Concentration of chemical in plant feed type i due to root uptake from soil

(mg/kg DW)

, where i = forage, silage, or grain ; see Equation 3

- 14 below

Pd (i) = Concentration of chemical in plant feed type i due to w et and dry deposition of particle

- phase chemical (mg/kg DW)

, where i = forage, silage, or grain; when i = grain, the Pd term equals zero

Pv (i) = Concentration of chemical in plant feed type i due to air

- to

- plant transfer of
vapor

- phase chemical (μg/g [or mg/kg] DW) where i = forage, silage, or grain ; when i = grain, the Pd term equals zero



### MIRC calculates the chemical concentration in animal feed due to root uptake from the soil using Equation 3- 14 . The equation is the same as Equation 3-2, except that a Br value appropriate to grasses is used and MIRC allows for different soil concentrations in the area used to grow animal feed than in the area used to grow produce for human consumption (see Section 6.1, user inputs). Note that for feed type i = grai ns , the Pd and Pv terms do not apply (are set to zero), because the feed products (i.e., corn kernels, soy beans) are protected from the air (i.e., by husks, pods).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 22 

### Equation 3- 14

. Chemical Concentration in Livestock Feed Due to Root Uptake

where:

Pr feed(i) = Concentration of chemical in plant feed type i due t o root uptake from soil on a

dry

- weight (DW) basis (mg chemical /kg plant feed DW)

, where i = forage, silage, or grain

Cs root

- zone_feed(i) = Average chemical concentration in soil at root

- zone depth in area used to grow

plant feed type i (mg chemical /kg soil DW )

, where i = forage, silage, or grain

Br feed(i) = Chemical

- specific p lant

- soil bioconcentration factor for plant feed t ype i (kg soil

DW/kg plant feed DW )

, where i = forage, silage, or grain



### The algorithms used to calculate Pd (i) 

### and Pv

(i) 

### when plant feed type i

= forage and silage are identical to those used to calculate Pd (i) 

### and Pv

(i) 

### for aboveground exposed produce (i.e., Equations 3-3 and 3-4, respectively)

. There are no conversions of DW feed to WW feed, because all feed ingestion rates for liv es tock are based on DW feed.



### 3.2 Chemical Intake Calculations for Adults and Non-Infant Children
MIRC calculates human chemical intake rates from the ingestion of home-grown foods as average daily doses (ADDs) normalized to body weight for each age group, chemical, and food type separately. ADDs , calculated using Equation 3-15

, are expressed in milligrams of chemical per kilogram of receptor body weight per day (mg/kg-day).

Equation 3- 15

. Average Daily Dose for Specified Age Group and Food Type

where:

ADD (y ,i ) = Average daily dose for age group y from food type or ingestion medium i (mg chemical /kg body weight

- day )

C (i) 

### = Concentration of chemical in food type i harvested from the contaminated area

(m g chemical / kg food or mg food /L water )

IR (y,i) 

### = Ingestion rate for age group y o f food type i (kg/day or L/day)

FC (i) 

### = Fraction of food type i that was harvested from contaminated area (u nitless )

ED (y) 

### = Exposure duration for age group y (years)

BW (y) 

### = Body weight for age group y (k g )

AT (y) 

### = Averaging time for calculation of da ily dose (years) for age group y , set equal to ED in MIRC

EF (y) 

### = Annual exposure frequency for age group y (days)



### Equation 3- 15 takes into account the chemical concentration in each food type i (or in water), the quantity of food brought into the home for consumption, the loss of some of the mass of the foods due to preparation and cooking, how much of the food is consumed per year, the amountAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 23 

### of the food obtained from contaminated areas , and the consumer’s body weight ( EPA 1997 a , 2003a) . In MIRC, ADDs are calculated separately for each chemical, home-grown food type, and consumer age group.

ADD values, expressed as intakes, not absorbed doses, are appropriate for comparison with RfDs and for use with cancer slope factors (CSFs) to estimate risk, as discussed in Section 5. An exception is for the breast-milk exposure pathway, where the dose absorbed by the mother is relevant to calculating the dose available to and absorbed by her nursing infant, as discussed in Section 3.4.

MIRC evaluates only one contaminated area (set of environmental concentrations), or exposure scenario, at a time. For screening level assessments, all components of this equation are assumed to remain constant for consumers in a given age group over time (e.g., seasonal and

annu al variations in diet are not explicitly taken into account). To calculate an ADD (y ,i ) 

### from the contaminated area for food group i over an entire lifetime of exposure, age-group-specific ingestion rates and body weights are used for the age groups describ ed in Section 2.3. In MIRC, the averaging time used to calculate the daily dose for an age group ( AT y 

### ) is equal to the exposure duration for that group ( ED y 

### ); therefore these variables drop out of Equation 3-15.

For each chemical included in a screening scenario, total average daily exposure for age
group y ( ADD (y) 

### ) is estimated as the sum of chemical intake from all ingestion pathways combined:

Incidental soil ingestion; Ingestion of fish; Ingestion of homegrown fruits (exposed and protected); Ingestion of homegrown vegetables (exposed, protected, and root); Ingestion of animal products from home-raised animals:

o Milk and other dairy products from cows,

o Beef products,

o Pork products, and

o Poultry and eggs; Ingestion of drinking water from specified source; and Ingestion of breast milk by infants.

Note that the last exposure pathway is limited to infants.

The algorithms for the first six exposure pathways listed above are described in Sections 3.2.1 through 3.2.6. The algorithms for the breast-milk ingestion pathway are described in Section 3. 4.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 24 

### 3.2.1 Chemical Intake from Soil Ingestion Equation 3- 16 shows the equation used to estimate chemical intake through incidental ingestion of soil.

Equation 3- 16

. Chemical Intake from Soil Ingestion

where:

ADD Soil (y) = Average daily chemical intake from incidental ingestion of soil or ingestion by child in age group y ( mg chemical /kg body weight

- day )

C Soil 

### = Concentration of chemical in soil from contaminated area on a dry

- weight (DW) basis ( μg/g soil DW )

IR Soil (y) 

### = Soil ingestion rate for age group y ( g DW /day )

FC Soil 

### = Fraction of s oil ingested that is from contaminated area (u nitless )

BW (y) 

### = Body weight for age group y (k g )

E F 

### = E xposure f req uency ; number of days per year of exposure for family(ies) as specified for scenario ( 365 days)
Note: MIRC saves soil ingestion rates in units of mg/day (not g/day); therefore, there is an additional 0.001 g/mg conversion unit in the actual MIRC algo rithm than shown here.



### 3.2.2 Chemical Intake from Fish Ingestion Ingestion of locally caught fish is included as a possible exposure pathway in MIRC (Equation 3- 17 ). Two types of fish are included in the exposure algorithm: trophic level 3 (T3) fish, equivalen t to small “pan” fish such as bluegill, and trophic level 4 (T4) fish, equivalent to game fish such as trout and walleye

. The chemical concentration in fish in Equation 3- 17 is estimated as the consumption-weighted chemical concentration using Equation 3- 18

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 25 

### Equation 3- 17

. Chemical Intake from Fish Ingestion

Equation 3-18

. Consumption-weighted Chemical Concentration in Fish

where:

ADD Fish (y) = Average daily chemical intake from ingestion of local fish for age group y ( mg/kg

- day )

L 1 Fish * 

### = Weight of fish brought into home that is discarded during preparation (e .g.,

head, bones, liver, other viscera, belly fat , skin with fat) ( unitless )

L2 Fish * 

### = Loss of weight during cooking, such as evaporation and loss of fluids into pan

(unitless )

C FishT3 

### = Chemical c oncentration in whole fish for trophic level 3 ( T3 ) fish on a wet

weight (WW) basis ( mg/kg WW )

C FishT4 

### = Chemical c oncentration in whole fish for trophic level 4 ( T 4) fish on a wet

weight (WW) basis ( mg/kg WW)

F T3 

### = Fraction of fish intake that is from T3 ( unitless )

F T4 = Fraction of fish intake that is from T4 ( unitless )

C Fish 

### = Consumption

- weighted mean chemical concentration in total fish (i.e., as

specified by Equation 3

- 18) ( mg/kg WW )

FC Fish 

### = Fraction of local fish consumed derived from contaminated area ( unitless )

BW (y) 

### = Body weight for age y ( kg )

IR Fish(y) * 

### = Local fish i ngestion rate for age y (g WW/day)

EF 

### = Exposure frequency; number of days per year of exposure for family(ies) as

specified for scenario ( 365 days)
* Parameter values must be internally consistent

. In contrast to the tables included in MIRC for ingestion rate options for homegrown food products, which are based on the products as brought into the home from the field (see Section 6.3.3), the tables of fish ingestion rate options included in MIRC are from CSFII data (see Section 6.3.4) and, therefore, are on an “as consumed” basis (i.e., after preparation and cooking losses), and L1 and L2 therefore are set equal to zero

. If the user wishes to enter local fish ingestion rates on an “as harvested” basis, the user also should enter L1 and L2 values as specified in Section 6.4. 3.



### When whole fish are prepared for cooking, it is usual for the viscera, head, and fins to be removed, particularly for larger fish. Many persons also remove (or do not eat) the skin, bones, and belly fat. EPA has, therefore, estimated the proportion of the weight of whole fish that tends to be lost during preparation and cooking across a variety of fish species (Exposure Factors Handbook Table 13-5, EPA 1997 a) and included those losses in its HHRAP algorithms for chemical intake from fish (L1 Fish 

### and L2 Fish 

### in Equation 3-17).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 26 

### 3.2.3 Chemical Intake from Fruit Ingestion Average daily doses of a chemical from homegrown exposed fruits are calculated separately for exposed and protected fruits (Equations 3- 19 and 3- 20 , respectively).

Equation 3- 19

. Chemical Intake from Consumption of Exposed Fruits

Equation 3- 20

. Chemical Intake from Consumption of Protected Fruits

where:

ADD ExpFruit (y) ADD ProFruit(y) = Average daily chemical intake from ingestion of exposed fruit or protected fruit

(depending on subscript) ( mg chemical /kg body weight

- day )

L1 ExpFruit 

### = Mean reduction in fruit weight resulting fr om removal of skin o r peel, core or

pit, stems or caps, seeds and defects, and from draining liquids from canned or frozen forms (u nitless )

L1 ProFruit 

### = Mean reduction in fruit weight that results from paring or other preparation

techniques for protected fruits (u nitless )

L 2 ExpFruit 

### = Mean reduction in fruit weight that results from draining liquids from cooked

forms of the fruit (u nitless )

C ExpFruit C ProFruit 

### = Chemical c oncentration in whole exposed fruits or whole protected fruits

(depending on subscript) on a wet

- weight (WW) basis ( mg chemical /kg exposed fruit WW)

EF 

### = Exposure frequency; number of days per year of exposure for family(ies) as

specified for scenario ( 365 days)

FC ExpFruit FC ProFruit 

### = Fraction of exposed fruits or protected fruits (depending on subscri pt) obtained

from contaminated area (unitless)

IR ExpFruit(y) IR ProFruit(y) 

### = Ingestion rate of home

- grown exposed fruits or protected fruits (depending on

subscript) for age y (g WW /kg body weight

- day)



### Fruit ingestion rates in the survey were based on weights of unprepared fruits (e.g., one apple; one pear) or the weight of a can of fruit (e.g., 8 oz can). The weight of the fruit ingested is less than the initial weight owing to common preparation actions ( L1 ExpFruit 

### and L1 ProFruit 

### ; e.g., coring apples and pears; peeling apples; pitting cherries). Cooking of exposed fruit (e.g., berries, apples, peaches) often results in further weight loss that results from liquids lost during cooking and drained from the cooking vessel ( L2 ExpFruit 

### )

. EPA has assumed that cooking of protected fruit results in no loss of weight for the fruit.

3.2.4 Chemical Intake from Vegetable Ingestion MIRC includes three separate algorithms for homegrown vegetables adapted from EPA’s HHRAP Modeling System ( EPA 2005a ): one for exposed vegetables such as asparagus, broccoli, lettuce, and tomatoes (although they are actually a fruit); one for protected vegetables such as corn, cabbage, soybeans, and peas; and one for root vegetables such as carrots, beets, and potatoes (see Equations 3- 21 , 3- 22 , and 3- 23 , respectively)

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 27 

### Equation 3- 21

. Chemical Intake from Exposed Vegetables

Equation 3- 22

. Chemical Intake from Protected Vegetables

Equation 3- 23

. Chemical Intake from Root Vegetables

where:

ADD ExpVeg (y) ADD ProVeg(y) ADD RootVeg(y) = Average chemical intake from ingestion of exposed vegetable s, protected

vegetable s, or root vegetable s (depending on subscript) for age group y ( mg chemical /kg body weight

- day )

L1 ExpVeg 

### = Mean net preparation and cooking weight loss for exposed vegetables

(u nitless ) ; includes removing stalks, par ing skins, discarding damaged leaves

L1 ProVeg 

### = Mean net cooking weight l oss for protected vegetables (u nitless ) ; includes

removing husks, discarding pods of beans and peas, removal of outer leaves

L1 RootVeg 

### = Mean net cooking weight loss for root vegeta bles (u nitless ) ; includes losses

from removal of tops and paring skins

L2 RootVeg = Mean net post cooking weight loss for root vegetables from draining cooking

liquids and removal of skin after cooking (u nitless )

C ExpVeg C ProVeg C RootVeg 

### = Chemical concen tration in exposed vegetables

, protected vegetables , or root

vegetables (depending on subscript) on a wet

- weight (WW) basis ( mg chemical /kg vegetable WW)

EF 

### = Exposure frequency; number of days per year of exposure for family(ies) as

specified for scenari o ( 365 days)
FC ExpVeg FC ProVeg FC RootVeg = Fraction of exposed vegetables

, protected vegetables , or root vegetables

(depending on subscript) obtained from contaminated area (u nitless )

IR ExpVeg(y) IR ProVeg(y) IR RootVeg(y) 

### = Ingestion rate of exposed veg etables

, protected vegetables , or root vegetables

(depending on subscript) for age group y (g vegetable WW /kg body weight

day )Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 28 

### 3.2.5 Chemical Intake from Animal Product Ingestion Calculations of chemical intake from the consumption of farm animals and related food products are provided below in Equations 3- 24 through 3- 28 for homegrown beef, dairy (milk), pork, poultry, and eggs, respectively.

Eq uation 3- 24

. Chemical Intake from Ingestion of Beef

where:

ADD B eef (y) = Average daily chemical intake from ingestion of beef for age group y ( mg/kg

day )

L1 B eef 

### = Mean net cooking loss for beef (u nitless )

L2 B eef 

### = Mean net post cooking loss for beef (u nitless )

C B eef 

### = Concentration of contaminan t in beef ( mg/kg WW ) )

EF 

### = Exposure frequency; number of days per year of exposure for family(ies) as

specified for scenario ( 365 days)

IR Beef(y) 

### = Ingestion rate of contaminated beef for age group y (g WW / kg

- day )

FC Beef = Fraction of beef consumed r aised on contaminated area or fed contaminated

silage and grains (u nitless )



### Equation 3- 25

. Chemical Intake from Dairy Ingestion

where:

ADD D airy (y) = Average daily chemical intake from ingestion of total dairy for age group y ( mg/kg

- day )

C D airy 

### = Average c oncentration of contaminant in total dairy ( mg/kg WW )

EF 

### = Exposure frequency; number of days per year of exposure for family(ies) as

specified for scenario ( 365 days)

IR D air y(y) 

### = Ingestion rate of contaminated total dairy for age group y (g WW /kg

- day )

FC D airy 

### = Fraction of total dairy products from contaminated area (unitless)Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 29 

### Equation 3- 26

. Chemical Intake from Pork Ingestion

where:

ADD P ork (y) = Average daily chemical intake from ingestion of pork for age group y ( mg/kg

day )

L1 P ork 

### = Mean net cooking loss for pork (u nitless ); includes dripping and volatile losses

during cooking; averaged over vari ous cuts and preparation methods

L2 P ork 

### = Mean net post cooking loss for pork (u nitless ); includes losses from cutting,

shrinkage, excess fat, bones, scraps, and juices; averaged over various cuts and preparation methods

C P ork 

### = Concentration of contamin ant in pork ( mg/kg WW )

EF 

### = Exposure frequency; number of days per year of exposure for family(ies) as

specified for scenario ( 365 days)

IR P ork(y) 

### = Ingestion rate of contaminated pork for age y ( g WW/kg

- day)

FC P ork = Fraction of pork obtained from co ntaminated area (u nitless )



### The reduction in the weight of pork during and after cooking may correlate with an increase or decrease in the concentration of the chemical in the pork as consumed depending on the chemical and depending on the cooking method.

Equation 3- 27

. Chemical Intake from Poultry Ingestion

where:

ADD P oultry (y) = Average daily dose (chemical intake) from ingestion of poultry ( mg/kg

- day )

L1 P oultry 

### = Mean net cooki ng loss for poultry (u nitless )

L2 P oultry 

### = Mean net post cooking loss for poultry (u nitless )

C P oultry 

### = Concentration of chemical in poultry ( mg/kg WW )

EF 

### = Exposure frequency; number of days per year of exposure for family(ies) as

specified for scenar io ( 365 days)

IR P oultry(y) 

### = Ingestion rate of poultry for age group y ( g WW /kg

- day )

FC P oultry = Fraction of poultry from contaminated area or fed contaminated grains

(u nitless )Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 30 

### Equation 3- 28

. Chemical Intake from Egg Ingestion

where:

ADD E gg (y) = Average daily chemical intake from ingestion of egg s for age group y ( mg/kg

day )

C E gg 

### = Concentration of contaminant in eggs ( mg/kg WW )

EF 

### = Exposure frequency; number of days per year of exposure for family(ies) as

specified for scenario ( 365 days)

IR E gg(y) 

### = Ingestion rate of contaminated eggs for age group y ( g WW /kg

- day )

FC E gg 

### = Fraction of eggs obtained from contaminated area (u nitless )



### 3.2.6 Chemical Intake from Drinking Water Ingestion If the user chooses to evaluate chemical ingestion via drinking water, the user specifies a chemical concentration in g/L (equivalent to mg/mL) based on their particular scenario. The chemical concentration could represent water from groundwater wells, community water, nearby surface waters, or other source. For this exposure pathway, ingestion rates are in units of milliliters of water per day (mL/day).

Equation 3- 29

. Chemical Intake from Drinking Water Ingestion

where:

ADD DW(y) = Average daily chemical intake from ingestion of drinking water from local residential water source for age group y ( mg/kg

- day )

C DW 

### = Concentration of contaminant in drinking water ( g/ L)

IR DW (y) 

### = Drinking water i ngestion rate for age group y (mL /day )

FC DW 

### = Fraction of drinking water obtained from contaminated area (u nitless )

BW (y) 

### = Body weight of age group y (kg)

EF 

### = Exposure frequency; number of days per year of exposure for family(ies ) as

specified for scenario ( 365 days)



### 3.3 Total Chemical Intake
To estimate the total ADD, or intake of a chemical from all of the exposure media that a singleindividual in each age group is expected to contact (e.g., soil, local fish, five types of homegrown produce, and five types of home-raised animals or animal products), the media-specific chemical intakes are summed for each age group. Total average daily exposure for a particular
age group y

( ADD (y) 

### ) is estimated as the sum of chemical intake from all ingestion pathways combined, as illustrated in Equations 3-30 through 3- 35 below.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 31 

### Equations 3- 30 to 3-35. Total Average Daily Dose of a Chemical for Different Age Groups

Equation 3- 30

.

Equation 3- 31

.

Equation 3- 32

.

Equation 3- 33

.

Equation 3- 34

.

Equation 3- 35

.

where i represents the i th 

### food type or ingestion medium and n equals the total number of food types or ingestion media, and ADD parameters are defined below:

ADD (<1) = Total average daily dose of chemical for infants less than one year from

ingestion of breast milk (mg/kg

- day)

ADD (1

-

2) = Total av erage daily dose of chemical from all ingestion sources for children ages 1 through 2 years (mg/kg

- day)

ADD (3

- 5) = Total average daily dose for children ages 3 through 5 years (mg/kg

- day)

ADD (6

- 11) = Total average daily dose for children ages 6 through 1 1 years (mg/kg

- day)

ADD (12

- 19) = Total average daily dose for children ages 12 through 19 years (mg/kg

- day)

ADD ( a dul t) = Total average daily dose for adult age 20 up to 70 years (mg/kg

- day)



### The lifetime average daily dose ( LADD ) is calculated as the ti me -weight average of the ADD values for each age group (Equation 3-36).

Equation 3- 36

. Lifetime Average Daily Dose (LADD)

The time-weighting factors simply equal the duration of exposure for the specified age category in years divided by the total lifespan, assumed to be 70 years

. For risk assessments for chemicals with a subchronic RfD or for developmental effects in children, ADD (y) 

### values for the child age groups are compared with the RfD (see Section 5).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 32 

### 3.4 Chemical Intake Calculations for Nursing Infants
The scientific literature indicates that infants can be exposed to some chemicals via their mothers’ breast milk . The magnitude of the exposure can be estimated from information on the mother’s exposure, data on the partitioning of the chemical into various compartments of the mother’s body and into breast milk, and information on the infant’ s consumption of milk and absorption of the chemical

. To add this exposure pathway to the MIRC application

, we adapted exposure algorithms and default assumptions from EPA’s Methodology for Assessing Health Risks Associated with Multiple Pathways of Exposure to Combustor Emissions ( EPA 1998)

, hereafter referred to as MPE, as explained below

. Note that this pathway generally is of most concern for lipophilic bioaccumulative chemicals (e.g., dioxins) that can cause developmental effects. The period of concern for the more hydrophilic

chemicals that cause developmental effects generally is earlier, that is, from conception to birth. Hydrophilic chemicals generally exchange well between the maternal and fetal blood supplies at the placenta.

3.4.1 Infant Average Daily Absorbed Dose The average daily dose of chemical absorbed by the infant ( DAI inf 

### ) is estimated in MIRC with Equation 3- 37 . This basic exposure equation relies on the concentration of the chemical in the breast milk, the infant’s breast -milk ingestion rate ( IR milk 

### ), the absorption efficiency of the chemical by the oral route of exposure ( AE inf 

### ), the bodyweight of the infant ( BW inf 

### ), and the duration of breast feeding ( ED ). Equation 3- 37 is EPA’s ( EPA 1998) modification of an average daily dose for the infant model first published by Smith (1987) and includes variables for both the concentration of the chemical in the breast milk fat ( C milkfat 

### ) and the concentration of the chemical in the aqueous phase of breast milk ( C aqueous 

### )

. The remainder of the DAI inf 

### -associated equations assume that most chemicals of concern will partition either to the lipid phase or to the aqueous phase of breast milk, although some chemicals may partition significantly to both phases of milk. Thus, the remaining equations in MIRC assume that either C milkfat 

### or C aqueous 

### is equal to zero and hence drops out of the equation.

For the parameters in Equation 3- 37 (and the equations that follow) that are not calculated from another equation, an EPA default value and options for other values available in MIRC for the infant breast-milk-exposure pathway are described in Section 6.4. The user also can overwrite those parameter values with a different value from the literature as appropriate.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 33 

### Equation 3- 37

. Average Daily Dose of Chemical to the Nursing Infant

where:

DAI inf = Average daily dose of chemical absorbed by infant (mg chemical /kg body weight

- day)

C milkfat = Concentration of chemical in lipid phase of maternal milk ( mg chemical /kg milk

lipid ; calculated using Equation 3

- 3 8 )

f mbm = Fraction of fat in breast milk (unitless)

C aqueous = Concentration of chemical in aqueous phase of maternal milk ( mg chemical /kg

aqueous phase milk ; calculated using Equation 3

- 42 )

IR milk = Infant milk ingestion rate over the duration of nursing ( kg milk /d ay )

AE inf = Absorption efficiency of the chemical by the oral route of exposure (i.e.,

c hemical

- specific fraction of ingested chemical that is absorbed by the infant) (unitless )

ED = Exposure duration, i.e., duration of breast feeding (days)

BW inf = Bo dy weig ht of infant averaged over the duration of nursing (kg)

AT = Averaging time associated with exposure of interest; equal to ED (days)



### As mentioned above, Equation 3- 37 includes terms for the chemical in both the lipid- and nonlipid phases of milk. Th e remaining equations, however, assume that a chemical of concern will partition to the lipid or aqueous phase of breast milk. Different models are used to estimate C milkfat 

### (described in Section 3.4.2) and C aqueous 

### (described in Section 3.4.3).

3.4.2 Chemical Concentration in Breast Milk Fat When developing MPE ( EPA 1998), EPA reviewed three first-order kinetics models for estimating chemical concentration in breast milk fat. The model selected for use in MPE is the model used in MIRC

. It is a changing-concentration model that EPA adapted from a model by Sullivan et al

. (1991). The model, shown in Equation 3-38, estimates the average chemical concentration in the breast milk over the entire period of breast feeding by reference to a maximum theoretical steady-state concentration. Studies of lipophilic chemicals such as dioxins suggest that concentrations in the maternal milk are highest during the first few weeks of breast feeding and then decrease over ti me (ATSDR 1998). Equation 3- 38 accounts for the changing concentration in breast milk fat, but estimates one average value to represent the concentration over the entire duration of breast feeding. The model is dependent on the maternal body burden of the chemical and assumes that the chemical concentration in breast milk fat is the same as the concentration in general maternal body fat. According to reviewers of the model, this assumption warrants further investigation because milk fat appears to be synthesized in the mammary glands and may have lower chemical concentrations than general body fat stores ( EPA 2001 a).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 34 

### Equation 3- 38

. Chemical Concentration in Breast Milk Fat

where:

C milkfat = Concentration of chemical in lipid phase o f maternal milk ( mg chemical /kg

lipid)

DAI mat = Daily absorbed maternal chemical dose ( mg chemical /kg maternal body weight

- day ; calculated using Equation 3

- 39 )

f f = Fraction of total maternal body burden of chemical that is stored in maternal fat (mg che mical in body fat / mg total chemical in whole body; value from literature or EPA default

- see Section 6.5 )

k elim = Chemical

- specific total elimination rate constant for elimination of the chemical

by non

- lactating women (per day; e.g., via u rine, bile t o feces, exhalation; value from literature or calculated using Equation 3

- 4 0 )

f fm = Fraction of maternal body weight that is fat stores ( unitless)

k fat_elac = Chemical

- specific r ate constant for total elimination of chemical in the lipid

phase of milk du ring nursing (per day; value from literature or calculated using Equation 3

- 41 )

t bf = Duration of breast feeding (days)

t pn = Duration of mother’s exposure prior to parturition and initiation of breast feeding (days)



### Equation 3- 38 relies on the daily maternal absorbed intake ( DAI mat 

### ) to determine the concentration of the chemical in the breast milk fat. DAI mat 

### is multiplied by the fraction of the chemical that is stored in maternal fat ( f f 

### ) to determine the amount (i.e., mass) of chemical in the fat. This product, divided by the chemical-specific elimination rate constant ( k elim 

### ) for nonlactating adult women and the fraction of the mother’s weight that is fat ( f fm 

### ), represents the maximum theoretical steady-state concentration of the chemical in an adult woman. If used alone to estimate the chemical concentration in breast milk fat, the equation as explained thus far is likely to overestimate the chemical concentration in milk fat because it does not account for losses due to breast feeding. Alone, this term ( DAI mat 

### f f 

### / k elim 

### f fm 

### ) also assumes that the biological half- life of the chemical in the mother’s breast milk fat is small relative to the duration of the mother’s exposure . However, for chemicals with half-lives that are longer than the exposure duration, which are the chemicals of concern in the applications of MIRC to date, an additional term is needed to determine the average concentration in the milk fat over the duration of her exposure.

To account for breast feeding losses and longer chemical half-lives in the mother than the exposure duration, an additional term is included in Equation 3- 38 . This term includes a fraction dependent on two rate constants, k elim 

### and the elimination constant for a lipophilic chemical in lactating women vi a the lipid phase of breast milk ( k fat



### _ elac 

### ), the duration of the mother’s chemical exposure prior to nursing ( t pn 

### ), and the duration of breast feeding ( t bf 

### ). The whole body concentration ( DAI mat 

### f f 

### / k elim 

### f fm 

### ), the maximum theoretical steady-state concentration, is multiplied by the rate of elimination averaged over the duration of the mother’s exposure, including her exposure prior to and during lactation. To review the derivation of Equation 3- 38

, see Appendix B of MPE ( EPA 1998).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 35 

### To estimate an average daily dose absorbed by an infant’s mother, or DAI mat 

### , the average daily dose ( ADD ) (in mg/kg-day) for the chemical from all sources that MIRC calculates for adults ( ADD (adult) 

### , described in Section 3.3, Equation 3- 35 ), is multiplied by an absorption efficiency ( AE mat 

### ) or fraction of the chemical absorbed by the oral route of exposure, as shown in Equation 3- 39 . The value for AE mat 

### can be estimated from absorption efficiencies for adults in general. Available data for some chemicals, in particular some inorganic compounds, indicate AE values for ingestion exposures of substantially less than 100 percent. For a few of these chemicals, data also indicate lower AEs for the chemical when ingested in food or in soil than when ingested in water (e.g., cadmium). For a screening level assessment, however, it is reasonable to either assume 100 percent for the AE mat 

### or to use the higher AE mat 

### of the food and water AE mat 

### values if available; hence, a single AE mat 

### parameter is included in Equation 3- 39

. Equation 3- 39

. Daily Maternal Absorbed Intake

where:

DAI mat = Daily maternal dose of chemical absorbed from medium i (mg/kg

- day)

ADD (adult) 

### = Average daily dose to the mother (mg/kg

- day) ( ca lculated by MIRC

– see

Section 3.3 , Equation 3

- 3 5 )

AE mat 

### = Absorption efficiency of the chemical by the oral route of exposure (i.e.,

c hemical

- specific fraction of ingested chemical that is absorbed ) by the mother (unitless) ( value from literature o r EPA default

– see Section 6.4)



### Equation 3- 35 , used to calculate ADD (adult), 

### is based on many medium-specific ingestion rates that are normalized to body weight. The adult body weights to which the homegrown food ingestion rates are normalized are the body weights of the consumers in the original USDA survey (see Section 6.3.3), which included both males and females. An assumption in the breast-milk exposure pathway is that those ingestion rates also are applicable to nursing mothers. The original data for ingestion rates for soil, drinking water, and fish are on a per person basis for males and females combined. MIRC divides those chemical intakes by an adult body weight for males and females combined as specified by the user (e.g., 71.4 kg mean value) to estimate the ADD normalized to body weight from those sources. If the user finds that those exposure media contribute the majority of the chemical intake for the risk scenario under consideration, the user may use alternative ingestion rates for those media and alternative body weights for nursing women, as described in Section 6.5.

Elimination rates for chemicals often are reported as the half-life of the chemical in the body following a known dose of chemical. Many chemicals exhibit a two-phase elimination process, the first being more rapid than the second. For screening risks for persistent and bioaccumulative chemicals, the half-life of the slower phase of elimination, presumably from

non -blood compartments of the body, is the more important of the two

. Assuming first-order kinetics, Equation 3- 40 is used to convert a measured half-life for elimination of a chemical for adults or non-lactating women to an elimination rate constant ( EPA 1998) . The equation can be used to estimate any kind of chemical loss rate constant from a measured chemical half-life.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 36 

### Equation 3- 40

. Biological Elimination Rate Constant for Chemicals for Non-lactating Women

where:

k eli m = Chemical

- specific elimination rate constant for elimination o f the chemical for

non

- lactating women (per day; e.g., via urine, bile to feces, exhalation)

ln2 = Natural log of 2 (unitless constant )

h = Chemical

- specific biological half

- life of chemica l for non

- lactating women (days)



### For chemicals transferred from the body of lactating women to breast milk, the rate of chemical elimination is augmented by the rate of chemical loss via the milk. The total elimination rate for lactating women sometimes is measured directly and reported in the literature. Where directmeasurements are not available, and for chemicals that partition predominantly to the lipidphase of milk, EPA has used Equation 3- 41 to estimate the total chemical elimination rate for lactating women, k fat



### _ elac 

### ( EPA 1998 ).

Equation 3- 41

. Biological Elimination Constant for Lipophilic Chemicals for Lactating Women

where:

k fat_elac = R ate constant for total elimin ation of chemical during nursing (per day) ;

accounts for both elimination by adults in general and the additional chemical elimination via the lipid phase of milk in nursing women

k elim = E limination rate constant for chemical from adults, including non

- lactating

women (per day; e.g., via urine, bile to feces, exhalation ; chemical

- specific ; value from literature or calculated from half

- life usi ng Equation 3

- 40 )

IR milk = Infant milk ingestion rate over the duration of nursing ( kg/d )

f f = Fraction of tot al maternal body burden of chemical that is stored in maternal fat (mg chemical in body fat / mg chemical total in body ; value from literature or EPA default)

f mbm = Fraction of fat in breast milk (unitless)

f fm = Fraction of maternal body weight that is fat stores ( unitless)

BW mat = Maternal body weight over the entire duration of the mother’s exposure to the chemical including during pregnancy and lactation (kg)



### Equation 3- 41 is based on a model from Smith (1987) and accounts for the additional elimination pathway for lipophilic chemicals via the breast milk fat

. The term K fat



### _ elac 

### is estimated by adding an estimate of the first-order elimination constant for breast feeding losses to k elim 

### , which is the chemical-specific total elimination rate constant for non-lactating women. The breast feeding losses are estimated from the infant’s intake rate of breast milk ( IR milk 

### ), the fraction of the total maternal body burden of the chemical that is stored in maternal body fat ( f f 

### ),Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 37 

### the fraction of the mothe r’s breast milk that consists of fat (lipids) ( f mbm 

### ), the mother’s body weight ( BW

mat 

### ), and the fraction of the mother’s weight that is body fat ( f fm 

### )

. In Equation 3- 41

, the value for the mother’s body weight should be specific to women of child -bearing age, as opposed to a body weight value for both males and females that is used to estimate an adult average daily dose and the mother’s absorbe d daily intake in Equation 3- 39 . Body weight values for the mother are described in Section 6.5. Smith’s (1987) model assumes that the chemical partitions to the lipid-phase of breast milk to the same degree that it partitions into the mother’s body fat . For highly lipophilic compounds, losses from breast feeding can be larger than losses by all other pathways ( EPA 1998).

3.4.3 Chemical Concentration in Aqueous Phase of Breast Milk When developing MPE ( EPA 1998), EPA also considered models to estimate chemical concentrations in the aqueous phase of breast milk (C aqueous 

### )

. EPA adapted Smith’s (1987) steady state concentration model for estimating C milkfat 

### and developed the C aqueous 

### model shown in Equation 3- 42 ( EPA

1998). Chemicals that would partition to the aqueous phase of human milk include water-soluble chemicals, such as salts of metals, and other hydrophilic chemicals that may be in equilibrium with bound forms of the chemical in different tissues. The C aqueous 

### equation assumes that the chemical concentration in the aqueous phase of milk is directly proportional to the chemical concentration in the mother’s blood p lasma. The portion of chemical sequestered in red blood cells (e.g., bound to RBC proteins) is assumed to be unavailable for direct transfer to breast milk.

Equation 3- 42

. Chemical Concentration in Aqueous Phase of Breast Milk

where:

C aqueous = Concentration of chemical in aqueous phase of maternal milk ( mg/kg )

DAI mat = Daily absorbed maternal chemical dose (mg /kg

- day ; calculated by Equation 3

- 39 )

f pl = Fraction of chemical in t he body (based on absorbed intake) that is in the blood plasma compartment (unitless ; value from literature or calculated by Equation 3

- 43 )

Pc bm = Partition coefficient for chemical between the plasma and breast milk in the aqueous phase (unitless); assum ed to equal 1.0

k aq _elac = Chemical

- specific rate constant for total elimination of chemical in the aqueous

phase of milk during nursing (per day ; value from literature or calculated in Equation 3

- 44 )

f pm = Fraction of maternal weight that is blood plas ma (unitless)



### Equation 3-42 is a steady-state concentration model that, like the Equation 3-38 for C milkfat 

### , is dependent on the maternal absorbed daily intake ( DAI mat 

### )

. In Equation 3-42

, DAI mat 

### is multiplied by the fraction of the absorbed chemical that is circulating in the blood plasma compartment ( f pl 

### ) and a partitioning coefficient for the chemical between plasma and the aqueous phase of breast milk ( Pc

bm 

### )

. For highly water-soluble chemicals that are not transported via special carrier molecules, t he chemical is assumed to diffuse passively from the mother’s blood serum to the aqueous phase of her milk, in which case Pc bm 

### would equal 1.0. The denominator includes the biological elimination constant for the chemical in the aqueous phase of breast milk in lactatingAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 38 

### women ( k

aq_elac 

### ) and the fraction of the mother’s weight that is plasma ( f pl 

### )

. Because the model assumes steady-state, it does not account for chemical species with long half-lives in the body or for body burden losses due to lactation. These factors are important for highly lipophilic chemicals and for non-lipophilic chemicals such as methyl mercury, lead, and cadmium that partition into body compartments such as red blood cells and bone. While these latter chemicals or forms of these chemicals are water-soluble when free, they have relatively long half-lives because they are in equilibrium with the chemical bound to macromolecules in some tissue compartments. Lead is of particular concern because it can be released from the bone into the blood during lactation, and thus into the breast milk ( EPA 2001 a). Due to this limitation, the model may over- or underestimate exposure to the infant.

Because Equation 3-42 is based on the relationship between the chemical concentrations in the aqueous phase of breast milk and the blood plasma, a value for the fraction of the chemical in the mother’s blood plasma ( f pl 

### ) is required. Ideally, an empirical value for f pl 

### should be used. If empirical values are not available, f pl 

### can be estimated from Equation 3-43, provided that an empirical value can be found for the fraction of the chemical in the body that is in the mother’s whole blood compartment ( f bl 

### ; EPA 1998).

Equation 3- 43

. Fraction of Total Chemical in Body in the Blood Plasma Compartment

where:

f pl = Fraction of chemical in body (based on absorbed intake) that is in the blood plasma compartment (unitless) ; chemical

- specific

f bl = Fraction of chemical in body (based on a bsorbed intake) in the whole blood compartment (unitless) ; chemical

- specific

f bp = Fraction of whole blood that is plasma (unitless)

Pc RBC = Partition coefficient for chemical between red blood cells and plasma

(unitless); chemical

- specific



### If the fraction of the total chemical in the body that is in the whole blood compartment ( f bl 

### ) is known for a given chemical, then the fraction of that chemical that is in blood plasma depends only on the partition coefficient for the chemical between the red blood cells and the plasma ( Pc RBC 

### ) and the fraction of whole blood that is plasma ( f bp 

### ).

Another parameter for which a value is needed to solve Equation 3- 42 is the total chemical elimination rate for lactating women for hydrophilic chemicals, k aq_elac



### . As for k fat_elac 

### for lipophilic chemicals, k

aq_elac 

### for hydrophilic chemicals would be equal to k elim 

### plus the loss rate for the chemical in the aqueous phase of breast-milk during lactation. In the case of hydrophilic chemicals, EPA has yet to propose a term for the additional elimination of a chemical in the aqueous phase of milk from breast feeding. Given basic physiological mechanisms, we assume that chemical loss rates via urine are likely to be significantly higher than loss rates from nursing, however

. Th is is because the counter-current anatomy of kidney tubules allows substantial concentration of chemicals in the tubules for elimination in urine compared with the concentration in circulating blood and because of active secretion of some chemicals into urine. Therefore, the best estimation of elimination of hydrophilic chemicals by lactating women is simply k

elim 

### , the elimination of the chemical from a non-lactating woman, as shown in EquationAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 39 

### 3-40. The extent to which k elim 

### is an underestimate of k aq_el ac 

### for a given chemical will determine the extent of conservative bias in k aq_elac



### . Equation 3- 44

. Biological Elimination Rate Constant for Hydrophilic Chemicals

where:

k aq

_ elac = Chemical

- specific r ate constant for total elimination of chemical by lactating

women for hydrophilic chemicals (per day)

k elim = Chemical

- specific rate constant fo r total elimination of chemical by non

lactating women (per day; e.g., via u rine, bile to feces, exhalation; value from literature or calculated from half

- life using Equation 3

- 40 )



### 3.4.4 Alternative Model for Infant Intake of Methyl Mercury

In this version of MIRC, we were unable to fully parameterize the aqueous model for mercury

. In particular, no empirical value could be found for the steady-state fraction of total hydrophilic chemical body burden in the mother that is in the blood plasma (f pl 

### , see Exhibit 6- 21 ). This parameter could be estimated using Equation 3-43 if a suitable chemical-specific fraction of chemical in the body that is in the whole blood (f bl 

### ) could be found. However, the value found for f bl 

### is based on a single-dose study and is not considered reliable for use in chronic exposure calculations.

W e therefore conducted a literature search to identify existing physiologically based toxicokinetic (P BTK) models of lactational transfer o f methylmercury (MeHg) in humans. Most PBTK models that we identified focused on gestational transfer of mercury between mo ther and fetus, including a PBTK dynamic compartmental model for gestational transfer of MeHg in humans developed by Gearhart et al

. (1995, 1996), and reparameterized by Clewell et al

. ( 1999)

. We did find, however, that Byckowski and Lipscomb (2001) had added a lactational transfer module to the Clewell et al

. (1999) model. Byckowski and Lipscomb compared their model’s predictions to epidemiological data from mother-nursing-infant pairs obtained following an accidental high-dose poisoning in Iraq (Amin-Zaki et al

. 1976 ) and from 34 mother-nursinginfant pairs examined in a low-dose, chronic exposure environment (Fujita and Takabatake 1977 ). Using data from the Iraq incident, Byckowski and Lipscomb (2001) found good agreement between their model’s predict ions and the clinical data relating MeHg concentrations in breast milk to MeHg concentrations in infant’s blood with time following the poisoning. To compare their model’s predictions to data from chronic exposure to low doses of MeHg, Byckowski and Lipscomb (2001) simulated MeHg intake for 500 days prior to conception, continued through gestation, and 6.5 months (200 days) of lactation. Their model’s predictions were consistent with Fujita and Takabatake ’s (1977) study, although use of hair/blood partiti on coefficients based on the results of the 1977 study precluded use of this comparison as model validation

. Both the model predictions and the mean values from the 1977 data indicated that the concentration of MeHg in the blood of nursing infants was close to the MeHg concentration in their mothers’ blood (approximately 0.0 25 to 0.027 mg/L, Figure 4 of report). At those blood concentrations, the PBTK model estimated the average maternal intake of MeHg to be 0.68 ± 0.33 (SD) μg /kg-day and the average infant intake of MeHg to be 0.80 ± 0.38 μg/kg

- day

. Therefore, for purposes of MIRC, the DAI inf 

### of MeHg is estimated to be the same as the maternal intake per unit body weight (Equation 3- 42 ).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 40 

### Equation 3- 45

. Calculation of Infant Average Daily Absorbed Dose of Methyl Mercury

where:

DAI

inf_MeHg = Average daily dose of MeHg absorbed by infant from breast milk (mg/kg

- day)

DAI mat_MeHg = Average daily dose of methyl mercury absorbed by th e mother, predominantly

from fish (mg/kg

- day )Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 41 

## 4 Dose-Response Values Used for Assessment

Chemical dose-response values included in MIRC include carcinogenic potency slope factors for ingestion and non-cancer oral reference doses (RfDs) for chronic exposur es . The cancer slope factors (CSFs) and RfDs for chemicals used to calculate PB-HAP emission thresholds are provided in Exhibit 4-3

. Dose-response values in MIRC that are used for EPA’s Risk and Technology Review (RTR) evaluations are consistent with dose-response data that the Agency’s Office of Air Quality Planning and Standards ( OAQPS) uses for risk assessments of hazardous air pollutants (HAPs) ( EPA 2007) . In general, OAQPS chose these values based on the following hierarchy of sources: EPA’s Integrated Risk Information System (IRIS); the Centers for Disease Control’s Agency for Toxic Substances and Disease Registry (ATSDR); and the California Environmental Protection Agency (CalEPA)

.

Exhibit 4

- 1 . Oral Dose

- response Values for PB

- HAP Chemicals Used to Calculate RTR Screening Threshold Emission Rates

Chemical CAS No. C ancer S lope F actor R e f erence D ose

Source Source

Inorgani cs Cadmium compounds in food 7440439 not available 1.0E

- 03 IRIS Mercury (elemental) 7439976 NA not available

Mercuric chloride 7487947 not available 3.0E

- 04 IRIS Methyl mercury (MeHg) 22967926 not available 1.0E

- 04 IRIS Organics Benzo(a)pyrene 50328 1.0E+01 EPA OAQPS a not available 2,3,7,8

- TCDD 1746016 1.5E+05 EPA ORD 1.0E

- 09 ATSDR ATSDR = Agency for Toxic Substances and Disease Registry IRIS = Integrated Risk Information System EPA OAQPS = EPA’s Office of Air Quality Planning and Standards NA = not applicable EPA ORD = EPA’s Office of Research and Development

a The method to assign oral cancer slope factors for polycyclic organic matter (POM) is the same as was used in the 1999 National Air Toxics Assessment (EPA 1999b). A complete description of the methodology is available at: http://www.epa.gov/ttn/atw/nata1999/99pdfs/pomapproachjan.pdf

.



### Cadmium EPA has developed two chronic RfDs for cadmium (Cd), one for food and one for water, based on data in IRIS indicating a lower absorption efficiency of cadmium from food than from water. The default RfD set in MIRC is the higher RfD for Cd compounds in food (no drinking of water is assumed to occur when calculating screening thresholds). Users of MIRC who assess exposures via drinking water may need to use the RfD for Cd compounds in water (i.e., 5.0E- 4 mg/kg-day).

Mercury EPA’s RfD for MeHg of 1E -04 mg/kg-day is based on a Benchmark Dose Lower Limit (BMDL) to dose-response data from an epidemiological study of neurobehavioral effects in children for which mercury concentrations had been measured in cord blood at birth. The island populations included in the study had been exposed for many years to MeHg in their seafood

. The RfD applies to the pregnant mother as well as young children. EPA has not specified theAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 42 

### minimum exposure duration at the RfD level of exposure that is appropriate to use in characterizing risk; we assume ten years for women of child-bearing age and 1 year for infants.

We note that human exposures to MeHg are primarily through the consumption of fish and shellfish (EPA 2001b). EPA found that on average, approximately 76 percent of the exposure to MeHg for women of childbearing age could be attributed to ingestion of mercury in freshwater and estuarine fish and shellfish, with the remaining 24 percent derived from marine fish and shellfish. Other sources accounted for less than 0.06 percent of total exposures (EPA 2001b).

Dioxins (2,3,7,8-TCDD)
For chemicals for which the critical health effect is developmental, either in utero and/or during the first months or years of life, the exposure duration and timing of exposure for comparison with the RfD (or comparable value) require special consideration. The most sensitive health endpoints for both mercury and 2,3,7,8-TCDD are neurological effects during development that have long-lasting effects on learning and social behaviors. To ensure a protective risk characterization for these chemicals, it is important to use the shortest exposure duration appropriate, at the appropriate life stage, for comparison with the toxicity reference values. This approach avoids “dilution” of an estimated average ADD that would result from averaging the lower daily chemical intake rates normalized to body weight for older children and adults with the potentially higher daily intake rates of infants over a longer exposure averaging period.

For 2,3,7,8-TCDD, although exposures may start in utero, a period of special concern is the nursing stage, because the highly lipophilic chemical is effectively transferred to the infant in the lipid phase of its mother’s milk. ATSDR has established a minimal risk level (MRL) of 1E-09 mg/kg-day for exposures of the mother or infant of 365 days or longer to 2,3,7,8-TCDD. The MRL is based on a behavioral study of offspring of female rhesus macaques that were exposed prior to conception, during gestation, and while nursing (ATSDR 1998). In the critical study, all mothers were exposed for seven months prior to opportunities for mating; however, dates of conception ranged over a five month period (some females did not conceive for several cycles). When the offspring were born, their mothers had been exposed for an average of 16.2 months. Ex posure continued for the 4-month lactation period, after which the offspring were weaned and tested for non-social and social behavioral deficits (ATSDR 1998, Bowman et al . 1989, Schantz and Bowman 1989, Schantz et al

. 1992). It is not known whether the behavior deficits result ed from pre- or post-natal exposures or both. In this case, it is appropriate to compare the 365-day MRL to the ADD for women of child-bearing age and to the ADD for a nursing infant less than 1 year of age during risk characterization (see Section 5).

The convention for assessing risk from mixtures of dioxins is by application of a toxic equivalency factor (TEF) to dioxin concentrations, which are then expressed as toxic equivalents (TEQs). Of the dioxin congeners, 2,3,7,8-TCDD is the most widely studied, and considered to be one of the two most toxic congeners. It is therefore assigned a TEF of one, with the other dioxin congener TEQ concentrations scaled relative to 2,3,7,8-TCDD concentrations on the basis of toxicity. The World Health Organization (WHO) 2005 TEFs presented in Exhibit 4-2 are used for risk assessment of dioxins for RTR.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 43 

### Exhibit 4

- 2

. WHO 2005 Toxic Equivalency Factors (TEFs) for Dioxins

D ioxin Congener CAS No. WHO 2005 Toxic Equivalency Factor

1,2,3,4,6,7,8

- Heptachlorodibenzofuran 67562 3 9 4 0.01 1,2,3,4,7,8,9

- Heptachlorodibenzofuran 5567389 7 0.01 1,2,3,4,7,8

- Hexachlorod

- benzofuran 70648269 0.1 1,2,3,6,7,8

- Hexachlorodibenzofuran 571174 49 0.1 1,2,3,7,8,9

- Hexachlorodibenzofuran 72918219 0.1 2,3,4,6,7,8

- Hexachlorodibenzofuran 60851345 0.1 1,2,3,4,7,8

- Hexachlorodibenzo

- p

- dioxin 39227286 0.1 1,2,3,6,7,8

- Hexachlorodibenzo

- p

- dioxin 57653857 0.1 1,2,3,7,8,9

- Hexachlorodibenzo

- p

- dioxin 19408 743 0.1 1,2,3,4,6,7,8

- Heptachlorodibenzo

- p

- dioxin 35822469 0.01 1,2,3,4,6,7,8,9

- Octachlorodibenzofuran 39001020 0.0003 1,2,3,4,6,7,8,9

- Octachlorodibenzo

- p

- dioxin 3268879 0.0003 1,2,3,7,8

- Pentachlorodibenzofuran 57117416 0.03 2,3,4,7,8

- Pentachlorodiben zofuran 57117314 0.3 1,2,3,7,8

- Pentachlorodibenzo

- p

- dioxin 40321764 1 2,3,7,8

- Tetrachlorodibenzofuran 51207319 0.1 2,3,7,8

- Tetrachlorodibenzo

- p

- dioxin 1746016 1 Source: van den Berg et al . 2006



### Polycyclic Organic Matter Previously, for risk assessment of inhalation exposures to polycyclic organic matter (POM) for EPA’s National Air Toxics Assessments (NATA) and for RTR, OAQPS developed an approach for characterizing risks associated with the individual POM species and POM groups reported in NEI. I ndi vidual PAHs were assigned to one of eight POM groups according to cancer potencies derived by EPA for IRIS and by CalEPA, and based on assumptions regarding relative carcinogenicity. OAQPS then estimated an inhalation CSF for each group. The same approac h was used to derive oral CSFs for POMs for use in multipathway risk assessment for RTR. POM groups (with their member POM species reported in NEI) and the corresponding CSFs used for RTR risk assessment are presented in Exhibit 4-3 . As noted in the main TSD, a screening threshold for non-inhalation risk was derived only for benzo[a]pyrene, and facility emissionswere then screened by comparing the total POM emissions to this threshold (where a toxicityweighted sum of POM emissions is calculated for each evaluated source).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 44 

### Exhibit 4

- 3 . Oral Dose

- response Values for Polycyclic Organic Matter (POM) Groups

Individual POM or POM group CAS No. C ancer S lope F actor 1

POM Group 71002 Benz(a)Anthracene/Chrysene (7PAH) 103

0.5 T otal PAH 234 Polycyclic Organic Matter 246
16

- PAH 40
16PAH

- 7PAH 75040 POM Group 72002

Anthracene 120127

0.5 Pyrene 129000

Benzo (g,h,i) perylene 191242

Benzo ( e ) pyrene 192972 Benzo(c)phenanthrene 195197 Perylene 198550 Benzo(g,h,i)Fluoranthene 203123 Benzo(a)fluoranthene 203338

Fluoranthene 206440 Acenaphthylene 208968

1

- Methylpyrene 2381217

12

- Methylbenz(a)Anthracene 2422794 Methylbenzopyrenes 247 Methylchry sene 248 Methylanthracene 26914181
Benzofluoranthenes 56832736
9

- Methylbenz(a)Anthracene 779022

1

- Methylphenanthrene 832699 Acenaphthene 83329

Phenanthrene 85018

Fluorene 86737

2

- Methylnaphthalene 91576

2

- Chloronaphthalene 91587

POM Gro up 73002 7,12

- Dimethylbenz ( a ) anthracene 57976 1000 POM Group 74002

Dibenzo ( a,i ) pyrene 189559 100 D[a,h]pyrene 189640Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 45 

### Exhibit 4

- 3 , continued. Oral Dose

- response Values for Polycyclic Organic Matter (POM) Groups

Individual PAH or PAH group CAS No. C ancer S lope F actor a

POM Group 75002

3

- Methylcholanthrene 56495

10 D[a,e]pyrene 192654

5

- Methylchrysene 3697243
Benzo ( a ) pyrene 50328

Dibenzo ( a,h ) anthracene 53703 POM Group 76002

Benzo ( b+k ) fluoranthene 102

1 Indeno ( 1,2 ,3

- c,d ) pyrene 193395

B ( j ) fluoranthen 205823

Benzo ( b ) fluoranthene 205992

Benzo ( k ) fluoranthene 207089

D ( a,j ) acridine 224420

Benz ( a ) anthracene 56553 POM Group 77002 Chrysene 218019 0.1 POM Group 77002

7

- PAH 75 0.5

a The method to assign oral c ancer slope factors for polycyclic organic matter (POM) is the same as was used in the 1999 National Air Toxics Assessment (EPA 1999b). A complete description of the methodology is available at: http://www.epa.gov/ttn/atw/nata1999/99pdfs/pomapproachjan.pdf

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 46 

## 5 Risk Estimation

For persistent and bioaccumulative hazardous air pollutants (BP-HAPs), risks from inhalation of a chemical directly from air generally will be negligible compared with risks from ingestion of the chemical with foodstuffs grown in an area subject to air deposition of the chemical. For other (non- PB ) HAPs, inhalation risks can be estimated separately and compared with risks associated with ingestion exposure to determine the focus of subsequent tiers of the risk assessment. Risk characterization for carcinogens with a linear mode of action at low doses is described in Section 5.1. Risk characterization for chemicals likely to exhibit a threshold for response (e.g., non-cancer hazards) is described in Section 5.2.



### 5.1 Cancer Risks
The estimated risk of developing cancer from exposure to a chemical from a specified source is characterized as the excess lifetime cancer risk (ELCR). The ELCR represents the incremental probability of an individual developing cancer over a lifetime as a result of lifetime exposure to the chemical. For a known or suspected carcinogen with a low-dose linear mode of action, the estimated ELCR is calculated as the product of the lifetime average daily dose (LADD) and the cancer slope factor ( SF ):

Equation 5-1

. Calculation of Excess Lifetime Cancer Risk

ELCR = LADD C SF where :

ELCR = Estimated excess lifetime cancer risk from a chemica l summed across all exposure pathways and media (unitless)

LADD = Lifetime average total daily dose from all exposure pathways and media

(mg/kg

- day)

C SF = Oral carcinogenic potency slope factor for chemical (per mg/kg

- day)



### As described in Section 3.3

, the LADD(in mg/kg-day) for a chemical is calculated to reflect agerelated differences in exposure rates that are experienced by a hypothetical individual throughout his or her lifetime of exposure. Th e tot al chemical intake is normalized to a lifetime, which for the purposes of this assessment is assumed to be 70 years.

EPA considers the possibility that children might be more sensitive than adults to toxic chemicals, including chemical carcinogens ( EPA 2005b,c). Where data allow, EPA recommends development of lifestage-specific cancer potency CSFs. To date, EPA has developed a separate slope factor for early lifestage exposure for only one chemical (i.e., 1,1,1- trichloroethane ; EPA

2007b ), and current data availability for most chemicals preclude this approach. EPA has, therefore, examined options for default adjustments of the CSF to protect children. To date, the only mode of action (MOA) for carcinogenesis for which EPA has adequate data to develop a reasonable quantitative default approach is mutagenesis ( EPA 2005b, c ). For carcinogens with a mutagenic MOA for cancer, EPA concluded that the carcinogenic potency of a chemical may be approximately tenfold greater for the first 2 years of life (i.e., birth up to second birthday) and threefold greater for the next 14 years of life (i.e., ages 2 through 15) than for adults ( EPA2005c). These conclusions are represented by agedependent adjustment factors (ADAFs) of 10, 3, and 1 for the first two lifestages and for adults, respectively

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 47 

### These three lifestages do not match the age categories for the home-grown food ingestion rates, the age categories in MIRC

. As a consequence, ADAFs for the age groups in MIRC are adapted as time-weighted average values as follows:

To estimate total lifetime risk from a lifetime of exposure to such a chemical, EPA recommends estimating the cancer risk for each of the three lifestages separately and then adding the risks for i = 1 to 6 age groups.

Equations 5-2 to 5-8

. Lifetime Cancer Risk: Chemicals with a Mutagenic MOA for Cancer

Equation 5-2. Risk (<1) 

### = ADD (0

- <1 ) 

### x 10 x C SF x (1 yr

/70 yr)

Equation 5-3



### . Risk (1

- 2) 

### = ADD (1 -2) 

### x 6.5 x C SF x (2 yr/70 yr)

Equation 5-4. Risk (3 -5) 

### = AD D (3-5) 

### x 3 x C SF x (3 yr/70 yr)

Equation 5-5. Risk (6 -1 1) 

### = ADD (6- 11 ) 

### x 3 x C SF x (6 yr/70 yr)

Equation 5-6. Risk (12- 19 ) 

### = AD D (12- 19 ) 

### x 2 x

C SF x (8 yr/70 yr)

Equation 5-7. Risk (adult) 

### = AD D (adult) 

### x 1 x C SF x ( 50 yr/70 yr)

Equation 5-8. ELCR

In other words, Equation 5-8 indicates that the total extra lifetime cancer risk (ELCR) equals the sum of the age-group-specific risks estimated by Equations 5-2 through 5-7, where:

Risk (<1) = R isk from chemical ingestion in first year of life Risk (1

- 2) = Risk from chemical ingestion from first birthday through age 2 years Risk (3

- 5) = Ri sk from chemical ingestion from age 3 through 5 years of age Risk (6

- 11) = Risk from chemical ingestion from age 6 through 11 years of age Risk (12

- 19) = Risk from chemical ingestion from age 12 through 19 years of age Risk (adult) = Risk from chemical ingestion from age 20 to 70 years age
ADD (< 1) = Average daily dose for infants under one year of age (mg/kg

- day) ADD (1

-

2 ) = Average daily dose from first birthday through age 2 years of age (mg/kg

- day) ADD (3

- 5) = Average daily dose from age 3 through 5 years of age (mg/kg

- day) ADD (6

- 11) = Average daily dose from age 6 through 11 years of age (mg/kg

- day) ADD (12

- 19) = Average daily dose from age 12 through 19 years of age (mg/kg

- day)
ADD (adult) = Average daily dose for adults age 20 to 70 years of age (mg/kg

- day)

C SF = O ral carcinogenic potency sl ope factor for chemical (per mg/kg

- day)

Risk (i) = R isk f rom chemical ingestion for the i th age group

ELCR = T otal extra lifetime cancer risk (incremental or extra risk)

n = Number of age groups (i.e., 6)Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 48 

### 5.2 Non-cancer Hazard Quotients

Non-cancer risks ar e presented as hazard quotients (HQs), that is, the ratio of the estimated daily intake (i.e., ADD) to the reference dose (e.g., chronic RfD). If the HQ for a chemical is equal to or less than 1, EPA believes that there is no appreciable risk that non-cancer health effects will occur. If the HQ is greater than 1, however, EPA cautions that adverse health effects are possible, although an HQ above 1 does not indicate an effect will definitely occur. This is because of the margin of safety inherent in the derivation of all RfD values

. The larger the HQ value, the more likely it is that an adverse effect may occur.

5.2.1 Hazard Quotients for Chemicals with a Chronic RfD For chemicals with a chronic RfD, MIRC calculates an HQ for each age group separately using Eq uation 5-9 to indicate the potential for adverse health effects associated with chronic exposure via ingestion pathways

. T he HQ is the ratio of a long-term, daily average exposure normalized to the receptor's body weight (i.e., ADD) to the RfD for that chemical.

Equation 5-9

. Hazard Quotient for Chemicals with a Chronic RfD

where:

HQ = Hazard quotient for chemical (unitless)

ADD = Average daily ingested dose of chemical (mg/kg

- day) from all food types and

ingested media for the age group

RfD = Chronic oral reference dose for chemical (mg/kg

- day)



### 5.2.2 Hazard Quotients for Chemicals with RfD Based on Developmental Effects For chemicals for which the toxicity reference value is an RfD based on developmental effects in infants, children, or young animals, a shorter exposure duration ( ED ) and averaging time ( AT ) may be requir ed . For this type of chemical (e.g., methylmercury, 2,3,7,8-TCDD), the appropriate ED/AT and sensitive lifestage for exposure may need to be estimated from the information provided in the critical developmental study(ies) from which the RfD was derived (e.g., in consultation with the RfD documentation in EPA’s IRIS or in a toxicological profile developed for the chemica l) . For screening-level risk assessments, however, a conservative approach is to compare the highest ADD from among the child age categories provided in MIRC to the RfD.

5.2.3 Hazard Index for Chemicals with RfDs When conducting screening-level assessments for multiple chemicals, it can be informative to calculate a hazard index (HI) for toxicologically similar chemicals ( EPA 2000). The HI is the sum of HQs across chemicals as shown in Equation 5- 12 . As with the HQ, if the HI value is less than 1, adverse health effects are not expected for that suite of chemicals. If the screening level HI exceeds 1, however, the risk assessor is advised to evaluate the assumptions of the screening-level assessment to determine if more realistic local values are available for parameters that drive risk. In addition, the risk assessor may need to examine the mode of action (MOA) and target organ(s) for the chemicals with the highest HQs to develop an appropriate approach to assessing their potential joint action.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 49 

### Equation 5- 10

. Hazard Index Calculation

HI = HQ 1 

### + HQ 2 

### ... HQ n 

### where:

HI = Hazard index (unitless)

HQ 1 = Hazard Quotient for chemical 1 (unitless)

HQ 2 = Hazard Quotient for chemical 2 (unitless)

HQ n = Hazard Qu otient for chemical n (unitless)



### The HI approach can be appropriate for chemicals with the same MOA and same target organ ; however, MOA often is difficult to determine. An HI usually is “developed for each exposure route of interest, and for a single to xic effect or for toxicity to a single target organ” ( EPA 2000; p 79 ). If a receptor is exposed to multiple chemicals that affect different target organs or that operate by different MOAs, and if more than one HQ is close to 1, the risk assessor is advise d to perform a follow-on evaluation of assumptions and to consider whether chemical interactions may play a role in chemical toxicity ( EPA 2000) . Exposures to more than one chemical can result in a greater or lesser toxic response than might be predicted on the basis of one or the other chemical acting alone (toxicologically independent) or acting in concert (toxicologically similar chemicals). Users are referred to EPA’s Supplementary Guidance for Conducting Health Risk Assessment of Chemical Mixtures fo r approaches to assessing the potential for adverse health effects from exposure to multiple chemicals ( EPA 2000).

Note that users of MIRC are responsible for determining how to interpret HQs for multiple chemicals.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 50 

## 6 Model Input Options

This section describes the input options currently included in MIRC

. Required user inputs for environmental media concentrations and air deposition rates, such as those predicted by (output of) TRIM.FaTE, are described in Section 6.1. Values for farm-food-chain (FFC) parameters for specific types of produce and animal products are discussed in Section 6.2.Options for parameterizing receptor characteristics are described in Section 6.3, including agegroup-specific values for body weight, water ingestion, and food ingestion by food type. Options for other exposure parameter values in MIRC, such as exposure frequency and loss of chemical during food preparation and cooking, are provided in Section 6.4

. Where values for chemical-specific parameters are presented, values are presented only for PB -HAP chemicals currently evaluated using the TRIM-based RTR screening scenario. The database included with MIRC contains chemical-specific parameter values for a large number of chemicals, because all of the chemical-specific input data compiled by EPA for use in HHRAP were uploaded into MIRC. However, only chemicals that are PB-HAPs evaluated for RTR are discussed in this document, and the HHRAP inputs provided for other chemicals have not been evaluated. The data presented in this chapter were reviewed and used to develop the set of modeling defaults used to calculate screening threshold emission rates for RTR. Note that the default values used to estimate RTR screening thresholds, and the justification for selecting a specific value from the data sets described in this chapter, are discussed in Chapter 7.



### 6.1 Environmental Concentrations
As noted in Section 2, MIRC is intended to estimate exposures and risks to self-sufficient farming and fishing families from airborne chemicals

. The tool analyzes one exposure scenario at a time; therefore, it is best used to evaluate a maximally exposed individual (MEI) or family when MIRC is used to screen for possible risks.

The following values specific to the air pollutant of concern are required inputs to MIRC:

a single air concentration (in g/m 3 

### ); the fraction of chemical in the air that is in the vapor phase; air- to -surface deposition rates for both vapor- and particle-phase chemical in the air (in g/m 2 

### -yr); two fish tissue concentrations, one each for forage and game fish (i.e., fish in TL 3 and TL 4) (in mg/kg wet weight); concentrations in drinking water (in g/L); and four chemical concentrations in soil (in μg/g dry weight), one each for: 1. surface soil in produce growing area, 2. surface soil where livestock feed, 3. root-zone soil in produce growing area, and 4. root-zone soil in livestock feed growing area.

The MIRC software is configured to estimate ingestion exposures via drinking water for a specified chemical concentration in the drinking water source (e.g., groundwater well)

. The user must provide the inputs listed above; no default values are included for these parameters in MIRC

. Media concentrations output by TRIM.FaTE can be entered into the tool manually from model output files or can be imported. For RTR evaluations, a tool to facilitate this process was developed using a Microsoft Excel routine written in Visual Basic.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 51 

### 6.2 Farm- Food -Chain Parameter Values
Using the chemical information specified in Section 6.1 above as inputs, MIRC calculates chemical concentrations in foods that are commonly grown or raised on family farms: exposed and protected fruits; exposed and protected vegetables; root vegetables; beef; total dairy products; pork; and poultry and eggs

.

6.2.1 List of Farm- Food -Chain (FFC) Parameters MIRC estimates chemical concentrations in the produce identified above using algorithms from HHRAP ( EPA

2005a) as described in Section 3.2. Parameter values required for these HHRAP algorithms, including chemical-specific media transfer factors (e.g., soil- to -plant transfer coefficients) and plant- and animal-specific properties (e.g., plant interception fraction, quantity of forage consumed by cattle), are included in tables in MIRC

. As described in Section 7, the HHRAP -recommended parameter values are the default values in MIRC; however, these and other inputs in MIRC can be edited as needed. Exhibit 6-1 describes the parameters that are included in the algorithms used to estimate chemical concentrations in the farm food categories. The parameter names and symbols are referenced in this section for plants/produce and animal products.

Exh ibit 6

- 1

. MIRC Parameters Used to Estimate Chemical Concentrations in Farm Foods

Parameter Description Units

Plants/Produce

Br AG

- produce

- DW(i) Chemical

- specific plant/soil chemical bioconcentration

facto r for edible portion of aboveground produce type i, exposed or protected Unitless ( g soil DW / g produce DW )

Bv AG (i) Chemical

- specific a ir

- to

- plant biotransfer factor for

aboveground produce type i for vapor

- phase chemical in air U nitless ([mg chemical / g DW plant] / [mg chemical / g air])

Fw Fraction of wet deposition that adheres to plant surfaces;

0.2 for anions, 0.6 for cations and most organics Unitless

Kd s Chemical

- specific s oil/water partition coefficient L soil pore water / kg soil DW

k p (i) Pla nt

- specific surface loss coefficient for aboveground

exposed produce and animal forage and silage yr - 1

MAF (i) Moisture adjustment factor for aboveground produce type i

to convert the chemical concentration estimated for dry

weight produce to the correspon ding chemical concentration for full

- weight fresh produce Percent water

RCF Chemical

- specific r oot concentration factor for tubers and

root produce on a wet

- weight (WW) basis L soil pore water/ kg root WW

Rp (i) Plant

- specific i nterception fraction for t he edible portion of

aboveground exposed produce or animal forage and silage Unitless

Tp (i) Length of plant exposure to deposition per harvest of the

edible portion of aboveground exposed produce or animal forage and silage Year

VG AG (i) Empirical correc tion factor for aboveground exposed

produce type i to address possible overestimate of the diffusive transfer of chemical from the outside to the inside of bulky produce, such as fruit UnitlessAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 52 

### Exhibit 6

- 1, continued. MIRC Parameters Used to Estimate Chemical Concentrations in Farm Foods

Parameter Description Units

VG rootveg Empirical correction factor for belowground produce (i.e.,

tuber or root vegetable) to account for possible overestimate of the diffusive transfer of chemicals f rom the outside to the inside of bulky tubers or roots (based on carrots and potatoes) Unitless

Yp (i) Plant

- specific y ield or standing crop biomass of the edible

portion of produce or animal feed kg produce DW/m 2

Animal Products
Bs Soil bioavailability factor for livestock Unitless

MF Chemical

- specific mammalian metabolism factor that

accounts for endogenous degradation of the chemical Unitless

Ba (b eef

) Chemical

- specific b iotransfer factor for chemical in diet of

cow to chemical in beef on a fresh

- wet (FW; equivalent to WW) basis mg chemical/kg FW tissue/mg chemical/day

or day/kg FW tissue

Ba (d airy ) Biotransfer factor in dairy day/kg FW tissue

Ba (p ork

) Biotransfer factor in pork day/kg FW tissue
Ba (p oultry

) Biotransfer factor in poultry day/kg FW tis sue Ba (e ggs

) Biotransfer factor in eggs day/kg FW tissue
Qs (m) Quantity of soil eaten by animal type m each day kg/day

Qp (i,m) Quantity of plant feed type i consumed per animal type m

each day kg/day

Source: EPA Source: EPA 2005 a DW = dry weight; FW = fresh weight; WW = wet weight



### 6.2.2 Produce Parameter Values
Exhibit 6-2 and Exhibit 6-3 provide the chemical-specific input values that are the current defaults for produce FFC food types in MIRC. Exhibit 6-4 presents additional non -chemicalspecific input values for parameters used in the algorithms that calculate chemical concentrations in produce. Unless otherwise noted, the default parameter values were obtained from HHRAP. Options for other parameter values are not included in MIRC at this time; however, the user can overwrite values if appropriate. Refer to HHRAP ( EPA 2005 a, Chapter 5 and associated appendices) for detailed descriptions of these parameters and documentation of input values

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 53 

### Exhibit 6

- 2

. Chemical

- Specific Inputs for Produce Parameters

for Chemicals Included in MIRC

Chemical Fraction of Wet

Deposition ( Fw

) (unitless) a Root

Concentration Factor ( RCF

) (b elowground) (L/kg) b Soil

- Water

Partition Coefficient ( Kds ) (L/kg) c Chemical Air

- to

Plant Biotransfer Factor ( Bv

AG (i) ) (unitless) d

Inorganics Cadmium compounds 0.6 NA 7.5E+01 NA e Mercury (elemental) 0.6 NA 1.0E+03 0 f

Mercuric chloride 0.6 NA 5.8E +04 1.8E+03 Methyl mercury 0.6 NA 7.0E+03 0 f

Organics Benzo(a)anthracene 0.6 5.7E+03 6.0E+04 1.9E+04 Benzo(a)pyrene 0.6 9.7E+03 1.6E+05 1.2E+05 Benzo(b)fluoranthene 0.6 1.2E+04 1.0E+04 1.7E+03 Benzo(k)fluoranthene 0.6 1.2E+04 1.9E+05 2.1E+05
Ch rysene 0.6 5.7E+03 6.0E+04 6.9E+02 Dibenz(a,h)anthracene 0.6 2.3E+04 5.8E+05 3.1E+07 Indeno(1,2,3

- cd)
pyrene 0.6 2.8E+04 5.3E+05 3.7E+05 2,3,7,8

- TCDD 0.6 4.0E+04 3.9E+04 6.6E+04

Source: EPA 2005 a. NA = not applicable

.
a 6E

- 01 is the value for cati ons and most organic chemicals

. As described in HHRAP ( EPA 2005 a ), Appendix B ( available at http://www.epa.gov/osw/hazard/tsd/td/combust/finalmact/ssra/05hhrapapb.pdf) , EPA estimated this value ( EPA 1994a, 1995a) from a study by Hoffman et al

. (1992) in w hich soluble gamma

- emitting radionuclides and insoluble particles tagged with gamma

- emitting radionuclides were deposited onto pasture grass via simulated rain

. Note that the values developed experimentally for pasture grass may not accurately represent a ll aboveground produce

- specific values

. Also note that values based on the behavior of insoluble particles tagged with radionuclides may not accurately represent the behavior of organic compounds under site

- specific conditions

. b For nonionic organic c hemicals, a s described in HHRAP ( EPA 2005 a ), Appendix A (available at http://www.epa.gov/osw/hazard/tsd/td/combust/finalmact/ssra/05hhrapapa.pdf ), RCF is used to calculate the below

- ground transfer of contaminants from soil to a root vegetable on a wet

- we ight basis as shown in Equation 3

- 6

. EPA estimated chemical

- specific values for RCF from empirical regression equations developed by Briggs et al

. (1982) based on their experiments measuring uptake of compounds into barley roots from growth solution

. Bri ggs’ reg ression equations allow calculation of RCF values from log K ow . For metals and mercuric compounds, empirical values for soil to root vegetable transfer on a dry

- weight basis are available from EPA or other sources

.
c As discussed in HHRAP ( EPA 20 05 a ), Appendix A, Kds describes the partitioning of a compound between soi l
pore

- water and soil particles and strongly influences the release and movement of a compound into the subsurface soils and underlying aquifer

. Kds values for mercuric compounds we re obtained from EPA (1997 b )

. For all PAHs except for benzo(b)fluoranthene, Kds values were obtained from EPA 2004 a. For benzo(b)fluoranthene and 2,3,7,8

- TCDD, Kds values were calculated using the correlation equation provided in EPA 1993.

d As discusse d in HHRAP ( EPA 2005 a ), Appendix A, the v alue for mercuric chloride was obtained from EPA 1997 b. Bv

AG(i) values for PAHs were calculated using the correlation equation derived for azalea leaves as cited in Bacci et al

. (1992), then reducing this value by a factor of 100, as suggested by Lorber (1995)

, who concluded that the Bacci factor reduced by a factor of 100 was similar to his own observations in various studies

. The 2,3,7,8

- TCDD value was obtai ned from Lorber and Pinsky (2000 )

.
e It i s assumed th at metals, with the exception of vapor

- phase elemental mercury, do not transfer significantly from air into leaves

. f Speciation and fate and transport of mercury from emissions suggest that Bv AG(i) values for elemental and methyl
mercury are likely to be zero ( EPA 2005 a ).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 54 

### Exhibit 6

- 3 . Chemical

- Specific Inputs by Plant Type for Chemicals in MIRC

Compound Name Plant Part Plant

- Soil Bio

Concentration Factor ( Br AG

- produce

- DW(i) ) (unitless) a Empirical Corre ction

Factor

- Belowground Produce ( VG rootveg ) (unitless) b Empirical Correction

Factor

- Aboveground Produce ( VG AG(i) ) (unitless) c

Inorganics

Cadmium compounds Exp. Fruit 1.3E

- 01 NA 1.0E+00 Exp. Veg. 1.3E

- 01 NA 1.0E+00 Forage 3.6E

- 01 NA 1.0E+00
G rain 6.2E

- 02 NA NA

Prot. Fruit 1.3E

- 01 NA NA Prot. Veg. 1.3E

- 01 NA NA

Root 6.4E

- 02 1.0E+00 NA Silage 3.6E

- 01 NA 5.0E

- 01

Mercury (elemental) Exp. Fruit NA NA 1.0E+00 Exp. Veg. NA NA 1.0E+00 Forage NA NA 1.0E+00

Grain NA NA NA

Prot. Fruit N A NA NA Prot. Veg. NA NA NA

Root NA 1.0E+00 NA Silage NA NA 5.0E

- 01

Mercuric chloride Exp. Fruit 1.5E

- 02 NA 1.0E+00 Exp. Veg. 1.5E

- 02 NA 1.0E+00 Forage 0 NA 1.0E+00

Grain 9.3E

- 03 NA NA

Prot. Fruit 1.5E

- 02 NA NA Prot. Veg. 1.5E

- 02 NA NA

R oot 3.6E

- 02 1.0E+00 NA Silage 0 NA 5.0E

- 01

Methyl mercury Exp. Fruit 2.9E

- 02 NA 1.0E

- 02 Exp. Veg. 2.9E

- 02 NA 1.0E

- 02 Forage 0 NA 1.0E+00
Grain 1.9E

- 02 NA NA

Prot. Fruit 2.9E

- 02 NA NA Prot. Veg. 2.9E

- 02 NA NA

Root 9.9E

- 02 1.0E

- 02 NA Silage 0 NA 5.0E

- 01Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 55 

### Exhibit 6

- 3, cont inued

. Chemical

- Specific Inputs by Plant Type for Chemicals in MIRC

Compound Name Plant Part Plant

- Soil Bio

Concentration Factor ( Br AG

- produce

- DW(i) ) (unitless) a Empirical Correction

Factor

- Belowground Produce ( VG r ootveg ) (unitless) b Empirical Correction

Factor

- Aboveground Produce ( VG AG(i) ) (unitless) c

Organics

Benzo(a)anthracene Exp. Fruit 2.0E

- 02 NA 1.0E

- 02 Exp. Veg. 2.0E

- 02 NA 1.0E

- 02 Forage 2.0E

- 02 NA 1.0E+00

Grain 2.0E

- 02 NA NA

Prot. Fruit 2.0E

- 02 NA NA

Prot. Veg. 2.0E

- 02 NA NA

Root 9.5E

- 02 1.0E

- 02 NA Silage 2.0E

- 02 NA 5.0E

- 01

Benzo(a)pyrene Exp. Fruit 1.3E

- 02 NA 1.0E

- 02 Exp. Veg. 1.3E

- 02 NA 1.0E

- 02 Forage 1.3E

- 02 NA 1.0E+00
Grain 1.3E

- 02 NA NA

Prot. Fruit 1.3E

- 02 NA NA

Prot. Veg. 1.3E

- 02 NA NA

Root 6.1E

- 02 1.0E

- 02 NA Silage 1.3E

- 02 NA 5.0E

- 01

Benzo(b)fluoranthene Exp. Fruit 1.1E

- 02 NA 1.0E

- 02 Exp. Veg. 1.1E

- 02 NA 1.0E

- 02 Forage 1.1E

- 02 NA 1.0E+00

Grain 1.1E

- 02 NA NA

Prot. Fruit 1.1E

- 02 NA NA

Prot. Veg. 1.1E

- 02 NA NA

Root 1.2E+00 1.0E

- 02 NA Silage 1.1E

- 02 NA 5.0E

- 01

Benzo(k)fluoranthene Exp. Fruit 1.2E

- 02 NA 1.0E

- 02 Exp. Veg. 1.2E

- 02 NA 1.0E

- 02 Forage 1.2E

- 02 NA 1.0E+00
Grain 1.2E

- 02 NA NA

Prot. Fruit 1.2E

- 02 NA NA

Prot. Veg. 1.2E

- 02 NA NA

Root 6.1E

- 02 1.0E

- 02 NA Silage 1.2E

- 02 NA 5.0E

- 01

Chrysene Exp. Fruit 2.0E

- 02 NA 1.0E

- 02 Exp. Veg. 2.0E

- 02 NA 1.0E

- 02 Forage 2.0E

- 02 NA 1.0E+00

Grain 2.0E

- 02 NA NA

Prot. Fruit 2.0E

- 02 NA NA Prot. Veg. 2.0E

- 02 NA NA

Root 9.5E

- 02 1.0E

- 02 NA Silage 2.0E

- 02 NA 5.0E

- 01Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 56 

### Exhibit 6

- 3, continued. Chemical

- Specific Inputs by Plant Type for Chemicals in MIRC

Compound Name Plant Part Plant

- Soil Bio

Concentration Factor ( Br AG

- produce

- DW(i) ) (unitless) a Empirical Correction

Factor

- Belowgro und Produce ( VG rootveg ) (unitless) b Empirical Correction

Factor

- Aboveground Produce ( VG AG(i) ) (unitless) c

Dibenz(a,h)anthracene Exp. Fruit 6.8E

- 03 NA 1.0E

- 02 Exp. Veg. 6.8E

- 03 NA 1.0E

- 02 Forage 6.8E

- 03 NA 1.0E+00
Grain 6.8E

- 03 NA NA

Prot. Fru it 6.8E

- 03 NA NA Prot. Veg. 6.8E

- 03 NA NA

Root 4.1E

- 02 1.0E

- 02 NA Silage 6.8E

- 03 NA 5.0E

- 01

Indeno(1,2,3

- cd)pyrene Exp. Fruit 5.9E

- 03 NA 1.0E

- 02 Exp. Veg. 5.9E

- 03 NA 1.0E

- 02 Forage 5.9E

- 03 NA 1.0E+00

Grain 5.9E

- 03 NA NA

Prot. Fruit 5.9E

- 03 N A NA Prot. Veg. 5.9E

- 03 NA NA

Root 5.3E

- 02 1.0E

- 02 NA Silage 5.9E

- 03 NA 5.0E

- 01

2,3,7,8

- TCDD Exp. Fruit 4.6E

- 03 NA 1.0E

- 02 Exp. Veg. 4.6E

- 03 NA 1.0E

- 02 Forage 4.6E

- 03 NA 1.0E+00
Grain 4.6E

- 03 NA NA

Prot. Fruit 4.6E

- 03 NA NA Prot. Veg. 4.6E

- 03 NA NA

Root 1.0E+00 1.0E

- 02 NA Silage 4.6E

- 03 NA 5.0E

- 01
Source: EPA 2005a. NA = not applicable.

a As discussed in HHRAP ( EPA 2005a), the Br AG

- produce

- DW(i) for aboveground produce and forage accounts for the uptake from soil and the subsequen t transport of contaminants through the roots to the aboveground plant parts

. For organics, correlation equations to calculate values for Br on a dry weight basis were obtained from Travis and Arms (1988)

. For cadmium, Br values were derived from uptake slope factors provided in EPA 1992

. Uptake slope is the ratio of contaminant concentration in dry weight plant tissue to the mass of contaminant applied per hectare soil

. Br aboveground values for mercuric chloride and methyl mercury were calculated usin g methodology and data from Baes et al

. (1984)

. Br forage values for mercuric chloride and methyl mercury (on a dry weight basis) were obtained from EPA 1997b

. The HHRAP methodology assumes that elemental mercury doesn’t deposit onto soils

. Therefore, i t’s assumed that there is no plant uptake through the soil.

b As discussed in HHRAP ( EPA 2005 a ), Appendix B, VG rootveg represents an empirical correction factor that reduces produce concentration

. Because of the protective outer skin, size, and shape of bulky produce, transfer of lipophilic chemicals ( i.e., log Kow greater than 4) to the center of the produce is not likely

. In addition, typical preparation techniques, such as washing, peeling, and cooking, further reduce the concentration of the chemical in the vegetable as consumed by removing the high concentration of chemical on and in the outer skin, leaving the flesh with a lower concentration than would be the case if the entire vegetable were pureed without washing

. For belowground produce, HHRAP ( EPA 2005 a ) recommends using a VGr ootveg value of 0.01 for PB

- HAP with a log Kow greater than 4 and a value of 1.0 for PB

- HAP with a log Kow less than 4 based on information provided in EPA 1994b

. In developing these values, EPA (1994b) assumed that the d ensity of the skin and the whole vegetable are equal (potentially overestimating the concentration of PB

- HAP in belowground produce due to root uptake).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 57 

### Exhibit 6

- 3, continued. Chemical

- Specific Inputs by Plant Type for Chemicals in MI RC

c As discussed in HHRAP ( EPA 2005 a ), Appendix B, VG ag represents an empirical correction factor that reduces ab oveground produce concentration and was developed to estimate the transfer of PB

- HAP into leafy vegetation versus bulkier aboveground produce (e.g., apples)

. Because of the protective outer skin, size, and shape of bulky produce, transfer of lipophilic PB

- HAP (log Kow greater than 4) to the center of the produce is not likely

. In addition, typical preparation techniques, such as washing, peel ing, and cooking, further reduces residues

. For aboveground produce, HHRAP ( EPA 2005 a ) recommends using a VG ag value of 0.01 for PB

- HAP with a log Kow greater than 4 and a value of 1.0 for PB

- HAP with a log Kow less than 4 based on information provided in EPA 1994 b. In developing these values, EPA (1994 b ) assumed the following: (1) translocation of compounds deposited on the surface of aboveground vegetation to inner parts of aboveground produce would be insignificant (potentially underestimating the conc entration of PB

- HAP in aboveground produce due to air

- to

- plant transfer); (2) the density of the skin and the whole vegetable are equal (potentially overestimating the concentration of PB

- HAP in aboveground produce due to air

- to

- plant transfer); and (3) th e thickness of vegetable skin and broadleaf tree skin are equal (effects on the concentration of PB

- HAP in aboveground produce due to air

- to

- plant transfer unknown)

. For forage, HHRAP recommends a VG ag value of 1.0, also based on information provided in EPA 1994 b. A VG ag value for silage is not provided in EPA 1994 b ; the VGag value for silage of 0.5 was obtained from NC DEHNR (1997); however, NC DEHNR does not present a specific rationale for this recommendation

. Depending on the composition of the si te

- specific silage, this value may under

- or overestimate the actual value

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 58 

### Exhibit 6

- 4

. Non

- Chemical

- Specific Produce Inputs

Plant Part Interception

Fraction ( Rp (i) ) (unitless) a Plant

Surface Loss Co efficient ( k p (i) ) (1/year) b Length of

Plant Exposure to Deposition ( Tp (i) ) (year) c Yield or

Standing Crop Biomass ( Yp (i) ) (kg/m 2 ) d Plant Tissue

Specific Moisture Adjustment Factor ( MAF

(i) ) (percent) e
Exposed Vegetable 0.982 18 0.16 5.66 92

Protected Fruit NA NA NA NA 90

Protected Vegetable NA NA NA NA 80

Forage (animal feed) 0.5 18 0.12 0.24 92

Exposed Fruit 0.053 18 0.16 0.25 85 Root Vegetables NA NA NA NA 87 Silage (animal feed) 0.46 18 0.16 0.8 92 Grain (animal feed) NA NA NA NA 90

Source: EPA 2005 a. NA = not applicable

.
a Baes et al

. (1984) used an empirical relationship developed by Chamberlain (1970) to identify a correlation between initial Rp values and pasture grass productivity (standing crop biomass [ Yp ]) to calculate Rp values f or exposed vegetables, exposed fruits, forage, and silage

. Two key uncertainties are associated with using these values for Rp : (1) Chamberlain’s(1970) empirical relationship developed for pasture grass may not accurately represent aboveground produce

. ( 2) The empirical constants developed by Baes et al

. (1984) for use in the empirical relationship developed by Chamberlain (1970) may not accurately represent the site

- specific mixes of aboveground produce consumed by humans or the site

- specific mixes of fo rage or silage consumed by livestock.

b The term kp is a measure of the amount of chemical that is lost to natural physical processes (e.g., wind, water) over time

. The HHRAP

- recommended value of 18 yr - 1 (also recommended by EPA 1994a and 1998) represent s the midpoint of a range of values reported by Miller and Hoffman (1983)

. There are two key uncertainties associated with using these values for kp : (1) The recommended equation for calculating kp includes a conservative bias in that it does not consider chemical degradation processes

. ( 2) Given the reported range of kp values from 7.44 to 90.36 yr - 1 , plant concentrations could range from about 1.8 times higher to about 5 times lower than the plant concentrations estimated in FFC media using the midpoint kp value of 18.

c HHRAP ( EPA 2005a) recommends using a Tp value of 0.16 years for aboveground produce and cattle silage

. This is consistent with earlier reports by EPA (1994a, 1998) and NC DEHNR (1997), which recommended treating Tp as a constant based on the average period between successive hay harvests

. Belcher and Travis (1989) estimated this period at 60 days

. Tp is calculated as 60 days ÷ 365 days/year = 0.16 years

. For forage, the average of the average period between successive hay harvests (6 0 days) and the average period between successive grazing (30 days) is used (that is, 45 days), and Tp is calculated as (60 days + 30 days)/ 2 ÷ 365 days/yr = 0.12 yr

. Two key uncertainties are associated with use of these values for Tp : (1) The average p eriod between successive hay harvests (60 days) may not reflect the length of the growing season or the length between successive harvests for site

- specific aboveground produce crops

. The concentration of chemical in aboveground produce due to direct (wet and dry) deposition ( Pd ) will be underestimated if the site

- specific value of Tp is less than 60 days, or overestimated if the site

- specific value of Tp is more than 60 days.

d Yp values for aboveground produce and forage were calculated using an equatio n presented in Baes et al

. (1984) and Shor et al

. (1982): Yp = Y hi / A hi , where Y

hi = Harvest yield of i th crop (kg DW) and A hi = Area planted to i th crop (m2), and using values for Y h and A h from USDA (1994b and 1994c)

. A production

- weighted U.S

. averag e Yp of 0.8 kg DW/m2 for silage was obtained from Shor et al

. 1982.

e MAF represents the plant tissue

- specific moisture adjustment factor to convert dry

- weight concentrations into wet

weight concentrations (which are lower owing to the dilution by water c ompared with dry

- weight concentrations)

. Values obtained from Chapter 10 of EPA's 2003 SAB Review materials for 3MRA Modeling System, Volume II, “Farm Food Chain and Terrestrial Food Web Data” ( EPA 2003a), which references EPA 1997c

. Note that the value for grain used as animal feed is based on corn and soybeans, not seed grains such as barley, oats, or wheat.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 59 

### 6.2.3 Animal Product Parameter Values MIRC also requires chemical-specific inputs for many of the animal product algorithms. The relevant values are shown in Exhibit 6-5 for the chemicals included in MIRC to date. The HHRAP algorithms require additional inputs for the animal products calculations that are not specific to PB- HAPs , but are specific to the animal and animal product type. The soil and plant ingestion rates recommended in HHRAP for beef cattle, dairy cattle, swine, and chicken are provided in Exhibit 6-6

.

E xhibit 6

- 5

. Animal Product Chemica l

- specific Inputs for Chemicals Included in MIRC

Compound Name Soil Bio

Availability Factor ( Bs ) (unitless) Biotransfer Factors (Ba m ) (day/kg FW tissue) a and Metabolism Factors (MF) (unitless) b

Mammal Non

- mammal

Beef ( Ba beef ) Dairy ( Ba dairy ) P ork ( Ba pork ) MF Eggs

( Ba eggs ) Poultry

( Ba poultry ) MF

Cadmium compounds 1 1.2E

- 04 6.5E

- 06 1.9E

- 04 1 2.5E

- 03 1.1E

- 01 NA Mercury (elemental) 1 0 0 0 1 0 0 NA
Mercuric chloride 1 1.1E

- 04 1.4E

- 06 3.4E

- 05 1 2.4E

- 02 2.4E

- 02 NA Methyl mercury 1 1.2E

- 03 1.7E

- 05 5.1E

- 06 1 3.6E

- 03 3.6E

- 03 NA Benzo(a)anthracene 1 4.0E

- 02 8.4E

- 03 4.8E

- 02 0.01 1.7E

- 02 2.9E

- 02 NA Benzo(a)pyrene 1 3.8E

- 02 7.9E

- 03 4.5E

- 02 0.01 1.6E

- 02 2.8E

- 02 NA Benzo(b)fluoranthene 1 3.6E

- 02 7.6E

- 03 4.4E

- 02 0.01 1.5E

- 02 2.7E

- 02 NA Benzo(k)fluoranth ene 1 3.6E

- 02 7.7E

- 03 4.4E

- 02 0.01 1.5E

- 02 2.7E

- 02 NA Chrysene 1 4.0E

- 02 8.4E

- 03 4.8E

- 02 0.01 1.7E

- 02 2.9E

- 02 NA Dibenz(a,h)anthracene 1 3.1E

- 02 6.5E

- 03 3.7E

- 02 0.01 1.3E

- 02 2.3E

- 02 NA Indeno(1,2,3

- cd)
pyrene 1 2.9E

- 02 6.2E

- 03 3.6E

- 02 0.01 1.2E

- 02 2.2E

- 02 NA

2,3,7,8

- TCDD 1 2.6E

- 02 5.5E

- 03 3.2E

- 02 1 1.1E

- 02 1.9E

- 02 NA
Source: EPA 2005 a , unless otherwise indicated

. NA = not applicable

.
a As discussed in HHRAP ( EPA 2005 a ), Appendix A, biotransfer factors for mercury compounds were obtained from EPA 199 7 b

. Considering speciation, fate, and transport of mercury from emission sources, elemental mercury is assumed to be vapor

- phase and hence is assumed not to deposit to soil or transfer into aboveground plant parts

. As a consequence, there is no transfer of elemental mercury into animal tissues

. Biotransfer factors for cadmium compounds were obtained from EPA 1995 b

. Biotransfer factors for 2,3,7,8

- TCDD and PAHs were calculated from chemical octanol

- water partitioning coefficients (Kow values) using the c orrelation equation from RTI (2005) and assuming the following fat contents: milk

- 4%; beef

- 19%; pork

- 23%; poultry

- 14%; and eggs

- 8%.

b As discussed in HHRAP ( EPA 2005a), EPA (1995c) recommends using a metabolism factor ( MF ) to account for metaboli sm of PAHs by mammals to offset the amount of bioaccumulation suggested by biotransfer factors

. EPA has recommended an MF of 0.01 for bis(2

- ethylhexyl)phthalate (BEHP) and 1.0 for all other chemicals ( EPA 1995d )

. For MIRC, an MF of 0.01 is also used to c alculate concentrations of PAHs in food products from mammalian species ba sed on the work of Hofelt et al

. (2001)

. This factor takes into account the P450

- mediated metabolism of PAHs in mammals; applying this factor in our approach reduced the concentrati ons of chemicals in beef, pork, and dairy by two orders of magnitude.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 60 

### Exhibit 6

- 6

. Soil and Plant Ingestion Rates for Animals

Animal Soil Ingestion Rate

–

Qs (m) (kg/day) a Plant Part Consumed by Anim al Plant Ingestion Rate

– Qp (I,m) (kg/day)

Beef cattle b 0.5 Silage 2.5 Forage 8.8

Grain 0.47

Dairy cattle c 0.4 Silage 4.1 Forage 13.2

Grain 3.0

Swine d 0.37 Silage 1.4

Grain 3.3 Chicken (eggs) e 0.022 Grain 0.2

Source: EPA 2005 a HHRAP (Chapter 5).

a Beef cattle : NC DEHNR (1997) and EPA (1994 b ) recommended a soil ingestion rate for subsistence beef cattle of 0.5 kg/day based on Fries (1994) and NAS (1987)

. As discussed in HHRAP, Fries (1994) reported soil ingestion to be 4 percent of the total dry matter intake

. NAS (1987) cited an average beef cattle weight of 590 kg, and a daily dry matter intake rate (non

- lactating cows) of 2 percent of body weight

. This results in a daily dry matter intake rate of 11.8 kg DW/day and a daily soil ingestion rate of about 0.5 kg/day

. Dairy cattle : NC DEHNR (1997 ) and EPA (1994 b ) recommended a soil ingestion rate for dairy cattle of 0.4 kg/day based on Fries (1994) and NAS (1987)

. As discussed in HHRAP, Fries (1994) reported soil ingestion to be 2 percent of the total dry matter intake

. NAS (1987) cited an average beef cattle weight of 630 kg and a daily dry matter intake rate (non

- lactating cows) of 3.2 percent of body weight

. This resulted in a daily dry matter intake rate of 20 kg/day DW, and a daily soil ingestion rate of approximately 0.4 kg/day

. Uncertainties associated with Qs include the lack of current empirical data to support soil ingestion rates for dair y cattle and the assumption of uniform contamination o f soil ingested by cattle

. S wine : NC DEHNR (1997) recommended a soil ingestion rate for swine of 0.37, estimated by assuming a soil intake that is 8% of the plant ingestion rate of 4.3 kg DW/day

. Uncertainties include the lack of current empirical data to support soil ingestion rat es and the ass umption of uniform contamination of the soil ingested by swine. Chicken : HHRAP ( EPA 2005a) assumes that chickens consume 10 percent of their total diet (which is approximately 0.2 kg/day grain) as soil, a percentage that is consistent with t he study from Stephens et al

. (1995)

. Uncertainties include the lack of current empirical data to support soil ingestion rates for chicken and the assumption of uniform contamination of soil ingested by chicken.

b The beef cattle ingestion rates of forag e, silage, and grain are based on the total daily intake rate of about 12 kg DW/ day (based on NAS [1987] reporting a daily dry matter intake that is 2 percent of an average beef cattle body weight of 590 kg) and are supported by NC DEHNR (1997), EPA (1994 b and 1990), and Boone et al

. (1981)

. The principal unc ertainty associated with these Qp values is the variability between forage, silage, and grain ingestion rates for cattle

.

c The dairy cattle ingestion rates of forage, silage, and grain are based on the total daily intake rate of about 20 kg DW/day (NAS 1987; EPA 199 2 ) as recommended by NC DEHNR (1997)

. Uncertainties include the proportion of each food type in the diet, which varies from location to location

. Assuming uniform contamination of plant materials consumed by cattle also introduces uncertainty.

d Swine are not grazing animals and are assumed not to eat forage ( EPA 1998)

. EPA (1994 b and 1998) and NC DEHNR (1997) recommended including only silage and grains in the diet of swine

. EPA ( 199 5c) recommended an ingestion rate of 4.7 kg DW/day for a swine, referencing N AS (1987)

. Assuming a diet of 70 percent grain and 30 percent silage ( EPA 1990), HHRAP estimated ingestion rates of 3.3 kg DW/day (grain) and 1.4 kg DW/day (silage)

. Uncertainti es associated with Qp i nclude variability of the proportion of grain and silage in the diet, which varies from location to location

.

e Chickens consume grain provided by the farmer

. The daily quantity of grain feed consumed by chicken is assumed to be 0.2 kg/day (Ensminger ( 1980 ) , Fries ( 1982 ) , and NAS ( 1987)

. Uncertainties associated with this variable include the variability of actual grain ingestion rates from site to site

. In addition, assuming uniform contamination of plant materials consumed by chicken introduces some uncertainty.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 61 

### 6.3 Adult and Non-Infant Exposure Parameter Values
The exposure parameters included in MIRC and the ir default and other value options are summarized in the following subsections. The default values were selected to result in a highly conservative screening scenario. Parameter value options were primarily obtained or estimated from EPA’s Exposure Factors Handbook (EFH ; EPA

1997a) and Child-Specific Exposure Factors Handbook

(CSEFH; EPA 2008a) . Where values were reported for age groupings other than those used in MIRC (see Section 2.3 above for MIRC age groups), time-weighted average values were estimated for the MIRC age groups from the available data.

In MIRC, ingestion rates for home-produced farm food items are included for exposed fruit, protected fruit, exposed vegetables, protected vegetables, root vegetables, beef, total dairy, pork, poultry, and eggs. Those ingestion rates are already normalized to body weight (i.e., g wet
weight 

### /kg-day), as presented in the original data analysis ( EPA 1997a) . The body weight parameter values presented in Exhibit 6-7 , therefore, are not applied in the chemical intake (ADD) equations for these food types.

In MIRC, ingestion rates also are included for drinking water (mL/day), soil (mg/day), and fish (g/day). These ingestion rates, however, are on a per person basis (i.e., not normalized for body weight). The body weight parameter values presented in Exhibit 6-7 , therefore, are applied in the chemical intake (ADD) equations for these media.

6.3.1 Body Weights Body weight ( BW ) options included in MIRC include mean, 5 th 

### , 10 th 

### , 50 th 

### , 90 th 

### , and 95 th 

### percentiles for adults and the five children’s age groups . For its default screening assessment, EPA uses the mean BW for each age group. The BWs currently in the MIRC database are listed in Exhibit 6-7 . For adults, BW represents the weighted average of male and female mean body weights for all races, ages 18-74 year s, from EPA’s 1997 EFH (EPA 1997a; Tables 7- 4 and 7- 5)

. In general, BW values for the five children’s age groups were calculated from the summary data provided in Table 8-3 of EPA’s 2008 CSEFH

. For purposes of comparison, alternative BW values for children ages 12 through 19 years also were estimated using data from Portier et al

. ( 2007 ). These values are listed in the last row of Exhibit 6-7 , but are not included in MIRC

. The means calculated using the two methods for children ages 12 through 19 years were essentially identical at 64 kg. The other percentile values differed by approximately 10 percent or less.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 62 

### Exhibit 6

- 7

. Mean and Percentile Body Weight Estimates

for Adult s and Children
Lifestage (years) Duration

(years) Body Weight (kg)

Mean 5 th 10 th 50 th 90 th 95 th
Adult (20

- 70) a 50 71.4 52.9 56.0 69.3 89.7 97.6
Child < 1 b 1 7.83 6.03 6.38 7.76 9.24 9.66
Child 1

- 2 c 2 12.6 9.9 10.4 12.5 14.9 15.6
Child 3

- 5 d 3 18 .6 13.5 14.4 17.8 23.6 26.2
Child 6

- 11 e 6 31.8 19.7 21.3 29.3 45.6 52.5
Child 12

- 19 f 8 64.2 39.5 45.0 64.2 83.5 89.0 [Child 12

- 19 g 8 64.3 41.1 44.6 60.9 88.5 98.4]

a BW represents the sample

- size weighted average of male and female mean body weights (all races, 18

- 74 years) from EPA’s 1997 EFH (Tables 7

- 4 for males and 7

- 5 for females)

. Note that these weights include the weight of clothing, estimated t o range from 0.09 to 0.28 kg

. Although the 18 to 74 year age category in EPA’s EFH does not match exactly the age 20 to 70 year categorization of adults in MIRC, the magnitude of error in the mean and percentile body weights is likely to be very small (i.e., less than 1%).

b Each BW represents a time

- weighted average of body weights for age groups bi rth to <1 month, 1 to <3 months, 3 to <6 months, and 6 to <12 months from Table 8

- 3 of the 2008 CSEFH

. Original sample sizes for each of these age groups can also be found in Table 8

- 3.

c Each BW represents a time

- weighted average of body weights for age groups 1 to <2 years and 2 to <3 years from Table 8

- 3 of the 2008 CSEFH

. Original sample sizes for each of these age groups can also be found in Table 8

- 3.

d BWs obtained directly from Table 8

- 3 of the 2008 CSEFH (age group 3 to <6 years).

e BWs obtain ed directly from Table 8

- 3 of the 2008 CSEFH (age group 6 to <11 years)

. This value r epresents a conservative (i.e., slightly low) estimate of BW for ages 6 through 11 years since 11

- year olds are not included in this CSEFH age group.

f Mean BW estimated using Table 8

- 22 of the 2008 CSEFH, which is based on NHANES IV data as presented in Portier et al

. (2007)

. This estimate was c alculated as the average of the 8 single

- year age groups from 12 to 13 years through 19 to 20 years

. Values for the other perc entiles were estimated using Portier et al ., 2007

. g Each BW represents a time

- weighted average of body weights for age groups 11 to <16 years and 16 to <21 years from Table 8

- 3 of the 2008 CSEFH

. Note that estimated values include 11

- year

- olds and ind ividuals through age 20, which contributes to uncertainty in the estimates for 12 to 19 years

. Those values are provided for comparison purposes only and are not included in MIRC.



### 6.3.2 Water Ingestion Rates MIRC also includes the option of calculating chemical ingestion via drinking water obtained from surface-water sources or from wells (i.e., from groundwater) in the contaminated area. Users have the option in MIRC to set drinking water ingestion rates to zero or to revise the drinking water ingestion rates in MIRC to better reflect site-specific water uses. The 2008 CSEFH recommends values for drinking water ingestion rates for children based on a study reported by Kahn and Stralka (2008). Table 3-4 of the CSEFH provides per capita estimates of community water ingestion rates by age categories. Community water ingestion includes both direct and indirect ingestion of water from the tap. Direct ingestion is defined as direct consumption of water as a beverage, while indirect ingestion includes water added during food or beverage preparation. The source of these data is the 1994- 1996 and 1998 U.S. Department of Agriculture’s ( USDA ’s) Continuing Survey of Food Intakes by Individuals (CSFII) (USDA 2000). Exhibit 6-8 includes the dr inking water ingestion rates for children that are included in MIRC.

Mean and percentile adult drinking water ingestion rates were obtained from EPA (2004b), which presents estimated per capita water ingestion rates for various age categories based onAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 63 

### data collected by the USDA’s 1994– 1996 and 1998 CSFII (USDA 2000 ). Adult ingestion rates, presented in Exhibit 6-8 , represent community water ingestion, both direct and indirect as defined above, for males and females combined, ages 20 years and older.

Exhibit 6

- 8

. Estimated Daily Per Capita Mean and Percentile Water Ingestion Rates for Children and Adults a

Lifestage (years) Ingestion Rates, Community Water (mL/day)

Mean 50 th 90 t h 95 th 99 th

Child <1 b 324 146 866 * 1,011 * 1,377 * Child 1

- 2 c 294 217 654 857 1,290 * Child 3

- 5 d 380 291 834 1,078 1,654 Child 6

- 11 e 447 350 980 1,235 1,870 * Child 12

- 19 f 697 516 1,537 2,022 * 3,195 * Adult g 1,098 920 2,224 2,801 4,488 Sou rces: EPA 2004b, 2008a * T he sample size does not meet minimum reporting requirements as described in EPA 2008 a

. For some of these MIRC age groupings, the values are based on the time

- weighted average value for 2 or more age ranges from CSEFH Table 3

- 4

. O ne or more age ranges within the group may not meet the minimum reporting requirements

, but not necessarily all of them fall within this category

. a Source is Kahn and Stralka 2008 , also presented in the CSEFH ( EPA 2008 a).
b Each IR represents a time

- we ighted average of ingestion rates for age groups birth to <1 month, 1 to <3 months, 3 to <6 months, and 6 to <12 months from Table 3

- 4 of the 2008 CSEFH

. c Each IR represents a time

- weighted average of ingestion rates for age groups 1 to <2 years and 2 t o <3 years from Table 3

- 4 of the 2008 CSEFH.
d Each IR represents the ingestion rate for age group 3 to <6 years from Table 3

- 4 of the 2008 CSEFH.

e Each IR represents the ingestion rate for age group 6 to <11 years from Table 3

- 4 of the 2008 CSEFH

. This value r epresents a conservative (i.e., slightly low) estimate of IR for ages 6 through 11 years since 11

- year olds are not included in this CSEFH age group.
f Each IR represents a time

- weighted average of ingestion rates for age groups 11 to <16 years, 16 to <18, and 18 to <21 years from Table 3

- 4 of the 2008 CSEFH

. Note that estimated values include 11

- year

- olds and individuals through age 20, which contributes to uncertainty in the estimates for 12 to 19 years.

g Adult drinking water ingestion rates were obtained from EPA (2004 b ), Appendix E, Part I, Table A1 for community water, both sexes (ages 20+), direct plus indirect water ingestion.



### 6.3.3 Local Food Ingestion Rates MIRC includes mean, median, 90 th 

### , 95 th 

### , and 99 th 

### percentile food-specific ingestion rates (IRs) for consumers-only of farm food chain (FFC) media for adults and children. The mean and percentile values are from EPA’s analysis of data from the USDA’s 1987 to 1988 Nationwide Food Consumption Survey (NFCS) (USDA 1993), as presented in Chapter 13 of the Agency’s Exposure Factors Handbook (i.e., Intake Rates for Various Home Produced Food Items) ( EPA 1997a) . Consumers-only means that individuals who did not report eating a specified type of food during the three-day period covered by the food ingestion part of the survey were not included in the analysis of ingestion rates for that food type. The questionnaire included the options for a household to self-identify in one or more of five categories: as a household that gardens, raises animals, hunts, fishes, or farms. As of September, 2008, that survey was the most recent NFCS available ( EPA 2008a, CSEFH), and we are not aware of any that might be more recent. 2



### For the adult age group in MIRC, we compiled data on food-specific IRs separately for two types of households as indicated in the “Response to Questionnaire” ( EPA 1997 a, Chapter 13): (1) households that farm (F) and (2) households that garden or raise animals (HG for homegrown).

2 Note that EPA’s 2008 CSEFH does n ot distinguish between exposed and protected fruits and vegetables when recommending food ingestion rates based on the same data set for the same age categories

. EPA’s 1997 analysis for its EFH therefore remains the most appropriate data source for use in MIRC.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 64 

### This division reflects EPA’s data analysis . EPA tabulated IRs for fruits and vegetables for households that that farm and for households that garden. EPA tabulated IRs for animals and animal products for households that farm and for households that raise animals. Thus, the first type of household, F, represents farmers who may both grow crops and raise animals and who are likely to consume more home grown/raised foods than the second type of household. The second type of household, HG, represents the non-farming households that may consume lower amounts of home- gr own or raised foods (i.e., HG encompasses both households that garden and households that raise animals).

Th e food-specific ingestion rates are based on the amount of each food type that households that farm (F) or households that garden and raise animals (HG) produced and brought into their homes for consumption and the number of persons consuming the food. EPA averaged the actual consumption rate for home-grown foods over the 1-week survey period

. The default food-specific ingestion rates in MIRC for adults are those for farming households (F) in Exhibit 6-9 . The user can specify use of the generally less conservative, non-farming household (HG) ingestion rates if they are more appropriate for the user’s exposure scenario (s econd column of IR values under Adults in Exhibit 6-9 ).

Exhibit 6

- 9

. Summary of Age

- Group

- Specific Food Ingestion Rates for Farm Food Items

Product Ingestion Rate by Age Group (g/ kg

- day) Children (F arm and H omegrown ) e Adults
Child <1 Child

1

- 2 Child

3

- 5 Child

6

- 11 Child

12

- 19 Farm f H omegrown g

Mean

Beef a NA 1.49 2.21 3.77 1.72 2.63 2.66 Dairy d NA 67 37 24.79 10.90 17.1 15.9 Eggs d NA 2.5 1.4 0.86 0.61 0.90 0.75 Expose d Fruit b NA 1.8 2.6 2.52 1.33 2.32 1.55 Exposed Vegetable NA 3.5 1.7 1.39 1.07 2.17 1.57

Pork d NA 2.2 2.1 1.49 1.17 1.30 1.34 Poultry d NA 3.6 3.4 2.13 1.59 1.54 1.58

Protected Fruit d NA 19 13 8.13 5.44 5.19 c 5.9 Protected Vegetable NA 2.5 1.3 1.1 0.776 1.3 1.01 Root Vegetable NA 2.5 1.3 1.32 0.937 1.39 1.15Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 65 

### Exhibit 6

- 9 , continued

. Summary of Age

- Group

- Specific Food Ingestion Rates for Farm Food Items

Product Ingestion Rate by Age Group (g/kg

- day)

Children (Farm and Homegr own) e Adults
Child <1 Child

1

- 2 Child

3

- 5 Child

6

- 11 Child

12

- 19 Farm f Homegrown g

50 th Percentile
Beef a NA 0.84 1.23 2.11 1.51 1.64 1.83 Dairy d NA 102 60 39 14 12.1 10.8 Eggs d NA 1.5 0.79 0.56 0.49 0.67 0.48 Exposed Fruit b NA 1.2 1.82 1.11 0 .609 1.3 0.88 Exposed Vegetable NA 1.9 1.2 0.643 0.656 1.38 0.89

Pork d NA 1.8 1.4 1.02 1.02 0.924 0.97 Poultry d NA 2.9 2.7 1.4 1.4 1.06 1.37

Protected Fruit d NA 10.2 7.6 4.2 2.3 2.08 c 2.42 Protected Vegetable NA 1.94 1.04 0.791 0.583 0.599 0.64

R oot Vegetable NA 0.92 0.46 0.523 0.565 0.88 0.67

90 th Percentile
Beef a NA 4.5 6.7 11.4 3.53 5.39 5.39 Dairy d NA 148 82 54.67 26.98 34.9 34.9 Eggs d NA 5.1 2.8 1.8 1.34 1.65 1.36 Exposed Fruit b NA 3.7 5.4 6.98 3.41 5 3.41 Exposed Vegetable NA 10.7 3.47 3.22 2.35 6.01 3.63

Pork d NA 4.5 4.4 3.04 2.65 3.08 2.9 Poultry d NA 7.4 6.8 4.58 3.28 3.47 2.93

Protected Fruit d NA 53 36 24.14 16.19 15.14 c 16 Protected Vegetable NA 3.9 2.5 2.14 1.85 3.55 2.32 Root Vegetable NA 7.3 4.3 3.83 2.26 3.11 2.81

95 th Percentile

Beef a NA 5.0 7.3 12.5 3.57 7.51 7.51 Dairy d NA 139 75 52 27 44 44 Eggs d NA 5.5 3.7 2.4 1.5 1.85 1.85 Exposed Fruit b NA 4.1 6.1 12 4.8 6.12 5.0 Exposed Vegetable NA 11.9 6.29 5.5 3.8 6.83 5.45

Pork d NA 6.2 6.0 4.7 3.3 3.7 3.4

P oultry d NA 8.2 7.2 5.3 3.7 4.8 3.3

Protected Fruit d NA 59 42 28 20 19.16 c 19.1 Protected Vegetable NA 9.4 5.1 3.12 2.2 5.4 3.05 Root Vegetable NA 10.4 4.73 5.6 3.3 4.6 3.64Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 66 

### Exhibit 6

- 9 , continued

. Summary of Age

- Group

- Specific Fo od Ingestion Rates for Farm Food Items

Product Ingestion Rate by Age Group (g/kg

- day)

Children (Farm and Homegrown) e Adults
Child <1 Child

1

- 2 Child

3

- 5 Child

6

- 11 Child

12

- 19 Farm f Homegrown g

99 th Percentile
Beef a NA 5.3 7.8 13.3 4.3 11 12.5 Dairy d NA 113 56 37 24 80 80 Eggs d NA 16 12 8.6 5.0 6.6 6.6 Exposed Fruit b NA 22 32.5 16 5.9 16 12.9 Exposed Vegetable NA 12 7.4 13 5.7 10 10

Pork d NA 9.1 9.9 6.3 4.2 4.9 4.3 Poultry d NA 10 10 6.4 4.8 6.2 5.3

Protected Fruit d NA 113 81 57 45 34 .42 c 47.3 Protected Vegetable NA 9.4 5.3 5.4 2.69 9.2 6.49 Root Vegetable NA 10.4 4.7 7.5 5.1 7.5 7.5
Source: EPA 1997 a (Chapter 13), unless otherwise noted. NA = not applicable

a No data are available for Child 1

- 2 or Child 3

- 5

. The v alue for Child 6

- 11 was used, scaled down by the ratio of the mean body weight for Child 1

- 2 or Child 3

- 5, as appropriate, to the mean body weight of Child 6

- 11

. b No data are available for Child 1

- 2

. The v alue for this age group is the IR for Child 3

- 5, scaled down b y the ratio of the mean body weight for Child 1

- 2 to the mean body weight for Child 3

- 5

. c These values represent a time

- weighted average IR for two age groups, using exposure duration (ED) for the 20

- 39 (ED=20 years) and 40

- 69 year age groups (ED=30 yea rs).
d In many cases, intake rates for children were not available in EPA ’s 1997 EFH

. Intakes for these receptor groups were calculated using the methodology recommended in HHRAP ( EPA 2005 a ), Section 6.2.2.2

. Sources to develop these values included EPA 1997 a and EPA 2003b.

e In Chapter 13 of the 1997 EPA EFH, age group

- specific IRs are provided for home produced items as a whole; separate IRs are not presented for children from households that raise animals and households that farm.
f These values repres ent the IRs for “households who farm.”

g These values represent the IRs for “households who raise animals.”



### For children, EPA estimated food-specific IRs for four age categories ( EPA 1997 a): 1 to 2 years, 3 to 5 years, 6 to 11 years, and 12 to 19 years. Sample sizes were insufficient to distinguish IRs for children in different types of households; hence, for children, a single IR value represents both F and HG households for a given food type and age category ( Exhibit 6-9 ). For some food types and age categories, there were insufficient data for EPA to provide consumer-only intake rates (i.e., data set for the subpopulation consisted of fewer than 20 observations). The HHRAP methodology, Section 6.2.2.2, recommends a method by which to calculate the “missing” age -specific consumer-only ingestion rates, as explained below

. Fo od

specific intake rates (IRs) for those child age groups and food items not included in Chapter 13 of the 1997 EFH, that is IR age_group

_x 

### , were derived using the following information:

Mean or percentile-specific consumer-only intake of the farm food item, as brought into the home, for the total NFCS survey population (from EFH Chapter 13)

– IR CO_total 

### ; Mean or percentile-specific per capita

intake of the food type from all sources, as consumed, for the specific child age group, from Chapter 3 of the CSFII Analysis of Food Intake Distributions

( EPA 2003c)

– IR

PC, age_group

_x 

### ; and Mean or percentile-specific per capita

intake of the farm food item for the total CSFII survey population (from Chapter 3 of EPA 2003c)

– IR

PC_total


### .Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 67 

### The ratio of IR PC, age_group

_x 

### to IR

PC_tot al 

### from the CSFII data shows the consumption rate of a particular food type by a specific age group relative to the consumption rate for that food type for the population as a whole. The ratio of IR CO, age_group _x 

### to IR CO_total 

### , that is the consumption rate of a particular food type by a specific age group (consumers only) relative to the consumption rate for that food type for the NFCS survey population as a whole (consumers only), should be approximately the same. Given the assumption that the two ratios are equal, Equation 6-2 was used to calculate the “missing” age -specific consumer-only IRs :

Equation 6-1. Calculation of Age-Group-Specific and Food-Specific Ingestion Rates

where:

IR CO, age

_ group _x = Mean or percentile

- specific consumer

- only intake of the food type from all sources, as consumed, for the specific child age group X

IR CO_total = Mean or percentile

- specific consumer

- only intake of the farm food item, as brought into the home, for the total NFCS survey population

IR PC, age

_ group _x = Mean or percentile

- specific per capita intake of the food type from all sources, as consumed, for the specific child age group X from the CSFII

IR PC_total = Mean or percentile

- specific per capita intake of the farm food item for the total

CSFII survey population



### In this discussion

, per capita (as opposed to consumer-only ) indicates the intake rates are based on the entire population rather than the subset of the population that ingests the particular food category (i.e., consumers). Here, the use of per capita ingestion rates are recommended by the HHRAP methodology because no consumer-only percentile-specific intakes are provided for the different age groups.

The above calculation implicitly assumes that the distribution of the consumption rate for a food type for a specific age group (consumers only) has the same shape as the distribution of the consumption rate for a food type for a specific age group in the general population ( per capita ). Otherwise, the separate calculation of each percentile might yield intake estimates that decrease as the percentile increases. This calculation artifact could occur if the shapes of the two distributions differ in the upper percentiles (or “tails”) of the distributions.

In the instances where the above calculations were used to fill data gaps in the above exhibit

, only the dairy child-specific age group intake estimates are not strictly increasing with increasing percentile. The distributions likely track better (and thus the above assumption of equal ratios is more reasonable) for lower percentiles, with deviations occurring du e to outlier ingestion rates based on only a few respondents in the tails of the distributions. The MIRC defaults use the 90 th 

### percentile ingestion estimates, which are likely more reliable than the 95 th 

### or 99 th 

### percentile estimates in this particular calculation.

6.3.4 Local Fish Ingestion Rates The USDA’s 1987 to 1988 Nationwide Food Consumption Survey (NFCS) (USDA 1993, 1994a), as presented in Chapter 13 of the Agency’s Exposure Factors Handbook (i.e., Intake Rates for Various Home Produced Food Items) ( EPA 1997a), includes family-caught fish ingestion rates by age category

. There are several disadvantages, however, to using that data source toAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 68 

### estimate fish ingestion rates. First, due to inadequate sample sizes, EPA did not report fish IRs for children less than 6 years of age. Second, the NFCS data were collected approximately two decades ago. Third, the reported fish IRs are for ages 6 to 11 and 12 to 19 and are based on 29 and 21 individuals in each age category, respectively ( EPA 1997a, Table 13- 23) . Finally, the IRs from NFCS data are based on total weight of fish as brought into the home, and do not include losses from preparation of the fish (i.e., removal of inedible parts and, possibly, the skin). Estimates of preparation losses for fish intended to apply to the NFCS fish IR data are very uncertain and are based on a wide variety of freshwater, estuarine, and marine fish, and squid ( EPA

1997a, Table 13- 5) . Therefore, a more recent survey was sought that included larger sample sizes, data for children younger than six years, and IRs for the parts of fish actually consumed.

EPA’s (2002) analysis freshwater and estuarine fish consumption from the USDA’s Continuing Survey of Food Intake by Individuals (CSFII) for 1994-96 and 1998 was chosen to provi de per capita fish IR options by age category in MIRC

. Although the fish consumption rates reported in the CSFII include all sources, commercial and self-caught, for purposes of screening level risk assessments, it was assumed that all freshwater and estuarine fish consumed are self-caught. The inclusion of commercially obtained and estuarine fish will overestimate locally caught freshwater fish IRs for many rural populations in the United States; however, it also may underestimate locally caught fish IRs for some populations (e.g., Native Americans, Asian and Pacific Island communities, rural African American communities). Because consumption of locally caught fish varies substantially from region to region in the United States and from one population or ethnic group to the next, users of MIRC are encouraged to use more locally relevant data whenever available

. For children ages 3 to 17 years and for adults, MIRC includes values for the mean and the 90th, 95th, and 99th percentile fish ingestion rates (freshwater and estuarine fish only) based on EPA’s analysis of 1994 -96 and 1998 CSFII data ( EPA 2002, 2008a). As shown in EPA’s 2008(a) CSEFH, Table 10-7, the 90th percentile per capita ingestion rates estimated from the two-day CSFII recall period are zero for some child age groups. Although not presented in CSEFH Table 10-7, median ingestion rates for all child age groups would be zero (considering the “consumer only” sample sizes [CSEFH Table 10

- 9] relative to the “ per capita ” sample sizes in Table 10- 7)

. The high percentile fish IRs that are zero result from the short duration of the CSFII survey (two days) compared with the averaging time of interest (a year) and the relatively infrequent consumption of fish (e.g., on the order of once a week to once a month or less) compared with the near daily ingestion of other types of food products (e.g., dairy, produce, meat). Use of zero for fish IRs, however, is not useful in MIRC. As a result, an alternative method was used to estimate fish ingestion rates for children and adults that could provide reasonable, non-zero values for all age groups and percentiles.

The alternative, age-group-specific fish ingestion rates were derived using values for each age
group, y :

Mean or other appropriate percentile c onsumer-only fish ingestion rates for age group y , IR CO,y 

### , from EPA ’s Estimated Per Capita Fish Consumption in the United States ( EPA 2002), Section 5.2.1.1, Table 5, for freshwater/estuarine habitat. 3

3 Most of these data also are provided in Table 10-9 of the CSEFH; the median values, however, are not presented in the CSEFH, and values for the mean and all other percentiles are slightly different due to rounding.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 69 

### Fraction of the population consuming freshwater/estuarine fish, F PC,y 

### , calculated as consumer-only sample size / U.S

. population sample for age group y . The data to calculate these fractions are available in the 2008 CSEFH and EPA 2002.

Equation 6-2 was used to calculate the alternative, per capita fish ingestion rates by age group 

### ( IR PC,y 

### ):

Equation 6-2

. Calculation of Alternative Age-Group-Specific Fish Ingestion Rates

where:

IR PC,y = Per capita fish ingestion rate for age group y (g/day)

IR CO,y = Consumer

- only fish ingestion rates for age group y (g/day) ( EPA 2002, Section 5.2.1.1, Table 5, for freshwater/estuarine habitat)

F PC,y = Fraction of the population consuming freshwater/estuarine fish, calculated as

consumer

- only sampl e size / total U.S

. population sample size for age group y (unitless) (2008 CSEFH, EPA 2002)



### In the above, per capita (as opposed to consumer-only ) indicates the intake rates are based on the entire population rather than the subset of the population that ingests the particular food category. Here, per capita ingestions are recommended by the HHRAP methodology because no consumer-only percentile-specific intakes are provided for the different age groups.

The mean and percentile consumer-only fish ingestion rates for children and adults and the fraction of the population consuming freshwater/estuarine fish used in calculating long-term per capita fish ingestion rates by age group are presented in Exhibit 6- 10 and Exhibit 6- 11 . The mean and percentile per capita fish ingestion rates estimated using this methodology are summarized in Exhibit 6- 12 and are available in MIRC. (Note that as detailed in Appendix 5, Exhibit 3-6, in developing the screening threshold emission rates, a conservative fish ingestion rate of 105.5 g/day was used.)

The fish ingestion rates provided in Exhibit 6- 12 and included in MIRC are intended to represent the harvest and consumption of fish in surface waters in a hypothetical depositional area. For site-specific application of this tool, users should consider using more localized survey data to estimate more appropriate fish ingestion rates. The fishing season varies substantially across the United States by latitude, and fish consumption patterns also vary by type of water body (e.g., ponds, lakes, rivers, streams, estuaries, coastal marine), cultural heritage, and general geographic area. Therefore, use of more localized information is encouraged.

As noted in Section 6.4.3, if the user overwrites the fish IRs shown in Exhibit 6- 12 with freshweight as caught values (e.g., values obtained from a local creel survey), the user is advised to set non-zero values for the preparation and cooking loss factors L1 and L2 in Equation 3-15. Suggested values are presented in Section 6.4.3.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 70 

### Exhibit 6

- 11

. Fraction of Population Consuming Freshwater/Estuarine Fish on a Single Day ( F PC,y 

### )

L ifestage (years) Fraction Consuming Fish

Child 3

- 5 0.0503 a

Child 6

- 11 0.0440 b

Child 12

- 19 0.0493 c

Adult 0.08509 d
Sources: EPA 2002, 2008a

a This value was calculated using the a ges 3 to 5 sample size for consumers only divided by the sample siz e for the U.S

. population divided by 2 to represent the proportion consuming fish on a single day (the

consumers

- only group includes individuals who consumed fish on at least one of two survey days) to match the one

- day ingestion rate.
b As in footnote a , the value was calculated using the a ges 6 to 10 sample size for consumers only divided by the sample size for U.S

. population divided by 2.

c The value was calculated by summing the ages 11 to 15 and 16 to 17 sample sizes for consumers only and dividing by both by the sum of the sample sizes for U.S

. population and by a factor of 2.
d The value was calculated using the ages 18 and older sample size for consumers only divided by the sample size for U.S. population from Section 5.1.1.1 Table 4. The result wa s divided by 2 to represent a

one

- day sampling period in order to match the one

- day ingestion rate. 

### Exhibit 6

- 10

. Daily Mean and Percentile Consumer

- Only Fish Ingestion R ates for Children and Adults ( IR CO,y 

### ) a

Lifestage (years) Ingestion Rates, All Fish (g/day)

Mean 50th 90 th 95 th 99 th

Child <1 NA NA NA NA NA
Child 1

- 2 b 27.31 15.61 64.46 87.60 138.76 *
Child 3

- 5 c 40.31 23.04 95.16 129.31 204.84 *
Child 6

- 11 d 61. 49 28.46 156.86 * 247.69 * 385.64 *
Child 12

- 19 e 79.07 43.18 181.40 * 211.15 * 423.38 *
Adult f 81.08 47.39 199.62 * 278.91 505.65 * Sources: EPA 2002, 2008a N A = not applicable; it is assumed that children < 1 year of age do not consume fish. * Indica tes that the sample size does not meet minimum reporting requirements as described in EPA 2002

. Owing to the small sample sizes, these upper percentiles values are highly uncertain.

a Per capita fish ingestion (FI) rates for children by age group are avai lable from Chapter 10 of the CSEFH ( EPA 2008a); however, all 50th and some 90th percentile ingestion rates are zero

. Per capita FI rates were therefore estimated as described in Equation 6

- 2 to provide reasonable, non

- zero values for all age groups and pe rcentiles.
b A fish IR for ages 1

- 2 years was not available . The v alue represents the consumer

- only fish ingestion rate for ages 3 to 5 from EPA (2002) (Section 5.2.1.1 Table 5 [freshwater/estuarine habitat]), scaled down by the ratio of the mean Child 1

- 2 body weight to the mean Child 3

- 5 body weight

. c These values represent the consumer

- only fish ingestion rate for ages 3 to 5 from EPA (2002), Section 5.2.1.1 Table 5 (freshwater/estuarine habitat)

. Sample size = 442.
d These values represent the cons umer

- only fish ingestion rate for ages 6 to 10 from EPA (2002), Section 5.2.1.1 Table 5 (freshwater/estuarine habitat)

. Sample size = 147.

e These values represent the time

- weighted average per capita fish ingestion rate for ages 11 to 15 and 16 to 17
yea rs from EPA (2002), Section 5.1.1.1 Table 5 (freshwater/estuarine habitat); the value may underestimate ingestion rate for ages 12 to 19 years

. Sample size = 135.
f These values r epresent the consumer

- only fish ingestion rate for individuals 18 years and older from EPA (2002), Section 5.2.1.1 Table 4 (freshwater/estuarine habitat)

. Sample size = 1,633.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 71 

### Exhibit 6

- 12

. Calculated Long

- term Mean and Percentile Per capita Fish Ingestion Rate s for Children a nd Adults ( IR PC,y 

### )

Lifestage (years) Ingestion Rates, All Fish (g/day)

Mean 50th 90 th 95 th 99 th

Child <1 NA NA NA NA NA
Child 1

- 2 a 1.37 0.79 3.24 4.41 6.98
Child 3

- 5 b 2.03 1.16 4.79 6.51 10.3
Child 6

- 11 c 2.71 1.25 6.90 10.9 17.0
Child 12

- 19 d 3.9 0 2.13 8.95 10.4 20.9
Adult e 6.90 4.03 16.99 23.73 43.02

Sources: EPA 2002, 2008a N A = not applicable; it is assumed that children < 1 year of age do not consume fish.

a V alues were c alculated as (consumer

- only IR for Child 1

- 2) x (fraction of popula tion consuming fish for Child 3

- 5).
b V alues were c alculated as (consumer

- only IR for Child 3

- 5) x (fraction of population consuming fish for Child 3

- 5).

c V alues were c alculated as (consumer

- only IR for Child 6

- 11) x (fraction of population consuming fish for Child 6

- 11).
d V alues were c alculated as (consumer

- only IR estimated for Child 12

- 19) x (fraction of population estimated to consume fish for Child 12

- 19).

e V alues were c alculated as (consumer

- only IR for Adults) x (fraction of population consuming f ish for Adults).



### MIRC also includes values for the mean and the 90th percentile fish ingestion rates for recreational anglers, black and female recreational anglers, and anglers of Hispanic, Laotian, and Vietnamese descent which are shown in Exhibit 6- 13 These populations are culturally or economically disposed to higher rates of fish ingestion than the general population. Recreational angler values are the EFH (EPA, 1997.) Black and female recreational anglers ingestion rates are presented in Burger et al . (2010.) The fish ingestion rates for Hispanic, Laotian, and Vietnamese populations were derived from a study by Shilling et al . (2010) of

c ontaminated fish consumption in California’s Central Valley Delta. Shilling et al

. (2 010) reported mean and 95 th 

### percentile ingestion rates for each subpopulation. In part due to the low sample size (n of 30 to 45), 95 th 

### percentile values were believed to be unrealistically high. The 90 th 

### percentile ingestion rate estimates presented in Exhibit 6- 13 were derived by EPA using information from Shilling et al . (2010; EPA, 2010 ).

Exhibit 6

- 13 . Calculated Mean and 90 th 

### Percentile Per capita Fish Ingestion Rates for Popu lations of Recreational Fishers (IR PC,y 

### ) Subpopulation

Percentile Units Recreational Fisher a Female

Recreational Fisher b Black

Recreational Fisher b Hispanic

Recreational Fisher c Laotian

Recreational Fisher c Vietnamese

Recreational Fisher c

Ingest ion of Fish



### Mean g/day 

### 8 39.1 171 25.8 47.2 27.1

90th % g/day 

### 11 123 446 98 144.8 99.1

a 1997 Exposure Factors Handbook (USEPA, 1997)
b Burger et al., 2010 , weights reported are post

- cooking for locally caught fish

c Shilling, F., A. White, L. Lippert , and M. Lubell. 2010. Contaminated fish consumption in California’s Central Valley Delta. Environmental Research 110: 334

- 344. , weights reported are post

- cooking for locally caught fish Burger et al ., 2010Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 72 

### Applications to date of MIRC have used whole fish concentrations estimated by TRIM.FaTE. The proportion lipid in TL3 and TL4 fish in TRIM.FaTE is assumed to be 5.7 percent (by weight) for the whole fish, based on information provided by Thomann (1989)

. The lipid content of the part(s) of the fish normally consumed is likely to be less than 5.7 percent. For example, EPA estimated a consumption-weighted mean lipid value for fillets of fish from TL3 to be 2.6 percent and from TL4 to be 3.0 percent (Table 6-9 in EPA 2003b) . If a user of MIRC wishes to account for reduced chemical concentration in fillet compared with whole fish for lipophilic chemicals, the user can specify a “preparation” loss of chemical (see Section 6.4).

For lipophilic chemicals (e.g., log Kow greater than 4), which partition primarily into the fatty tissues of fish, much of the higher concentration tissues might be stripped from the fish during preparation (e.g., belly fat, viscera which includes fat in liver, etc, fat under skin). The degree to which the concentration of chemical in a fillet is less than the average total concentration in the whole fish is chemical specific. Assuming that the chemical concentration in the fillet is the same as in the whole fish may result in a conservative bias for highly lipophilic chemicals. For persons who prefer to consume fillets with the skin on and do not discard belly fat, assuming the same concentration of chemical in the fish consumed as in the whole fish is protective.

6.3.5 Soil Ingestion Rates Adult gardeners may incidentally ingest soils from gardening activities, and gardening and farming families might ingest soil particles that adhere to exposed fruits and exposed and belowground vegetables. Soils that are re -suspended in the air by wind can resettle on exposed fruits and vegetables

. Ch ildren may incidentally ingest soils in those ways, but in addition, children playing outdoors may ingest soils directly or by hand- to -mouth activities during play

. MIRC includes soil ingestion rate options by age group for these types of exposures. MIRC does not include options for children who may exhibit pica, or the recurrent ingestion of unusually high amounts of soil (i.e., on the order of 1,000 - 5,000 mg/day or more) ( EPA 2008 a).

Data on soil ingestion rates are sparse; the soil ingestion rates listed in Exhibit 6- 14 and included in MIRC are based on very limited data, as is evident from the values listed. The studies evaluated by EPA for children generally focused on children between the ages of 1 and 3 to 6 years and were not specific to families that garden or farm. The default ingestion rates in MIRC are the 90 th 

### percentile values, as for other ingestion rate parameters.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 73 

### Exhibit 6

- 14

. Daily Mean and Percentile Soil I ngestion Rates for Children and Adults
Age Group (years) Soil Ingestion Rate (mg/day)

Mean a 50 th a 90 th 95 th 99 th

Child < 1 NA
Child 1

- 2 50 50 400 b 400 b 400 b

Child 3

- 5 50 50 400 b 400 b 400 b

Child 6

- 11 50 50 201 c 331 d 331 d

Child 12

- 19 50 50 201 c 331 d 331 d

Adult 20

- 70 50 50 201 c 331 d 331 d

Sources: EPA 1997a, 2008a

a For the mean and 50 th percentile soil ingestion rates for children, value represents a “central tendency” estimate from EPA’s 2008 CSEFH, Table 5

- 1

. For adults, value is the recommended mean value for adults from EPA’s 1997 EFH, Chapter 4, Table 4

- 23.
b These values are the recommended “upper percentile” value for children from EPA’s 1997 EFH, Chapter 4, Table 4

- 23

. The 2008 CSEFH included a high

- end value associated w ith pica only.

c These values are 90th percentile adult ingestion rate s calculated in Stanek et al

. 1997 , and they are used to represent older children and adults

. d These v alue s are 95th percentile adult ingestion rate s calculated in Stanek et al

. 1997 , a nd they are used to represent older children and adults

. 

### 6.3.6 Total Food Ingestion Rates Although not included in MIRC for deterministic screening-level exposure and risk assessments, total food ingestion rates would be included in any probabilistic module develop ed for MIRC

. The total food ingestion rates presented in Exhibit 6- 15 will be used to normalize or to truncate the sum of food-specific ingestion rates to reasonable values

. This procedure is particularly important when chemical intake from multiple upper-percentile food ingestion rates for different types of food are added together. Individuals representing the upper percentile ingestion rate for one food category might not be the same individuals who reported high percentile ingestion rates for one or any of the other food categories.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 74 

### Exhibit 6

- 15

. Daily Mean and Percentile Per Capita Total Food Intake for Children and Adults
Lifestage (years) Percent of Group

Consumin g Food Mean 50th 90 th 95 th 99 th

Total Food Intake (g/day, as consumed)

Child < 1 a 67.0%

- 99.7% h 322 270 599 779 1152

Child 1

- 2 b 100% 1,032 996 1537 1703 2143

Child 3

- 5 c 100% 1,066 1,020 1,548 1,746 2,168

Child 6

- 11 d 100% 1,118 1,052 1,642 1,825 2,218

Child 12

- 19 e 100% 1,197 1,093 1,872 2,231 2,975
Adult f 100% 1,100 1,034 1,738 2,002 2,736 Total Food Intake (g/kg

- day, as consumed)

Child < 1 a 67.0%

- 99.7% h 39 34 72 95 147

Child 1

- 2 b 100% 82 79 125 144 177

Child 3

- 5 c 100% 61 57 91 102 1 32

Child 6

- 11 d 100% 40 38 61 70 88

Child 12

- 19 e 100% 21 19 34 40 51
Adult g 100% 14.8 13.9 23.7 27.6 35.5 Sources: EPA 2005e, 2008a

a These values represent a time

- weighted average for age groups birth to <1 month (N=88), 1 to <3 months (N=245), 3 t o <6 months (N=411), and 6 to <12 months (N=678) from Table 14

- 3 of the 2008 CSEFH

. b These values represent a time

- weighted average for age groups 1 to <2 years (N=1,002) and 2 to <3 years (N=994) from Table 14

- 3 of the 2008 CSEFH

. c These values were o btained from Table 14

- 3 of the 2008 CSEFH (age group 3 to <6 years, N=4,112).
d These values were o btained from Table 14

- 3 of the 2008 CSEFH (age group 6 to <11 years, N=1,553)

. These values r epresents a conservative (i.e., slightly low) estimate for ag es 6 through 11 years since 11

- year olds are not included in this CSEFH age group.

e These values represent a time

- weighted average for age groups 11 to <16 years (N=975) and 16 to <21 (N=743) years from Table 14

- 3 of the 2008 CSEFH

. Note that estimated v alues include 11

- year

- olds and individuals through age 20, which contributes to uncertainty in the estimates.
f These values represent a time

- weighted average for age groups 20 to 39 years (N=2,950) and 40 to 69 years (N=4,818) from Table 5B of the 2005 EP A analysis of CSFII

. g These values represent a time

- weighted average for age groups 20 to 39 years (N=2,950) and 40 to 69 years (N=4,818) from Table 5A of the 2005 EPA analysis of CSFII

. h Percents consuming foods from Table 14

- 3 of the 2008 CSEFH inc lude: 67.0% (birth to <1 month); 74.7% (1 to <3 months); 93.7% (3 to <6 months); and 99.7% (6 to <12 months)

. Infants under the age of 1 that consume breast milk are classified as “non

- con s umers” of food.


### 6.4 Other Exposure Factor Values
The other exposure parameters included in the MIRC algorithms are exposure frequency (Section 6.4.1), fraction of the food type obtained from the contaminated area (Section 6.4.2), and reduction in the weight of the food types during preparation and cooking (Section 6.4.3)

. For the breast milk ingestion pathway, additional exposure parameters are included in the FFC algorithms (Section 6.5)

.

6.4.1 Exposure Frequency The exposure frequency (EF) represents the number of days per year that an individual consumes home-produced food items that are contaminated with the chemical being evaluated. In MIRC, the default value for EF is 365 days/year for all exposure sources and all potentialAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 75 

### receptors. This assumption is consistent with the food ingestion rates used in MIRC (i.e., daily intake rates equivalent to annual totals divided by 365 days) and does not imply that residents necessarily consume home-produced food products every day of the year.

If the user wishes to evaluate daily intake rates based on shorter averaging times, the user can overwrite both the food-specific ingestion rates and the EF for each home-grown food product. Users of MIRC might want to specify a lower EF values for various food types where residents obtain some of their diet from commercial sources and where consumption of home grown produce is seasonal.

6.4.2 Fraction Contaminated The fraction contaminated (FC) represents the fraction of each food product consumed that is contaminated by the chemical at a level consistent with environmental concentrations in the area of concern (e.g., area with maximum deposition rates). Obviously, the most conservative assumption is that all food products consumed (i.e., 100 percent) are from the location represented by the chemical concentrations input into MIRC

. For non-infant children and the adult age cohorts, MIRC includes the default FC of 1, assuming that 100 percent of the food product consumed is produced by households that farm, garden, or raise animals

. The user can vary this default FC value for individual food products to tailor the assessment to a particular exposure scenario

.

6.4.3 Preparation and Cooking Losses Food preparation and cooking loss es are included in the FFC exposure calculations to account for the amount of a food product as brought into the home that is not ingested due to loss durin g preparation, cooking, or post-cooking. These losses need to be accounted for in the ADD equations because the food ingestion rates calculated from the USDA 1987 to 1988 NFCS are based on the weight of home grown produce and animal products brought from the field into the house prior to any type of preparation. Not all of the produce or products were eventually ingested. In general, some parts of the produce and products are discarded during preparation while other parts might not be consumed even after cooking (e.g., bones)

. Thus, the actual food ingested is generally less than the amount brought into the home.

Three distinct types of preparation and cooking losses are included in the ingestion exposure algorithms in MIRC: (1) loss of parts of the food type from paring (i.e., removing the skin from vegetables and fruits) or other types of preparation (e.g., removing pits, coring, deboning), (2) additional loss of weight for the food type during cooking (e.g., evaporation of water), and (3) post-cooking losses (e.g., non-consumption of bones, draining cooking liquid [e.g., spinach]). MIRC includes mean values for these three types of preparation and cooking loss es for exposed fruit, protected fruit, exposed vegetables, protected vegetables, root vegetables, beef, pork, poultry, and fish. Different types of losses apply to different types of foods. Therefore, the losses can be represented by only two parameters, L1 and L2 , the definitions of which vary according to the food type as explained in the endnotes in Exhibit 6- 16 . All preparation and cooking loss parameter values were estimated as specified in the Exhibit’s endnotes from data presented in Chapter 13 of the EPA’s 1997 EFH.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 76 

### Exhibit 6

- 16

. Fraction Weight Losses from Preparation of Various Foods

Product Mean Cooking, Paring, or Preparation Loss (Cooking Loss Type 1 [L1])

(unitless) a Mean Net Post Cooking (Cooking Loss Type 2 [L2])

( unitless) b

Exposed Fruit c 0.244 0.305 Exposed Vegetable 0.162 d NA
Protected Fruit 0.29 e NA Protected Vegetable 0.088 f NA Root Vegetable g 0.075 0.22 Beef 0.27 0.24
Pork 0.28 0.36 Poultry 0.32 0.295 h

Fish i 0.0 0.0 or 1.5 j

Source: EPA 1997 a (Chapter 13; Tables 13

- 5 [meats], 13

- 6 [fruits], and 13

- 7 [vegetables]) NA = Not Available

a For fruits , includes losses from draining cooked forms

. For vegetables , includes losses due to paring, trimming, flowering the stalk, thawing, draining, scraping , shelling, slicing, husking, chopping, and dicing and gains from the addition of water, fat, or other ingredients

. For meats , includes dripping and volatile losses during cooking.
b For fruits , includes losses from removal of skin or peel, core or pit, s tems or caps, seeds and defects; may also include losses from removal of drained liquids from canned or frozen forms

. For vegetables , includes losses from draining or removal of skin

. For meats , includes losses from cutting, shrinkage, excess fat, bones, scraps, and juices.

c These values represent average s of means for all fruits with available data (except oranges) (Table 13

- 6).
d This value r epresents an average of means for all exposed vegetables with available data (Table 13

- 7)

. Exposed vegetables i nclude asparagus, broccoli, cabbage, cucumber, lettuce, okra, peppers, snap beans, and tomatoes.

e This value was set equal to the v alue for oranges (Table 13

- 6).
f This value r epresents an average of means for all protected vegetables with available data (Table 13

- 7)

. Protected vegetables include pumpkin, corn, peas, and lima beans.
g These values r ep resent average s of means for all root vegetables with available data (Table 13

- 7)

. Root vegetables include beets, carrots, onions, and potatoes.
h This valu e r epresents an average of means for chicken and turkey (Table 13

- 5).
i If the user changes fish ingestion rates to match a survey of the whole weight of fish brought into the home from the field (divided by the consumers of the fish), an appropriate value for L1 would be 0.3 ( EPA 1997a, Table 13

- 5)

. For volatile or water soluble chemicals, a non

- zero value for L2 also may be appropriate

. Although EPA (1997a) recommended 0.11 for L2, it varies substantially by chemical.
J Cooking loss accounts for the dif ference between ingestion rates for cooked fish and calculated Hg concentrations in whole fish. Cooking fish tends to re duce the overall weight of fish, and volatilization of mercury is unlikely to occur during cooking, increasing the concentration of mer cury by a factor of roughly 1.5 (Morgan, Berry, and Graves, 1997) 4



### There are substantial uncertainties associated with the L1 and L2 parameters, including the wide variation in values across produce types that were averaged together to recommend a central tendency value for each. For example, the L2 factor does not distinguish between weight loss during cooking by water evaporation, which might leave the chemical in the fruit, and pouring the cooking liquid down the drain (chemical lost) or using the liquid to create a sauce (chemical not lost). In addition, the concentration of chemical might be highest in the skin, which often is discarded, and lower in the consumed portion of many bulky fruits and vegetables. Finally, the data EPA used to evaluate L1 included negative losses (i.e., weight

4 Morgan, J.N., M.R. Berry, and R.L. Graves. 1997. “Effects of Commonly Used Cooking Practices on Total Mercury Concentration in Fish and Their Impact on Exposure Assessments.” Journal of Exposure Analysis and Environmental Epidemiology 7(1):119- 133.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 77 

### gains) due to hydration of dried vegetables (e.g., peas and lima beans), which increases the range of L1 values across different vegetables.

Note that the default L1 and L2 values for fish are set to zero with the exception of methyl
mercury. That is because the data source for the fish ingestion rates is not the USDA’s 1987 to 1988 NFCS (USDA 1993, 1994) as reported in EPA’s EFH , which reported food as brought into the home, as is the case for the other food categories. Instead, the fish IR data included in MIRC are from a more recent and larger survey, EPA’s (2002) analysis of freshwater and estuarine fish consumption from the USDA’s 1994 -96 and 1998 CSFII

. That survey reports ingestion rates of fish parts actually consumed, and so no loss processes for preparation are needed . The zero value for L2 assumes that no chemical is lost by volatilization and that pan juices are consumed. The user may reset that value where chemical-specific data are available

. In the case of methyl mercury, the chemical is not lost by volatilization during cooking, but liquid from the fish is lost. This lowers the mass of fish consumed, thereby increasing the methyl mercury concentration. As such, L2 is set at 1.5 as detailed by Burger et al (2010)

. 5 

### (Note that due to uncertainties associated with the cooking conversion factor of 1.5 for methyl mercury, it was not used in the multipathway screening assessment. However, this is an area that should be investigated further for potential use in the future.)

If the user manually changes fish ingestion rates to match a local survey of the whole weight of fish brought into the home from the field (divided by number of persons consuming the fish), the user should also set the L1 and L2 parameter to non-zero values

. An appropriate value for L1 would be 0.3 ( EPA 1997 a, Table 13- 5) . For volatile or water soluble chemicals, a non-zero value for L2 also may be appropriate. Although EPA recommended 0.11 for L2 ( EPA 1997a, Table 13-5), it varies substantially by chemical

. 

### 6.5 Breast-Milk Infant Exposure Pathway Parameter Values
Values used for parameters in the breast-milk exposure pathway algorithms (Section 3.4) can be scenario-specific, receptor-specific, and/or chemical-specific and might be empirically derived or estimated by an appropriate model. For parameters that are scenario-specific or for which empirical values are required, the default values provided in MIRC are listed. For parameters for which MIRC calculates values, the appropriate equation is listed. Scenario- and receptor-specific parameters are discussed in Section 6.5.1 and chemical-specific parameters are discussed in Section 6.5.2.

6.5.1 Receptor-specific Parameters Receptor-specific values are needed for parameters that describe the characteristics or activities of the exposed individual

. In this context, there are two relevant receptors: the mother and the infant. Exhibit 6- 17 lists the parameters and their default values. The text that follows describes the input value or value options for each exposure parameter required by MIRC to calculate the infant absorbed chemical intake rate, or DAI inf 

### . For parameter values that can be estimated when empirical values are not available, see the equation description in Section 3.4.

5 Burger J. 2010. Daily consumption of wild fish and game: Exposures of high end recreationalists. Environmental Health Research 12(4): 343-354.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 78 

### Exhibit 6

- 17

. Scenario

- and Receptor

- Specific Input Parameter Values Used to

Estimate Infant Exposures via Breast Mil k

Parameter Description Default Value

AT Averaging time for inf ant’s exposure via breast milk, i.e., duration of

nursing (days) =ED

BW inf Body weight of infant (kg) averaged over duration of nursing exposure 7.8

BW mat Body weight of mother (kg) averaged over duration of mother’s

exposure 66

DAI mat Daily absorbed in take of chemical by mother (mg/kg

- day) Equation 3

- 36

ED Exposure duration for infant, i.e., duration of breast feeding (days) =AT
AT/ED Averaging time divided by exposure duration 1.0
f bp Fraction of mother’s whole blood that is plasma (unitless) 0.65
f fm Fraction of mother’s body weight that is fat (unitless) 0.30
f mbm Fraction of fat in mother’s breast milk (unitless) 0.04
f pm Fraction of mother’s body weight that is plasma (unitless) 0.046

IR milk Mean infant milk ingestion rate over duration of n ursing (kg/day) 0.709

t bf Duration of breast feeding (days) 365

t pn Duration of maternal chemical exposure prior to nursing (days) 3285



### Averaging time ( AT

) and exposure duration ( ED ). AT refers to the time over which the infant’s exposure to the chemical of concern is averaged. ED refers to the duration of the infant’s
exposure

. For the exposure scenario considered for this age group, both AT and ED equal the duration of the nursing period, and they therefore cancel each other out in the infant average daily dose equation.

Infant body weight ( BW inf 

### ). The user selects a value for BW inf 

### , the time-weighted average body weight of the infant over the entire duration of breast feeding, based on the age at which the infant stops breast feeding. For example, if the infant breast feeds for one year, the user should select the body weight for an infant that is averaged from birth to the first birthday

. Similarly, if an infant breast feeds for 6 months, the user should select the body weight for an infant that is averaged from birth to six months. Because the default breast feeding duration ( t bf 

### ) is one year (i.e., 365 days), the default infant body weight is 7.8 kg, which is the time-weighted average for the mean infant body weight between birth and its first birthday from EPA’s (2008) Child Specific Exposure Factors Handbook (CSEFH; EPA 2008 a). Exhibit 6- 18 presents additional values for the infant body weight parameter that the user can select instead of the MIRC default.

Exhib it 6

- 18

. Average Body Weight for Infants

Statistic 0 to < 6 months

(kg) 0 to < 12 months

(kg) 0 to < 18 months (kg) 0 to < 24 months

(kg)

Mean 6.5 7.8 a 9.0 9.6

5 th percentile 5.0 6.0 7.0 7.5
10 th perce ntile 5.3 6.4 7.4 7.8
15 th percentile 5.5 6.7 7.7 8.2
25 th percentile 5.8 7.0 8.1 8.7
50 th percentile 6.4 7.8 8.9 9.5Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 79 

### Exhib it 6

- 18

. Average Body Weight for Infants

Statistic 0 to < 6 months

(kg) 0 to < 12 months

(kg) 0 to < 18 months (kg) 0 to < 24 months

(kg)

Mean 6.5 7.8 a 9.0 9.6

75 th percentile 7.1 8.6 9.9 10.5
85 th percentile 7.4 9.0 10.3 11.0
90 th percentile 7.7 9.2 10.6 11.3
95 th percentile 8.0 9.7 11.1 1 1.8

Source: EPA 2008a; each value is the time

- weighted average from the data summaries presented in the CSEFH, Table 8

- 3.

a MIRC default



### Maternal body weight ( BW mat 

### ). This parameter represents the body weight of the mother averaged over the entire dura tion of the mother’s exposure to the chemical of concern . The maternal body weight is needed to calculate the biological elimination constant for the lipophilic chemical in lactating women ( k fat_elac 

### )

. MIRC assumes that the mother will be pregnant for 9 months (i.e., 0.75 year) and will be lactating for 1 year

. The MIRC default maternal body weight also assumes that the mother has been exposed for 10 years total. For 8.25 years, she is not pregnant or lactating, for 0.75 year she is pregnant, and for 1 year she is lactating. The MIRC default BW

mat 

### of 66 kg is based on CSFII data compiled by EPA for non-lactating and nonpregnant women between the ages of 15 and 44 (i.e., women of child-bearing age), lactating women, and pregnant women ( EPA 2004b)

. Exhibit 6- 19 presents additional values for the maternal body weight parameter which the user may choose to use instead of the MIRC default. The BW

mat 

### value is not the value that MIRC uses to estimate the mother’s absorbed daily inta ke ( DAI mat 

### )

. The daily ingestion rates for home-grown/raised food products in MIRC are for men and women combined, with the rates normalized to body weight. The ingestion rates for soil, water, and fish included in MIRC are not normalized to body weight but are based on both men and women. For those ingestion rates, MIRC uses an average body weight value for males and females to estimate the average daily dose (intake) of the chemical in mg/kg- day

. These values are subject to the assumption that the body-weight normalized ingestion rates and resulting ADD values are applicable to nursing mothers.

Exhibit 6- 19

. Time-weighted Average Body Weight for Mothers

Statistic Weight (kg)
Mean 66.0 a
5 th 47.1 10 th 50.2 25 th 54.3 50 th 62.0 75 th 72.0 90 th 85.7 95 th 97.0
Source: EPA 2004b

a MIRC default value



### Exposure duration ( ED ). See discussion of AT and ED above.

Fraction of mother’s whole blood that is plasma ( f bp 

### ). Steinbeck (1954) reported that plasma volume accounts for approximately 60 percent of the total blood volume in non-lactating humanAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 80 

### females ( EPA

1998). Harrison (1967) and Ueland (1976) reported plasma volumes between 63 to 70 percent in postpartum women ( EPA 1998) . The default value in MIRC of 65 percent (0.65 ) is the value recommended by EPA in its Methodology for Assessing Health Risks Associated with Multiple Pathways of Exposure to Combustor Emissions (MPE, EPA

1998).

Fraction of mother’s body weight that is fat ( f fm 

### ). A limitation of using a steady-state, instead of a dynamic partitioning, model for lactational transfer of chemicals is that several key parameters change over the course of exposure

. For example, Equation 3-38, used to estimate the concentration of a lipophilic chemical in breast milk fat, assumes that the mother’s body fat will remain constant over the entire duration of breast feeding (t bf 

### ), which is unlikely to be true ( EPA 2001 a). Another limitation of the single analytic model is that chemical transfer rates from bl ood to milk are unlikely to be the same as the rate of mobilization of the chemical from fat stores to the blood ( EPA 2001 a). Studies cited in ATSDR’s toxicological profile for chlorinated dibenzo -pdioxins show a correlation between percent body fat and the elimination rate of dioxins, with longer half-lives for dioxins in individuals with a higher proportion of fat in their bodies (ATSDR 1998) . In the context of a screening model, however, EPA recommends a default value for the fraction of a mother’s bo dy comprised of fat of 0.3 based on data and discussions presented by Smith (1987) and Sullivan et al

. (1991) ( EPA

1998). A fraction of 0.3 indicates that 30 percent of the mother’s body weight is fat, which is a conservative value ( EPA 2001a). To establish a conservative screening scenario, the MIRC default value for f fm 

### is 0.30

. Fraction of fat in mother’s breast milk ( f mbm 

### ). The C

milkfat 

### model (Equation 3-38) assumes that a constant fraction of breast milk is fat, even though there is evidence that indicates variation in the fat content of breast milk throughout lactation (Sim and McNeil 1992)

. Different studies suggest a fat content of breast milk in humans of between 1 and 5 percent (Jensen 1987, Schecter et al

. 1994, Hong et al

. 1994, McLachlan 1993, Bates et al

. 1994, NAS 1991, Butte et al

. 1984, Maxwell and Burmaster 1993, EPA 1997a, Smith 1987, Sullivan et al

. 1991) . The MIRC default value for f mbm 

### of 0.04 (i.e., 4 percent) is the value EPA recommended for MPE ( EPA 1998)

. Fraction of maternal weight that is plasma ( f pm 

### )

. Altmann and Dittmer (1964) estimated that plasma volume for adult women ranged from 37 to 60 mL/kg of body weight and averaged about 45 mL/kg. Ueland (1976) observed that the average plasma volume of women 6 weeks postpartum was 45 mL/kg of body weight. Using a value of 1.026 for the specific gravity of plasma from Conley (1974), EPA estimated a value of 0.046 for the fraction of maternal weight that is plasma ( EPA

1998). The MIRC default for f pm 

### therefore is 0.046.

Infant breast milk ingestion rate ( IR milk 

### ) . Milk ingestion rates vary with several factors, including the age and size of the infant and use of other foods such as formula. Based on its review of a several studies, EPA recommended time-weighted average and upper percentile milk ingestion rates for infants that nurse for six and for twelve months ( EPA 1997a, Chapter 14, Table 14-15). To estimate an “average” value, EPA first estimated study -sample-size weighted average values for 1, 3, 6, 9, and 12 months of age and then developed time-weighted average milk ingestion rates from those ( EPA 1997a). EPA estimated an upper percentile (upper bound) value as the mean plus two standard deviations. MIRC converts the ingestion rates measured volumetrically (mL/day) to ma ss -based estimates (kg/day) assuming the density of human milk to be 1.03 g/mL (reported by NAS 1991 and recommended by EPA 1997a). The resulting values are shown in the first two rows of Exhibit 6- 20 . The MIRC screening-level default of 980 mL/day is an upper-bound estimate based on a one-year nursing period.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 81 

### Exhibit 6- 20 also includes the recommended values for four non-overlapping age categories from the CSEFH ( EPA

2008, Table 15- 1) . The values demonstrate that although infants grow substantially from birth to one year of age, the “upper bound” estimates of their milk ingestion rates are very close to 1 liter per day at all stages of development in the first year.

Exhibit 6

- 20

. Infant Breast Milk Intake Rates

Age Category Average

(mL/d) Average

(kg/d) “Upper Bound”

(mL/d) “Upper

Bound” (kg/d) Reference

1 to 6 months 742 0.764 1,033 1.064 EPA 1997a †

0 to < 12 months 688 0.709 980 a 1.01 a EPA 1997a †

0 to < 1 month 510 0.525 950 0.979 EPA 2008 ††

1 to < 3 months 690 0.711 980 1.01 EPA 2008 †

3 to < 6 months 770 0.793 1,000 1.03 EPA 2008 †

6 to < 12 months 620 0.639 1,000 1.03 EPA 2008 †

a MIRC default ; † Based on review of multiple studies ; †† Based on a single study



### Duration of breast feeding ( t bf 

### ). This parameter is equal to the infant’s exposure duration ( ED ) and the infant’s averaging time ( AT ). In its MPE Methodology, EPA asserts a conservative value for the duration of breast feeding of 1 year (i.e., 365 days) and a central tendency estimate of 6 months (180 days) ( EPA 1998). Reviewers of MPE noted that 365 days may be overly conservative, given than only 20 percent of infants are breast fed for 6 months, at which point alternative foods are introduced, at least in addition to breast milk (EPA 2001 a). Nonetheless, to establish a conservative screening scenario, the MIRC default for t bf 

### is 365 days.

Duration of the mother’s exposure to the chemical of concern prior to nursing ( t pn 

### ). The model shown as Equation 3-38 includes this parameter to reduce the over-estimate of chemical concentration in milk fat that occurs if the model is applied to a chemical with a long biological half-life (e.g., many years). The factor is needed for applications of the model to scenarios with a brief exposure duration (e.g., beginning a few months prior to the start of nursing) relative to the chemical half life. As the duration of an exposure scenario increases to meet and exceed the chemical half life, however, the overestimate that occurs without this parameter is reduced. For example, assume a chemical biological half-life of 8 years and a nursing period of 1 year. If exposure of the mother starts at the beginning of nursing, using Equation 3-38 without the t pn 

### term results in an over-estimate of the concentration of the chemical in breast milk by a factor of 28.1 compared with the prediction using Equation 3-38 with the t pn 

### term ( EPA

1998, Table 9- 6)

. However, at longer pre-natal exposures of the mother, the magnitude of the over-estimate is reduced: for a 10-year exposure, the magnitude of the overestimate without the t pn 

### term is 2.28, and for a 30-year exposure, the overestimate is reduced to 1.39.

For purposes of the screening-level of assessment for di oxins, we assume an exposure duration equal to the half-life of the chemical, or 10 years. Only 3285 days of that period are pre-natal (i.e., 3650 minus 365 days, assuming 1 year lactation period). Although longer exposure periods are possible for the screening scenario, there is sufficient uncertainty in the model to merit accepting a conservative bias for this parameter value

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 82 

### 6.5.2 Chemical-Specific Parameter Values The chemical-specific parameters in the breast-milk pathway in MIRC are listed in Exhibit 6- 21

. Note that the parameters for which values are needed are different for the lipophilic chemicals (i.e., dioxins), for which lactational transfer is assumed to occur via milk fat, and inorganic chemicals, for which the transfer is assumed to occur via the aqueous phase of breast milk (i.e., mercury).

Absorption efficiency of the chemical by the oral route of exposure for the infant ( AE inf 

### ). The models included in MIRC assume that the AE inf 

### from the lipid phase of breast milk is equal to the AE inf 

### from the aqueous phase of the milk

. Reviewers of the model stated that this assumption may not be valid and that ideally, the equation DAI inf 

### would include variables for the AE inf 

### from the breast milk fat and the AE inf 

### from the aqueous phase of breast milk (EPA 2001 a). However, since the MIRC assumption is that chemicals will partition to either the lipid or aqueous phase of milk, it is not necessary at this time to have multiple AE inf 

### values for a given chemical. If data on the AE from the mother or an adult but not for the infant are available, data for the adult may be used for AE

inf 

### . Reviewers also recommended that chemical-specific values come from studies that account for absorption of the chemical from milk, because absorption from other matrices (e.g., solid foods) may not be relevant ( EPA 2001a). If chemical-specific data are not available for adults or infants, a conservative default value for AE inf 

### for a screening level assessment is 1.0, which assumes 100 percent absorption ( EPA 1998)

.
The default value for AE inf 

### in MIRC for both MeHg and dioxin is 1.0. For ingested lipophilic chemicals, it is reasonable to assume that absorption will be high ( EPA 2004c). ATSDR (1998) reported that dioxins are well absorbed by the oral route of exposure, with one human experiment indicating more than 86 percent absorption. It is EPA policy to assume 100 percent absorption for chemicals with reported AEs of 50 percent or higher ( EPA 2004c). MeHg also is well absorbed, with measured values as high as 95 percent, and so a value of 100 percent is used in MIRC ( EPA

2001b).

Exhibit 6- 21

. Chemical-specific Input Parameter Values for Breast Milk Exposure Pathway

Parameter and Description 2,3,7 ,8

- TCDD MeHg

AE inf Infant absorption efficiency of the chemical by the oral route of exposure (i.e., fraction of ingested chemical that is absorbed by the infant; unitless) 1.0 (default) 1.0 (default)

AE mat Maternal absorption efficiency of the chemical by the oral route of exposure (i.e., fraction of ingested chemical that is absorbed by the mother; unitless) 1.0 (default) 1.0 (default)

f bl Fraction of steady

- state total body burden of

hydrophilic chemical in mother that is in the mother’s whole blood compartment (unitless) NA 0.059 (Kershaw et al

. 1980) a

f f Fraction of steady

- state lipophilic chemical body

burden in mother that is stored in body fat (unitless) ≥ 0.90 (ATSDR 1992) NA

f pl Fraction of steady

- state total hydrophilic chemical

body burden in mother that is in the blood plasma compartment (unitless) NA Not yet identified b

h Biological half

- life for chemical in non

- lactating

women (days) 3650 ( EPA 19 94c) 50 (Sherlock et al

.

1984)



### k aq_elac Rate constant for total elimination of hydrophilic

chemicals by lactating women (per day) NA = 

### k elim

k elim Rate constant for elimination of chemical for non

lactating women (per day; related to chemical half

1.9E

- 04 b 1.4E

- 02 cAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 83 life)

k fat_elac Rate constant for total elimination of lipophilic

chemicals by lactating women (per day) Est

. using Equation 3

- 41 NA

Pc bm Partition coefficient for hydrophilic chemical between maternal blood plasma and aqueous phase of brea st milk (g milk/g plasma; model assumption) NA 1.0 (model assumption)

Pc RBC Partition coefficient for hydrophilic or protein

bound chemical between red blood cells (RBC) and plasma in maternal blood (mL whole blood/mL RBC) NA 40 (Hollins et al

. 1975)

NA = not applicable

. ND = not yet determined from literature

. a This value is based on a single

- dose study and may not be appropriate for a chronic exposure model.
b An empirical value for this variable is currently missing for application of model.
d Th is value was calculated from biological half

- life ( h ) using Equation 3

- 40

.



### Note that AE

values for some inorganic compounds are substantially less than 1.0. For cadmium, for example, AEs for adults of 0.025 to 0.05 have been reported ( EPA 2004c, Exhibit B- 4)

. Absorption efficiency of the chemical by the oral route of exposure for the mother ( AE mat 

### ) . The default value for both dioxins and MeHg is 1.0, as described in the previous paragraph.

Fraction of total maternal chemical body burden that is in the whole blood ( f bl 

### ). The default value fo r MeHg in MIRC, 0.059, is from Kershaw et al

. (1980), which reported kinetics of blood deposition and clearance of MeHg in humans. Individuals consumed one meal of fish that contained between 18 and 22 μg Hg/kg body weight. The fraction of the dose deposited in the blood volume after mercury was fully distributed in tissues was 5.9 percent or 0.059. This study used a single-dose and thus may not be appropriate for a chronic exposure analysis.

Fraction of total maternal chemical body burden that is in body fat ( f f 

### ). Based on ATSDR’s Toxicological Profile for Selected PCBs (ATSDR 1992) and Sullivan et al

. (1991), EPA concluded that the “fraction of ingested contaminant stored in fat may be >90%” for lipophilic chemicals such as PCBs and dioxins ( EPA 1998) . This statement was interpreted to mean that 90 percent of the maternal body burden of chemical at “steady state” is located in body fat for dioxins at steady state

. Fraction of total maternal chemical body burden that is in blood plasma ( f pl 

### ). For hydrophilic chemicals, this parameter represents the steady-state fraction of the total chemical in the body that is circulating in the blood plasma. Values for f pl 

### may be available for some chemicals in the scientific literature. No value for this parameter for methyl mercury has been identified from the literature at this time. A value can be calculated using Equation 3-43. However, this equation requires a reliable value for f bl 

### , and the value found for mercury may not be appropriate for a chronic exposure analysis (see above).

Chemical half-life in non-lactating women ( h ) . In general, highly lipophilic chemicals tend to have relatively long biological half-lives

. EPA estimates that the half-life for dioxins is between 7 and 10 years ( EPA

1994a). ATSDR estimates that the half-life for 2,3,7,8-TCDD in particular may be as long as 12 years (ATSDR 1998). To establish a conservative screening scenario, the MIRC default half-life for dioxins is set to 10 years or 3650 days.

The half-life for methylmercury is on the order of weeks, not years. Greenwood et al

. (1978) measured blood clearance rates for MeHg in lactating Iraqi women exposed accidentally toAttachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 84 

### MeHg via bread prepared from wheat treated with a fungicide that contained MeHg. The data indicated a mean half-life for MeHg of approximately 42 days

. Sherlock et al

. (1984) reported

an average measured half-life for MeHg of 50 days with a range of 42-70 days

. The MIRC default for MeHg is set to the longer average half life of 50 days.

Chemical elimination rate constant for lactating women

– aqueous ( k

aq_elac 

### ). The parameter k aq_elac 

### is equal to k

elim 

### plus the loss rate for the chemical in the aqueous phase of breast-milk during lactation. EPA has yet to propose a term for the additional elimination of a chemical in the aqueous phase of milk from breast feeding. In the absence of empirical values, a reasonable assumption for water soluble chemicals is that k aq_elac 

### is equal to k

elim 

### as discussed for Equation 3- 43 . The extent to which k elim 

### is an underestimate of k aq_elac 

### for a given chemical will determine the extent of conservative bias in k aq_elac



### . Chemical elimination rate constant for non-lactating women ( k elim 

### ). Although values for this parameter often are reported directly in the literature, MIRC estimates k elim

### from chemical halflife assuming first-order kinetics as shown in Equation 3- 40 . For example, for a biological halflife of 3,650 days for dioxins, k elim 

### is estimated to be 1.9E-04 per day. Assuming a biological half-life of 50 days for MeHg, the value for k elim 

### is estimated to be 0.014 per day.

Rate constant for total elimination of lipophilic chemicals by lactating women ( k fat_elac 

### ). Although values for this parameter might be found in the scientific literature for some chemicals, in MIRC

, k fat_elac 

### for dioxins is calculated from Equation 3- 41 . When the parameters in that equation are set to the default values in MIRC for dioxins, MIRC estimates a value of 0.0015 per day for k fat_elac



### . Partition coefficient for chemical between maternal blood plasma and aqueous phase of breast milk ( Pc

bm 

### ). The aqueous model, presented in Equation 3-42, assumes that the concentrations in the plasma and aqueous phase of breast milk are directly proportional ( EPA 1998)

. Therefore, the default value for this parameter for MeHg in MIRC is 1.0.

Partition coefficient for chemical between red blood cells and plasma in maternal blood ( Pc RBC 

### ). Chemical-specific values for this parameter should be located in the scientific literature. If chemical-specific values are unavailable and it is assumed that there is equal distribution of the chemical in the plasma and red blood cells, EPA suggests a default value of 1.0 ( EPA 1998)

. F or MeHg, MIRC includes a value of 40 based on Hollins et al

. (1975) study of cats exposed to MeHg, which reported a ratio of radio-labeled mercury in red blood cells to plasma of 97.7 to 2.3 (i.e., ratio of 42.5).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 85 

## 7 Summary of MIRC Default Exposure Parameter Settings

T he default settings included in MIRC are intended to be characteristic of a conservative (but plausible) exposure scenario that results in a negligible or extremely low chance of underestimating risk to farming households in an area with chemical concentrations and air deposition rates as specified by the user. These default parameter values were used to derive the screening threshold emission rates used for screening emissions of PB-HAPs from sources included in RTR risk assessments. These values are the default, or initial setting, for parameter values in MIRC as described in Section 6. This section summarizes the default parameter values used to calculate screening thresholds.

This chapter is organized to present the chemical- and scenario-specific inputs to MIRC by data type

. The screening-level analysis uses 90 th 

### percentile ingestion rates, presented in Section 7.1, and population-specific characteristic assumptions, presented in Section 7.2, that are generally conservative in nature. Screening thresholds were derived for five RTR chemical species: benzo(a)pyrene, cadmium, mercuric chloride, methyl mercury, and 2,3,7,8-TCDD ; Section 7.3 presents chemical-specific parameter inputs for these five chemicals. Finally, Section 7.4 presents default parameter values for the nursing infant exposure scenario, which applied only to dioxin and methyl mercury.



### 7.1 Default Ingestion Rates
The screening-level (or default) values for ingestion rates for soil, fish, breast milk, and for each farm food type are equal to the 90th percentile of the distribution of national data for that ingestion medium ( Exhibit 7-1 ). The default settings also assume that all food types are obtained from the area of chemical deposition specified by the user (i.e., fraction of food from contaminated area = 1.0).

For estimates of screening threshold emission rates for PB-HAPS, environmental concentrations and air deposition rates were estimated using TRIM.FaTE for the area of maximal deposition in the vicinity of a hypothetical facility, and thus represent risks estimated for a maximally exposed individual/farm/family

.

Exhibit 7-1 also includes a sum of the 90 th 

### percentile ingestion rates for homegrown food categories and fish ingestion (preceding rows) to show the implied total food ingestion rate associated with setting multiple food-type-specific ingestion rates at a 90 th 

### percentile. Because the 90 th 

### percentiles for each farm food category are likely to reflect different individuals, it is likely that addition of multiple 90 th 

### percentile intake values will exceed the total food ingestion rates likely for the general population.

The final row in Exhibit 7-1 lists the likely magnitude of the overestimates by age category. The preceding row includes the 90 th 

### percentile of the distribution of individual total food ingestion rates from the USDA’s 1994 -96 and 1998 Continuing Survey of Food Intakes by Individuals (CSFII) (USDA 2000) data sets, as analyzed by EPA ( EPA 2005e) . The total ingestion rate for the farming households takes into account the cooking losses typical of each food category to provide a better comparison with the 90 th 

### percentile individual total food ingestion rates (which are based on consumption of prepared foods).Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 86 

### Exhibit 7

- 1

. Farm Food Category Ingestion Rates for Conservative Screening Scenario for Farming Households

Product 90 th Percentile Consumer Ingestion Rate

Units a

Infants < 1 yr Child

1

- 2 yrs Child

3

- 5
yrs Child 6

- 11
yrs Child

12

- 19
yrs Adult

Farm Food Item Beef NA 4.5 6.7 11.4 3.53 5.39 g/kg

- day Dairy c NA 148 82 54.7 27.0 34.9 g/kg

- day Eggs c NA 5.1 2.8 1.80 1.34 1.65 g/kg

- day Exposed Fruit NA 3.7 5.4 6.98 3.41 5 g/kg

- day Exposed Vegetable NA 10.7 3.5 3.22 2.35 6.01 g/kg

- day Pork c NA 4.5 4.4 3.04 2.65 3.08 g/kg

- day Poultry c NA 7.4 6.8 4.58 3.28 3.47 g/kg

- day Protected Fruit c NA 53 36 24.1 16.2 15.1 b g/kg

- day Protected Vegetable NA 3.9 2.5 2.14 1.85 3.55 g/kg

- day Root Vegetable NA 7. 3 4.3 3.83 2.26 3.11 g/kg

- day
Other
Breast milk d 1.01 NA NA NA NA NA kg/day Soil (dry) NA 400 e 400 e 201 f 201 f 201 f mg/day Water NA 654 834 980 1537 2224 mL/day Fish (per individual) g NA 3.24 4.79 6.9 8.95 17 g/day Fish (per kg BW) h NA 0.26 0.26 0.22 0.14 0.24 g/kg

- day Total Food Ingestion Rates for Comparison Only (not in MIRC; excludes soil and water)
Total Food: Homegrown only i NA 219 131 95 52 67 g/kg

- day

Total Food: All Sources j NA 125 91 61 34 23.7 g/kg

- day
Overestimate (ratio of Hom egrown/Total) k NA 1.8 1.4 1.6 1.5 2.8 (unitless)

Sources: EPA 1997a (Chapter 13), unless otherwise noted. NA = not applicable

a As indicated by the units, the ingestion rates for produce and animal products are already normalized to consumer body weight

. Ingestion rates for soil (mg/day) and water (mL/day) are not normalized to body weight

. Soil is reported as dry weight, water as volume, and the remaining values on a wet

- weight basis.
b This value r epresents a weighted average for the 20

- 39 and 40

- 69 age groups.

c For several farm food categories, ingestion rates were not available in EPA’s 1997 EFH or 2008 CSEFH ( EPA 1997a, 2008a)

. Ingestion rates for these child age categories were calculated using the methodology recommended in HHRAP ( EPA 2005a), S ection 6.2.2 .2, as described in Section 6.3.3 of this document

. Sources to develop these values included EPA 1997a and EPA 2003c

. d Infants are assumed to consume only breast milk for one year

. e This value r epresents an estimated “upper percentile” f or children ( EPA 1997a).
f These values represent soil ingestion rates for individuals who consume homegrown food products from Stanek et al

. 1997

. g 90 th percentile adult fish ingestion rates are based on data from 1995

- 1996 and 1998 CSFII as summarized in EPA 2002; child fish ingestion rates are based on the same survey data, but estimated by multiplying average two

- day consumption rate for children who consumed fish on one or both days of the survey by the frequency of fish consumption (i.e., proportio n of children that reported consuming fish out of all children sampled).
h F i sh ingestion rates, original data in g/day, have been normalized to body weight in this table to allow addition into total food estimate using the mean body weight for each age c ategory.
i Sum of 90 th percentile post

- cooking food ingestion rates . This estimate is calculated by multiplying the food ingestion rates on previous rows (excluding soil and water) by (1

- L 1 )x(1

- L 2 ), where L 1 and L 2 are the loss rates from Exhibit 6

- 16 . The rows are then summed to get the total post

- cooking ingestion rate. j 90 th percentile total food intake rates from EPA 2008a and 2005e based on CSFII data 1994

- 96 and 1998;

see Exhibit 6

- 15 of this docume nt.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 87 

### The final row of Exhibit 7-1 is the ratio of the two preceding rows. The magnitude of the overestimate that results from adding 90 th 

### percentile values for 10 different categories of homegrown foods for children is a factor of 1.8. The overestimate of the 90 th 

### percentile total food ingestion rate for adults is larger, a factor of 2.8. This bias may be considered when evaluating the cancer risks and noncancer hazard quotients estimated by MIRC.



### 7.2 Default Screening-Level Population -Specific Parameter Values
The screening-level values for body weights (BWs) for the RTR screening threshold analysis, which serve as the default values in MIRC, are mean values and are presented in Exhibit 7-2

. As stated in Section 6, EPA recommends using the mean BW for each age group when using upper (90 th 

### ) percentile values for medium ingestion rates. Use of the mean body weights introduces no bias toward over- or underestimating risk.

Exhibit 7

- 2

. Mean Body Weight Estimates for Adults and Childre n a
Lifestage (years) Duration (years) Mean Body Weight (kg)

Adult b (20

- 70) 50 71.4
Child < 1 c 1 7.83
Child 1

- 2 c 2 12.6
Child 3

- 5 d 3 18.6
Child 6

- 11 e 6 31.8
Child 12

- 19 f 8 64.2

a Source s : EPA 1997, 2008a

b These values were calculated from data presented in EPA ’s ( 1997 a) Exposure Factors Handbook

.
c These values were calculated as time

- weighted average body weight (BW) from data presented in Table 8

- 3 of EPA ’s (2008a ) Child

- Specific Exposure Factors Handbook (CSEFH)

. d These values were obtained directly f rom Table 8

- 3 of the 2008 CSEFH

.
e These values were o btained directly from Table 8

- 3 of the 2008 CSEFH for age group 6 to <11 years

. The values represents a sl ight under estimate of BW for ages 6 through 11 years

, since 11

- year olds are not included in this CSEFH
age group.

f These values were calculated as time

- weighted average BW for age groups 11 to <16 years and 16 to <21 years from Table 8

- 3 of the 2008 CSE FH

. The direction of the possible bias is unknown

. The values match the estimate based on Table 8

- 22 of the NHANES IV data as presented by Portier et al

. (2007).


### 7.3 Default Chemical-Specific Parameter Values for Screening Analysis

Exhibit 7-3 presents chemical-specific parameter values for input to MIRC for the screeninglevel analysis

. Values for reference dose (RfD), cancer slope factor (CSF), bioavailability when ingested in soil ( Bs ), mammalian metabolism factors ( MF ), correction factors for belowground produce ( VG rootveg 

### ), wet deposition fractions ( Fw ), air to plant transfer factors ( Bv AG 

### ), root concentration factors ( RCF ), and soil-water partition coefficient ( Kds ) are presented in Exhibit 7-3

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 88 

### Exhibit 7

- 3

. Chemical

- Specific Parameter Values for Input to MIRC a

Parameter Description Benzo( a )

- pyrene Cadmium Mercuric chloride Methyl

m ercury 2,3,7,8

-

TCDD Units

RfD Reference Dose for Chemical 0 0.00 05 0.0003 0.0001 1E

- 09 mg/kg

- day

C SF Oral carcinogenic potency slope factor

for chemical 10 0 0 0 150

, 000 mg/kg

- day

Bs Soil bioavailability factor for livestock 1 1 1 1 1 unitless

MF Mammalian metabolism factor 0.01 1 1 1 1 unitless

VG rootveg Empirical correction factor for

belowground produce, i.e., tuber or root vegetable, to account for possible overestimate of the transfer of chemicals from the outside to the inside of bulky tubers or roots (based on carrots and potatoes) 0.01 1 1 0.01 0.01 unitless

Fw Fraction of wet deposition that adheres

to plant surfaces; 0.2 for anions, 0.6 for cations and most organics 0.6 0.6 0.6 0.6 0.6 unitless

Bv AG Air

- to

- plant biotransfer factor for

aboveground produce for vapor

- phase chemical in air 124

, 742 0 1

, 800 0 6 5

, 500 [mg/g produce DW]
/ [mg/g air]

RCF Chemical

- specific root concentration

factor for tubers and root produce 9

, 684 0 0 0 39

, 999 L soil pore water/kg root WW

Kds Chemical

- specific soil/water partition

coefficient 160

, 000 75 58

, 000 7

, 000 38

, 904.51 L so il pore water/kg soil DW

a Values presented in this Exhibit are previously presented in Exhibit 4

- 1

, Exhibit 6

- 2

, Exhibit 6

- 3

, and E xhibit 6

- 5

. Howeve r, exact values used in the analysis are presented here, rather than values restricted by significant figures.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 89 

### Only single estimates were developed for each of these parameters for HHRAP ( EPA 2005a), and the potential direction and magnitude of bias toward over- or underestimating risks were not investigated in this analysis. The inputs that are both chemical-specific and plant-type-specific, as presented in Exhibit 6-3 , are not repeated here. Again, only single estimates weredeveloped for these parameters and the potential direction and magnitude of bias toward overor underestimating risks were not investigated. Finally, Exhibit 7-4 presents biotransfer factors for each of the chemicals and animal types assessed in the screening level assessment.

Exhibit 7

- 4

. Chemical and Animal

- Type Specific Biotransfer Factor (Ba) v alues for Input to MIRC ([mg chemical/kg WW tissue or dairy ] / [mg chemical intake/ day] = day/kg WW tissue or dairy)

Chemical Beef Dairy Pork Poultry Eggs

Benzo(a)pyrene 0.03756242 0.00790788 0.0454703 0.02767758 0.01581576
Cadmium 0.00012 0.0000065 0.00019149 0.10625 0.0025

Mercuric c hloride 0.000105 0.00000143 0.00003393 0.023925 0 .023925 Methyl m ercury 0.00124 0.0000169 0.00000507 0.003575 0.003575 2,3,7,8

- TCDD 0.02612123 0.00549921 0.03162044 0.01924722 0.01099841
Note: Exact values used in the analysis are presented here, rather than values restricted by significant figures.



### Sensitivity analyses were conducted to identify which, if any, of these parameter values significantly influence risk estimates from MIRC; results are presented elsewhere

. Further evaluation of the possible range and distribution of values can be conducted for any parameter that appears important to the model outputs.



### 7.4 Screening-Level Parameter Values for Nursing Infant Exposure
EPA also included an assessment of risk to nursing infants exposed to dioxins and to methylmercury (MeHg) in their mother’s milk for a family farming and catching fish in the area of maximal air deposition of chemical. Input values were summarized in Section 6.5.

7.4.1 Dioxins For dioxins, chemical intake via breast milk by nursing infants was estimated using the model presented in EP A’s Methodology for Assessing Health Risks Associated with Multiple Pathways of Exposure to Combustor Emissions (MPE, EPA 1998a) . The assumption that lactational transfer of dioxins to the infant occurs via the lipid-phase of milk appears reasonable

. The following screening-level assumptions used in that model should bias the results toward some overestimate of risks.

Duration of nursing is a full year and no other foods or liquids are consumed by the infant; a more “typical” value would be six months. Ab sorption efficiency of dioxin in food or milk by mother and infant are 100 percent; this assumption might overestimate absorption but probably by no more than 15 percent. The fat content of human milk is assumed to be 4 percent, a value toward the high end of the reported range of values (1 to 5 percent). The maternal chemical intake is estimated using 90 th 

### percentile ingestion rates for the different homegrown foods (see discussion for Exhibit 7-1 ); this assumption might overestimate total ingestion of homegrown foods by a factor of more than 3.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 90 

### If the fraction of the maternal body burden of dioxin that is in the body fat compartment is greater than 90 percent, as suggested by ATSDR (1998), then actual exposures of the infant may be less than estimated.

There also are parameter values and model assumptions for the lipid-phase breast-milk pathway for which possible bias is unknown.

The accuracy of the model is unknown; it has not been verified or validated with empirical data. Using a half-life of 10 years for dioxins may over- or under-estimate risks.

Finally, there is one assumption that might possibly introduce some bias toward underestimating risks. The model results are sensitive to the biological half-life of the chemical in the mother relative to the length of her exposure prior to the lactation period. Using an exposure duration for the mother equal to the assumed half-life for dioxins, 10 years, may underestimate the duration of exposure of the mother.

7.4.2 Methyl Mercury

For MeHg, empirical data from a single human study (Fujita and Takabatake 1977) was used in conjunction with a physiologically based pharmacokinetic (PBPK) model of lactational transfer of MeHg developed and partially validated by Byckowski and Lipscomb (2001) to support a very simple predictive model. Both the human data and the PBPK model indicated that for relatively low MeHg exposures, the concentration of MeHg in the nursing infant’s blood is similar to its concentration in the mother ’ s blood. The PBPK model suggested in addition that the average daily dose of MeHg absorbed from milk by the nursing infant ( DAI inf 

### ) is indistinguishable from the dose of MeHg absorbed by its mother from her food ( DAI mat 

### )

. The data are limited, and the model includes various assumptions; however, there is no known directional bias in the estimates.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 91 

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U.S. Environmental Protection Agency (EPA)

. 20 04c. Risk Assessment Guidance for Superfund. Volume I: Human Health Evaluation Manual (Part E, Supplemental Guidance for Dermal Risk Assessment), Final. Office of Superfund Remediation and Technology Innovation, Washington, D.C. EPA/540/R/99/005; OSWER 9285.7-02EP; NTIS PB99-963312. July.

U.S. Environmental Protection Agency (EPA)

. 2005a. Human Health Risk Assessment Protocol for Hazardous Waste Combustion Facilities. Office of Solid Waste and Emergency Response, Washington, DC. EPA- 530 -R- 05 -006. September. Available at: http://www.epa.gov/osw/hazard/tsd/td/combust/risk.htm

. U.S. Environmental Protection Agency (EPA). 2005b. Guidance on Selecting Age Groups for Monitoring and Assessing Childhood Exposures to Environmental Contaminants. Risk Assessment Forum. Washington, DC. November. EPA/630/P-03/003F. Available at: http://cfpub.epa.gov/ncea/cfm/recordisplay.cfm?deid=146583

. U.S. Environmental Protection Agency (EPA). 2005c. Guidelines for Carcinogen Risk Assessment. Risk Assessment Forum, Washington, DC. EPA/630/P-03/001F. March. Available from: http://www.epa.gov/IRIS/cancer032505-final.pdf

. U.S. Environmental Protection Agency (EPA)

. 2005d. Supplemental Guidance for Assessing Susceptibility from Early-Life Exposure to Carcinogens. Risk Assessment Forum: Washington, D.C. EPA-630/R- 03 -003F. March. Available at: http://www.epa.gov/ttn/atw/childrens_supplement_final.pdf

. U.S. Environmental Protection Agency (EPA). 2005e. Analysis of Total Food Intake and Composition of Individual's Diet Based on the U.S. Department of Agriculture's 1994-96, 1998 Continuing Survey of Food Intakes By Individuals (CSFII) (Final). Office of Research andDevelopment, National Center for Environmental Assessment, Washington, D.C. EPA/600/R05/062F. Available at: http://cfpub.epa.gov/ncea/cfm/recordisplay.cfm?deid=132173

. U.S. Environmental Protection Agency (EPA). 2007a. Prioritized Chronic Dose-Response Values for Screening Risk Assessments (Table 1). Office of Air Quality Planning and Standards; June 12, 2007. Available at: http://www.epa.gov/ttn/atw/toxsource/summary.html

. U.S. Environmental Protection Agency (EPA)

. 2007b. Toxicological Review of 1,1,1- Trichloroethane (CAS No. 71- 55 -6) In Support of Summary Information on the Integrated Risk Information System (IRIS). Office of Research and Development, Washington, DC. EPA/635/R-03/006. August. Available at: http://www.epa.gov/iris

U.S. Environmental Protection Agency (EPA)

. 2008a. Child-Specific Exposure Factors Handbook. Office of Research and Development, Washington, D.C

. EPA/600/R-06/096F. September. Available at: http://cfpub.epa.gov/ncea/cfm/recordisplay.cfm?deid=199243

.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 2- 99 

### U.S. Environmental Protection Agency (EPA)

. 2008b. Draft Report on EPA OAQPS Risk and Technology Review Methodologies: For Review by the EPA Science Advisory Board; Case Studies

– MACT I Petroleum Refining Sources, Portland Cement Manufacturing. Office of Air Quality Planning and Standards, Office of Air and Radiation, Research Triangle Park, NC. July 14, 2008.

U.S. Environmental Protection Agency (EPA). 2009

. Guidance for Implementing the January 2001 Methylmercury Water Quality Criterion. Office of Water, Office of Science a nd Technology, Washington , D .C

. EPA 823 -R- 09 -002. January. Available at: http://www.epa.gov/waterscience/criteria/methylmercury/pdf/guidance-final.pdf

.

U. S. Food and Drug Administration (FDA). 2009. Draft Risk and Benefit Assessment Report and Draft Summary of Published Research. Center for Food Safety and Applied Nutrition. January 15. Available at: http://www.cfsan.fda.gov/seafood1.html

U.S. Environmental Protection Agency ( EPA ), 2010. Personal communication from Zachary Pekar, Ambient Standards Group, Office of Air and Radiation, U.S. Environmental Protection Agency, to Heidi Hubbard, ICF International, [December 15, 2010]

Van den Berg, M., L.S. Birnbaum, M. Denison, M. De vito, W. Farlans, M. Feeley, H. Fiedler, H. Hakansson, A. Hanberg, L.. Haws, M. Rose, S. Safe, D. Schrenk, C. Tohyama, A. Tritscher, J. tuomisto, M. Tysklind, N. Walker, and R .E. Peterson. 2006. The 2005 World Health Organiza tion reevaluation of human and m ammalian toxic equivalency factors for dioxins and dioxin

- like compounds. Toxicol Sci . 93(2): 223

- 41.

Whitehead, R.G., and A.A. Paul. 1981. Infant growth and human milk requirements: A fresh approach. Lancet 2(8239): 161-163.Attachment 2 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 

### [This page intentionally left blank.]

### Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR: Summary of Approach and Evaluation



# ATTACHMENT 3: Systematic Sensitivity AnalysisAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-i [This page intentionally left blank.]Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- ii 

### TABLE OF CONTENTS

1 Systematic Sensitivity Analysis Variables and Results

................................... 1

1.1 Sensitivity Analyses

......................................................................................................................... 1 1.1.1 Systematic Sensitivity Analysis

............................................................................................. 2 1.1.2 Evaluation of Ingestion Rate Assumptions

........................................................................... 6 1.1.3 Evaluation of Body Weight Assumptions

............................................................................ 14 1.1.4 Sensitivity When Accounting for Temporally Correlated Body Weight and Ingestion Rates

15 1.1.5 Comparison of Scenarios Using Site-Specific and Screening Threshold Meteorological

Data

..................................................................................................................................... 16

Exhibit 1. The 26 Variables with the Highest Elasticities for Benzo[a]Pyrene Lifetime Risk (-5% Perturbation of Variable)

............................................................................................................................... 8 Exhibit 2. The 25 Variables with the Highest Elasticities for 2,3,7,8-TCDD Lifetime Risk (-5% Perturbation of Variable)

.................................................................................................................................................... 9 Exhibit 3. The 28 Variables with the Highest Elasticities for Cadmium Hazard Quotient for Child 1- 2 ( -5% Perturbation of Variable)

............................................................................................................................. 10 Exhibit 4. The 25 Variables with the Highest Elasticities for Divalent Mercury Hazard Quotient for Child 1- 2 ( -5% Perturbation of Variable)

................................................................................................................. 11 Exhibit 5. The 26 Variables with the Highest Elasticities for Methyl Mercury Hazard Quotient for Child 1- 2 (-5% Perturbation of Variable)

.................................................................................................................... 12 Exhibit 6. Ratio of the Modeled Total Ingestion Rates and the USEPA Total Ingestion Rates

................. 13 Exhibit 7. Comparison of the Risks and Hazard Quotients in the Screening Threshold and Alternate Ingestion Cases

.......................................................................................................................................... 14 Exhibit 8. The Risk or Hazard Quotient Estimates Using Alternate Body Weight Percentiles

................... 15 Exhibit 9. Comparison in the Elasticities In Lifetime Risk in the Correlated and Uncorrelated Analyses Assuming a 5% Decrease in the Input Variables

........................................................................................ 16 Exhibit 10. Summary of Site-specific Meteorological Data Parameters

..................................................... 17 Exhibit 11. Percent Change in Risk or Hazard Quotient Using Site-specific Meteorological Data

............. 17 Exhibit 12. The Wind Speed and the Direction Toward Which the Wind is Blowing for All Conditions for Site 1

........................................................................................................................................................... 18 Exhibit 13. Variables Included in the Systematic Sensitivity Analysis

........................................................ 19 Exhibit 14. Elasticities and Rankings for the Variables with the Highest Elasticities for Benzo[a]Pyrene

.. 25 Exhibit 15. Elasticities and Rankings for the Variables with the Highest Elasticities for 2,3,7,8 - TCDD

... 27 Exhibit 16. Elasticities and Rankings for the Variables with the Highest Elasticities for Cadmium

............ 29 Exhibit 17. Elasticities and Rankings for the Variables with the Highest Elasticities for Divalent Mercury 31 Exhibit 18. Elasticities and Rankings for the Variables with the Highest Elasticities for Methyl Mercury

... 33Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- iii [This page intentionally left blank.]Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-1 

## 1 Systematic Sensitivity Analysis

The sensitivity analysis presented in this attachment was originally performed on a previous configuration of the screening scenario. Since that time, the model configuration of the screening scenario has been refined to improve its sophistication and accuracy. The screening thresholds and model parameters presented earlier in this document are based on the updated model configuration. Time constraints precluded the performance of a revised sensitivity analysis on the updated model configuration, and therefore, the sensitivity analysis presented below has not been updated to reflect the latest model configuration on which the current screening thresholds are based. Readers may note that while some of the specific numeric estimates of the relative sensitivity of model parameters are likely to be different in the updated model configuration from the estimates presented below, the general trends are expected to be similar. One of the significant changes since the updating of the model configuration has been the dominance of the fish ingestion pathway for all the modeled PB-HAPs. Parameters that influence exposure via the fish ingestion route are therefore expected to be more sensitive in the current model configuration than estimated in the analysis presented below.

This attachment provides the tables of the variables included in the systematic sensitivity analysis in Exhibit 13 . The variables are organized into three categories: TRIM.FaTE variables, MIRC farm food chain variables, and MIRC ingestion and bodyweight variables.

This attachment also provides detailed elasticities and rankings for the variables with the highest elasticities for Benzo[a]Pyrene ( Exhibit 14 ), 2,3,7,8

– TCDD ( Exhibit 15 ), cadmium ( Exhibit 16 ), divalent mercury ( Exhibit 17 ), and methyl mercury ( Exhibit 18 ). In each case, the elasticities and rankings are provided for the local systematic sensitivity analysis (variables perturbed up and down by 5%) and the range systematic sensitivity analysis (variables perturbed up and down by 50%).

1.1 Sensitivity Analyses



### The hypothetical subsistence farmer/fisher exposure scenario used to screen emissions of PBHAPs described in this document was parameterized using generally conservative inputs. The goal was to construct a modeling scenario that is sufficiently health-protective (i.e., conservative) such that it can be used with confidence to screen out emissions that do not pose unacceptable multipathway risks, while also avoiding overly conservative characteristics that diminish the functionality of the scenario (i.e., by allowing too many “false positives,” or facilities that fail the screen for which the risks are actually acceptable). The level of conservatism of the scenario is dictated largely by the values selected by the user for model inputs. A sensitivity analysis is a useful method for evaluating the influence of model parameters and user selections for parameter values. By providing quantitative information on the importance of model parameters to a selected output, a sensitivity analysis thus also provides information on which parameters may be most influential in dictating the uncertainty associated with the results.

The sensitivity analyses conducted on the RTR screening modeling scenario encompassed the fate and transport modeling carried out using TRIM.FaTE and the farm food chain (FFC) and ingestion exposure modeling performed using MIRC. 1 

### A systematic sensitivity analysis was conducted on these parameters to obtain information regarding the relative importance of user

1 PB -HAP dose-response values used for risk calculation (i.e., oral cancer slope factors and oral reference doses, plus the mutagenicity correction factor applied to certain age groups) were not included in the sensitivity analysis

.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-2 

### inputs (Section 4.4.1). In addition, several other analyses were performed to evaluate model performance with respect to parameterization of ingestion rates (Section 4.4.2), body weight (Section 4.4.3), assumed relationships between ingestion and body weight over time (Section 4.4.4), and meteorological conditions (Section 4. 4.5). Each section presents the methods employed to conduct the sensitivity analyses, evaluation results, and notes regarding interpretation of the results. Results of these sensitivity analyses are useful in informing the level of uncertainty in screening results, highlighting parameters and aspects of the modeling scenario worthy of additional research if refinement is appropriate (e.g., for evaluating sources of PB-HAPs that do not pass the screen), and suggesting variables that are likely to be worthy of more detailed examination if a more quantitative uncertainty analysis is desired (e.g., using probabilistic methods).

1.1.1 Systematic Sensitivity Analysis

1.1.1.1 Methods

As with all predictive models, the user-specified inputs for TRIM.FaTE and MIRC influence model outputs and thus estimation of emission screening thresholds. The degree to which model outputs diverge from a nominally “correct” answer (e.g., the actual incremental risks for an individual exposed to PB-HAP emissions) encompasses both uncertainty (because values are not known with perfect accuracy) and variability (because each value selected represents a discrete choice out of a range of possible parameter values within a distribution, such as variability in body weights among individuals in an exposed population). In this analysis, we did not attempt to separately evaluate uncertainty and variability, and variation in model outputs is assumed to encompass both uncertainty and variability. Representation of each parameter with a single fixed value without representing uncertainty or variability in model calculations is a limitation of deterministic model application.

As a first step to quantifying the combined uncertainty and variability in model outputs and the screening thresholds, an analysis was performed to identify the variables to which the risk or hazard quotient calculations are most sensitive. Model sensitivity was evaluated separately for each of the PB-HAPs. The model output to which sensitivity was measured varied by chemical depending on the health impacts of greatest concern. Parameter influence on cancer risk was measured for benzo[a]pyrene and 2,3,7,8-TCDD, and influence on non-cancer hazard quotient was measured for cadmium, divalent mercury, and methyl mercury. This part of the analysis was conducted systematically by “perturbing,” or changing, the value of each selected parameter independently (i.e., one at a time, holding all other inputs at their base value) by a certain percentage and calculating the corresponding percent change in the risk or hazard quotient value. This metric is referred to as elasticity (i.e., ratio of the percent change of the model output to percent change in the input variable), with higher elasticities corresponding to greater influence.

This type of systematic sensitivity analysis has the advantage of focusing on a wide range of inputs at once so that the variables can be ranked in order of importance. However, by perturbing the variables by fixed percentages, the analysis does not necessarily focus on the most physically relevant values of each parameter. An alternate analysis could examine each variable independently (taking into account the plausible range of input values) and look at the effects of using different plausible variable values on the risk or hazard quotient estimates. We focus on a systematic sensitivity analysis here with the goal of prioritizing variables; additional examinations may be helpful in the future to better define the uncertainty.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-3 

### In the systematic sensitivity analysis, we estimated both local sensitivity, quantified as the elasticity when a parameter value is perturbed by a small percentage of its base (or default) value, and range sensitivity, for which parameters were varied by a larger percentage of the base value. These two elasticities can be different if the relationship between input and output is nonlinear (e.g., if the perturbed parameter is in the denominator of an equation in the calculation). For the evaluation of risks associated with exposures to PB- HAPs , a large difference between local and range sensitivity could indicate that variables that are less important in the base scenario used to calculate screening thresholds scenario assumptions may be more important in a less conservative site-specific evaluation. In this case, following recommendations in the Risk Assessment Guidance for Superfund (EPA 2001; see Volume III, Part A, Appendix A), we perturbed parameter values by +/-5% of the base case default value in the local sensitivity analysis and +/- 50% in the range sensitivity analysis. Thus, with some exceptions noted below, this resulted in four model simulations and corresponding elasticities for each parameter included in the analysis for each of the PB-HAPs.

Typically, a range sensitivity analysis (also referred to as “nominal sensitivity analysis”) measures the effect on model outputs across the entire expected or plausible range of values for a given input. This provides more comprehensive information on the behavior of the model with respect to the input being varied by demonstrating the maximum potential influence of that input on model outputs. In the case of the RTR modeling scenario, information on the expected or most likely input ranges is available on only a few of the parameters defined by the user, and there is a relatively large number of parameters to be evaluated. The selection of both 5 and 50 percent as perturbation increments was intended to be an efficient compromise between conducting an authentic range sensitivity analysis and evaluating only more localized sensitivity.

To obtain a comprehensive estimate of the relative sensitivity of risk results across the range of numerical user inputs, as many TRIM.FaTE and MIRC inputs as possible were included in the analysis. To that end, all the MIRC ingestion and exposure variables were included. For TRIM.FaTE, properties assumed a priori to have greater influence on model outputs were included. The large number of user-specified numerical inputs to TRIM.FaTE and computational limitations made inclusion of all TRIM.FaTE inputs in this sensitivity analysis impractical. TRIM.FaTE inputs for this sensitivity evaluation were selected based on results obtained from previous TRIM.FaTE evaluations (including the TRIM.FaTE mercury test case; EPA 2005b) and professional judgment/intuition drawing on experience with the model.

The full set of inputs included in the systematic analysis is shown in Exhibit 13 . Parameters are grouped by the model in which they are used, with the MIRC variables further divided into farm food chain and ingestion/body weight categories. In some cases, inputs included in the analysis could not be increased by either 5% or 50% or both, since the variable has a physical upper bound which cannot be exceeded (e.g., the number of days of exposure per year was already set to 365, so it cannot be increased by 5% or 50%). The footnotes in Exhibit 13 indicate the variables that could not be increased by 5% and/or 50%. For some inputs, the ability to perturb the input depends on the PB-HAP being modeled, as indicated. In addition, some inputs were assigned a baseline value of zero for estimating a screening threshold (e.g., the empirical correction factor for protected vegetables and the exposure variables related to the water pathway). These variables are not included in the systematic sensitivity analysis. In all, approximately 240 variables were examined.

Two types of inputs included in the systematic analysis, pH and the moisture adjustment factor (MAF), received special treatment.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-4 

### pH, which is a user input for the surface soil, root zone soil, surface water, and sediment compartments, is measured on a logarithmic scale, and this input is (in some cases) used in the exponent of TRIM.FaTE algorithms. To obtain sensitivity metrics for pH inputs that can be compared to results for other inputs with more linear relationships with risk, the values for pH were changed to the equivalent hydrogen ion concentration (that is, 10 pH 

### ) and that value was varied by 5 or 50%. Then, the log base ten of the varied hydrogen ion concentration was calculated to serve as the pH to use in TRIM.FaTE for the sensitivity

case.

The moisture adjustment factor indicates the percent of a produce item that is water; this factor is used to convert from wet weight to dry weight concentration in MIRC. This calculation is made by finding the percent of the produce that is not water (i.e., 100 minus MAF) and multiplying by the wet-weight basis concentration. Because the physical variable of interest is really the fraction of produce that is NOT water, this value (100 minus MAF) was used in the sensitivity analysis as the base value (rather than MAF itself).

In addition, in two cases, known or assumed correlations between inputs were taken into account in the systematic sensitivity analysis.

The fractions of T3 and T4 fish that are consumed must add to one in MIRC; thus, when one was changed by a given percentage, the other was also changed to ensure the sum was still one.

In parameterizing several sediment and water inputs used in TRIM.FaTE, soil/sediment and runoff/surface water balance is assumed. These relationships are not explicitly accounted for by TRIM.FaTE but rather were calculated off-line prior to setting the input value in the model. TRIM.FaTE variables subject to soil or sediment balances include erosion rate, precipitation rate, runoff rate, sediment deposition velocity, suspended sediment concentration, sediment porosity, water retention time in the pond, and the suspended sediment concentration. For example, increasing the sediment deposition velocity results in an increase in the sediment resuspension velocity to ensure the sediment mass balance is preserved (the specific relationships assumed between inputs are described elsewhere). These correlations were respected in the systematic sensitivity analysis such that when an independent input was perturbed, any dependent input variables were altered correspondingly to preserve the water and sediment balances.

Other TRIM.FaTE and MIRC inputs are also related. Some of the relationships involving ingestion rates and body weight were evaluated in the context of the sensitivity analysis, as described in the sections that follow. In general, however, the current analysis did not endeavor to determine additional correlations or account for them in the sensitivity calculations conducted.

1.1.1.2 Results

Exhibit 1 through Exhibit 5 display the variables with the highest elasticities for each PB-HAP. The inputs were sorted according to the elasticities estimated for a decrease in input by 5%. This case (as opposed to the case where variables were increased by 5%) was chosen because all inputs, including those for which the base case value was set at the maximum, could be part of the sorting procedure. Parameters were sorted by absolute value of elasticity, and the bars in the charts are color coded to distinguish whether the input is used in TRIM.FaTE, MIRC farm food chain calculations, or MIRC ingestion exposure calculations. TheAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-5 

### top 25 inputs are shown for all PB-HAPs; for some chemicals, additional inputs are included if more than one input corresponded to the 25 th 

### highest elasticity.

In general, mixing height, emission rate, and horizontal wind speed always appear near the top of the ranking for all PB-HAPs analyzed. The emission rate elasticity is always 1.00, indicating that a 5% reduction in the emission rate gives a 5% reduction in the risk or hazard quotient. The mixing height and horizontal wind speed elasticities are always negative and are either above or below 1.00. When the mixing height is decreased, the PB-HAP emissions spread over a smaller volume and more of the PB-HAP mass remains near the surface for deposition. When the horizontal velocity decreases, the PB-HAP remains within the model domain for a longer time and the concentrations in the model compartments increase accordingly.

A fourth input, sediment deposition/resuspension rate, has an elasticity greater than one in magnitude for methyl mercury. This sensitivity case represents a decrease in the user-specified input for sediment deposition velocity by 5% and a concurrent 7% decrease in the resuspension velocity (calculated to maintain the sediment balance 2 

### ). This value is particularly important for methyl mercury HQ because methylation of mercury occurs to a large degree in the sediment, and a decrease in deposition velocity results in a larger, proportionate decrease in the resuspension velocity, indicating a longer residence time in the sediment and a higher degree of methylation.

Only the above four inputs (mixing height, emission rate, horizontal wind speed, and sediment deposition) have absolute elasticities greater than or equal to one. Beyond these, the inputswith the highest elasticities are those that influence the primary exposure pathways for each PBHAP. Primary ingestion exposure pathways (in this case defined as the food categories that account for 75% to 85% of the total risk or hazard) are indicated at the top of each of the charts.

For benzo[a]pyrene ( Exhibit 1 ), the primary pathways are ingestion of fruits, vegetables, and dairy products, and most of the inputs with the highest elasticities are used in farm food chain and ingestion exposure calculations. Because wet deposition is of particular importance, the exposed fruits and vegetables represent the more sensitive pathway compared with the protected fruits and vegetables. In addition, the analysis reveals that within the food chain diet of the dairy cows, risk is most sensitive to the inputs used to estimate chemical transfer via the cow’s forage pathway (as opposed to the silage or grain pathways).

Sensitivity results obtained for 2,3,7,8-TCDD ( Exhibit 2 ) are consistent with the observation that the primary pathways are fish, beef, and dairy ingestion. Results also reinforce the conclusion that cancer risk is more sensitive to the forage pathway for dairy and beef than the grain or silage pathways.

Sensitivity results for cadmium ( Exhibit 3 ) reflect the primary pathways of fruits, vegetables, and fish, but in this case the hazard quotient is more sensitive to the protected fruits and vegetables (and thus also the soil variables) than the exposed fruits and vegetables. The HQ is also more sensitive to variables affecting the T3 fish than the T4

2 The sediment balance maintains a zero net flux of sediment mass into the sediment at all times (i.e., a steady state) by balancing the deposition, resuspension, and burial fluxes. The burial flux is calculated by subtracting the amount of sediment flushed from the pond from the amount introduced into the pond via erosion at every time step. The deposition rate is specified. Then, the resuspension rate is calculated by adding the burial and deposition fluxes to ensure no net flux into or out of the sediment.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-6 

### fish, consistent with higher cadmium concentrations estimated by TRIM.FaTE for that fish type.

Elasticities for divalent mercury ( Exhibit 4 ) reflect the primary pathways of soil, fruits, and vegetables through the importance of the rain and erosion variables and the protected fruit and vegetable variables. Finally, results for methyl mercury ( Exhibit 5 ) are consistent with fish consumption as the primary pathway, with inputs specific to T4 fish more important than those specific to T3 fish due to the higher bioaccumulation potential (and therefore exposures) associated with higher trophic level fish.

Looking across the different PB-HAPs, several of the TRIM.FaTE variables with high elasticities are highly dependent on assumptions made in configuring the TRIM.FaTE modeling scenario, including mixing height, horizontal wind speed, rain rate, dry deposition velocity, surface water retention time (correlated directly with pond depth and other inputs given the water balance that is assumed), and surface water temperature. These inputs, which would likely be set differently for a site-specific analysis, represent influential parameters worthy of additional evaluation to quantify the conservative nature of the scenario. The area of the parcels and the temporal pattern of the precipitation may also be influential; however, these were not evaluated quantitatively in the systematic sensitivity analysis given the complexity involved with adjusting these inputs.

Differences between the results of the local and range sensitivity analyses are presented in Attachment 3, Exhibits 2 through 6. These tables show elasticities and elasticity rankings by PB -HAP for each input that appears in the top 25 elasticities for all four analyses (i.e., perturbation by -50%, -5%, 5%, and 50% of the base case value). The rankings for some inputs are somewhat different across the four cases, but no drastic differences are noted when comparing the range and local sensitivity analyses for any of the PB-HAPs. This suggests the local sensitivity analysis may be sufficient for drawing some conclusions about the relative influence of user-specified inputs on the risk and hazard quotient estimates.

The results of this sensitivity analysis indicate the 25-30 variables to which the risk and hazard quotient estimates are most sensitive. In proceeding with a probabilistic analysis which would quantify the uncertainty in the model estimates, these variables would be of primary importance and should be the focus when developing input variable distributions. Further research could also confirm that these variables are set in an appropriately conservative fashion for the purposes of developing a screening scenario.

1.1.2 Evaluation of Ingestion Rate Assumptions

To calculate the screening threshold levels, the conservative assumption was made that a person ingests food at the 90 th 

### percentile level for each food type included in the analysis. These ingestion rates can then be added to get the assumed total ingestion rate. 3 

### USEPA 2008 and 2005d provide estimates of the 90 th 

### percentile total ingestion rate for different age groups (that is, percentiles for total amount of food ingested, rather than a sum of individual percentiles) based on CSFII data 1994-96 and 1998 (see Exhibit 6-12 of Attachment 2). When comparing the two, the total ingestion rates used to determine the screening thresholds tend to be a factor of two to three times higher than the 90 th 

### percentile total ingestion rates (see Exhibit 7-1 of Attachment 2). An alternative approach that still captures the high-end would be to use the 90 th

3 This calculated total ingestion rate will not include any other food consumed by the homestead family outside of the MIRC food categories. In making the comparison with the total ingestion rates, then, the assumption is made that the entire diet of the family is captured by the MIRC food categories.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-7 

### percentile ingestion rates for food types associated with highest risks for a given PB-HAP (to account for the individual who may happen to eat higher-than-typical amounts for each of those food categories) while setting ingestion rates for other food types to a lower percentile in order to bring the total ingestion rate to a more realistic level (e.g., to something closer to the 90 th 

### percentile total ingestion rate).

In order to determine the effect of lowering the ingestion rates for the non-primary ingestion pathways (and provide information on whether this refinement would be worth the additional complexity in the model set-up), ingestion rates were kept at the 90 th 

### percentile for the primary (risk-driving) food types for each PB-HAP but were reduced to median ingestion rates for the same population (subsistence famers) for the other types of food. This scenario, referred to here as the “alternate ingestion case,” was evaluated for each PB -HAP. Specifically, the total food ingestion rates was calculated for the alternate ingestion cases for each PB-HAP, and these values were compared with the USEPA 2008 and 2005d estimates of 90 th 

### percentile totalAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-8 

### Exhibit 1 . The 26 Variables with the Highest Elasticities for Benzo[a]Pyrene Lifetime Risk (

- 5% Perturbation of Variable) Pr imary Pathways: Fruits, Vegetables, and DairyAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3-9 

### Exhibit 2 . The 25 Variables with the Highest Elasticities for 2,3,7,8

- TCDD Lifetime Risk (

- 5% Perturbation of Variable) Primary Pathways: Fish, Beef, and DairyAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 10 

### Exhibit 3 . The 28 Variables with the Highest Elasticities for Cadmium Hazard Quotient for Child 1

- 2 (

- 5% Perturbation of Variable) Primary Pathways: Fruits, Vegetables, and FishAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 11 

### Exhibit 4 . The 25 Variable s with the Highest Elasticities for Divalent Mercury Hazard Quotient for Child 1

- 2 (

- 5% Perturbation of Variable) Primary Pathways: Soil, Fruits and VegetablesAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 12 

### Exhibit 5 . The 26 Variables with the Highest Elasticities for Methyl Mercury Hazard Quotient for Child 1

- 2 (

- 5% Perturbation of Variable) Primary Pathway: FishAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 13 

### ingestion (referred to as the “EPA total ingestion rate”) via a ratio ( Exhibit 6 ). Because the EPA total ingestion rate represents the total amount of cooked food consumed, preparation losses were applied to each of the food category-specific ingestion rates input into MIRC before the ratio was calculated. Soil consumption was not included in these calculations. In addition, the estimated screening level cancer risk or HQ for each PB-HAP was compared to the recalculated risk/HQ for the alternate ingestion cases ( Exhibit 7 ).

As expected, the ratios presented in Exhibit 6 demonstrate that using the alternate ingestion rate combination tends to result in lower estimated total ingestion rates, approaching the (more realistic) USEPA total ingestion rates for the child age groups. The degree to which the total ingestion rate is decreased depends on the numb er of pathways labeled “primary pathways” for risk (as well as the mass of food represented by a given pathway). Thus, it is reasonable that lower total ingestion rates (and lower ratios with respect to EPA total ingestion rate) are calculated for methyl mercury, for which only one pathway (fish) drives risk, and higher rates and ratios are calculated for benzo[a]pyrene, for which several food types are important.

Exhibit 7 compares the lifetime risk or child age 1-2 HQ for the alternate ingestion rate case to the corresponding risk/HQ for the screening threshold case. Overall, the changes in risk and HQ were relatively modest, ranging between 7% and 20%. This result indicates that relaxing the conservative assumption of high ingestion rates for all the pathways does not significantly change the risk and hazard calculations but does drive the total ingestion rates closer to the USEPA 90 th 

### percentile total ingestion rates. However, implementing this multi-percentile technique requires prior knowledge of the dominant pathways for each chemical, which is determined primarily from the model estimates themselves. Assuming 90 th 

### percentile ingestion rates for all food categories has the advantage of simplicity (using the same set of ingestion rates for all chemicals) and does not dramatically impact the risk and hazard quotient estimates.

Exhibit 6 . Ratio of the Modeled Total Ingestion Rates and the USEPA Total Ingestion Rates

Ratio of Ingestion Rates
Child (1

- 2) Child

(3

- 5) Child

(6

- 11) Child

(12

- 19) Adult

(20

- 70)

Benzo[a]Pyrene Alternate Ingestion 1.7 1.3 1.4 1.4 2.6

2,3,7,8

- TCDD Alternate Ingestion 1.3 1.0 1.0 1.0 1.8

Cadmium Alternate Ingestion 1.3 1.1 1.2 1.0 1.6

Divalent Mercury Alternate Ingestio n 1.3 1.1 1.1 1.0 1.6

Methyl Mercury Alternate Ingestion 0.9 0.8 0.8 0.6 0.8

Screening Threshold Ingestion 1.8 1.4 1.6 1.5 2.8Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 14 

### Exhibit 7 . Comparison of the Risks and Hazard Quotients in the Screening

Threshold and Alterna te Ingestion Cases

PB

- HAP Categories with

90th Percentile Ingestion in Alternate Case a Categories with

Median Ingestion Rates in Alternate Case a Case Value

Benzo[a]pyrene Pro. fruit, pro.

veg., exp. fruit, exp. veg., root veg., and dairy Soil, fish, be ef, pork

poultry, and eggs Screening threshold

lifetime risk 1.00E

- 06

Alternate ingestion case 7.98E

- 07

Percent Change in Risk

- 20.2%

2,3,7,8

- TCDD Fish and dairy Soil, pro. fruit, pro. veg., exp. fruit, exp. veg., root veg., beef, pork, poultry, and eggs Screening threshold

lifetime risk 1.00E

- 06

Alternate ingestion case 9.14E

- 07
Percent Change in Risk

- 8.6%

Cadmium Fish, pro. fruit,

pro. veg., exp. fruit, exp. veg., and root veg. Soil, beef, dairy,

pork, poultry, and
eggs Screening thre shold child

(1

- 2) hazard quotient 1.00E+00

Alternate ingestion case 9.05E

- 01
Percent Change in Risk

- 9.5%

Divalent Mercury Soil, pro. fruit,

pro. veg., exp. fruit, exp. veg., and root veg. Fish, beef, dairy,

pork, poultry, and
eggs Screening thres hold child

(1

- 2) hazard quotient 1.00E+00

Alternate ingestion case 9.26E

- 01
Percent Change in Risk

- 7.4%

Methyl Mercury Fish Soil, pro. fruit, pro. veg., exp. fruit, exp. veg., root veg., beef, dairy, pork, poultry, and eggs Screening threshold ch ild

(1

- 2) hazard quotient 5.62E

- 01

Alternate ingestion case 5.19E

- 01
Percent Change in Risk

- 7.8%

a Pro. fruit is protected fruits, pro. veg. is protected vegetables, exp. fruit is exposed fruits, exp. veg. is exposed vegetables, and root veg. is root vegetables.



### 1.1.3 Evaluation of Body Weight Assumptions

As stated in Attachment 2, Section 6.1.3, the screening threshold rates were calculated using mean body weight following EPA’s default screening recommendation. This assumption does not represent the most conservative assumption, however, since lower percentile body weights will give higher risk and hazard quotient estimates. In contrast, the ingestion rates were set to the more conservative 90 th 

### percentile level. To investigate the sensitivity of using alternate body weight percentiles, an alternate MIRC run was performed using the 5 th 

### , 50 th 

### , 90 th 

### , and 95 th 

### percentiles for body weight while keeping all other variable values as specified in the screening threshold calculations. These alternate risk or hazard quotient model estimates and the percent change relative to the screening threshold calculations are shown in Exhibit 8 . Changing from the mean to the median body weights produces only very modest changes to the risks/hazard
qu otients. Changing to the 5 th 

### percentile body weights gives the most conservative model estimates, with percent changes of up to 22% for the PB-HAPs used to set the screening threshold rates and a 26% change in methyl mercury. Using upper percentiles for body weights produces modest decreases in risk or hazard quotient of 3% to 16% for the PB-HAPs used to set the screening threshold rates. Thus, changing the body weight to either a moreAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 15 

### conservative or less conservative percentile produces changes in the risk or hazard quotient which are appreciable but not dramatic (i.e., typically less than 25%), suggesting the mean body weight assumption may be an appropriate choice for the screening scenario.

Exhibit 8 . The Risk or Hazard Qu otient Estimates Using Alternate Body Weight Percentiles

Screening T hreshold 5th Percentile Median 90th Percentile 95th Percentile

Risk or HQ a %

Ch b Risk or

HQ a %

Ch b Risk or HQ a %

Ch b Risk or

HQ a %

Ch b
Benzo[a]pyrene c 1.0E

- 06 1.1E

- 06 6% 1.0E

- 06 0% 9.7E

- 07

- 3% 9.6E

- 07

- 4% 2,3,7,8

- TCDD c 1.0E

- 06 1.2E

- 06 22% 1.0E

- 06 2% 8.8E

- 07

- 12% 8.4E

- 07

- 16%
Cadmium d 1.00 1.07 7% 1.00 0% 0.96

- 4% 0.95

- 5% Divalent Mercury d 1.00 1.16 16% 1.00 0% 0.91

- 9% 0.89

- 11% Methyl Mercury d 0.56 0.71 26% 0.57 1% 0.48

- 15% 0.46

- 18%

a HQ is the hazard quotient for a child aged 1

- 2.
b % Ch Is the percent change in the risk or hazard quotient relative to the screening threshold calculations.

c Percent change in lifetime risk.
d Percent change in the hazard quoti ent for a child age 1 to 2.



### 1.1.4 Sensitivity When Accounting for Temporally Correlated Body Weight and Ingestion Rates

In calculating lifetime cancer risks, age-specific ingestion rates and body weights are used to estimate the lifetime average daily dose. In the systematic sensitivity analysis, the body weights and ingestion rates for each of the five age categories were changed independently to assess the sensitivity of lifetime risk to each input separately (for example, body weight was first perturbed only for a child 1-2 yrs old, leaving body weight unchanged for other age groups). However, in actuality, ingestion rates (and body weights) for an individual during different age groups will likely be correlated across that individual’s lifetime. For example, a person who eats higher-than-average amounts of poultry when they are 11 can be reasonably expected to eat higher-than-average amounts when they are 50 due to lifetime dietary preferences. To estimate the effect th is correlation has on sensitivity of cancer risk to ingestion rate

, a perturbation of -5% for a given food type was applied to ingestion rate for all age categories and the resulting elasticity was compared to the previous result (obtained ignoring temporal/age-group correlations). This assumption was applied separately to each ingestion rate category

, and separately to body weight, to estimate the effect of age group correlations for these inputs ( Exhibit 9 ). Because only benzo[a]pyrene and 2,3,7,8-TCDD were evaluated for cancer risks, this analysis was only performed for these two PB

- HAP s (t he other PB -HAPs use HQs calculated separately for each age group

, and the correlation analysis is not applicable).

The systematic sensitivity analysis suggested that cancer risks associated with benzo[a]pyrene are relatively insensitive to body weight and any individual food ingestion rate (where both inputs were varied for a single age group at a time)

. When body weight or ingestion rate for a given food type is decreased by 5% for all age groups in concert, the corresponding elasticity increases by a factor of two to three. This increase is significant enough to cause the dairy ingestion, exposed fruit ingestion, body weight, and exposed vegetable ingestion variables to be ranked among the most influential variables on the basis of absolute elasticity.

For 2,3,7,8-TCDD, the systematic sensitivity analysis illustrated that cancer risk is sensitive to body weight, fish ingestion rate, and dairy ingestion rate. Elasticities for these inputs increase by a factor of 1.3 to 1.6 when the inputs are kept constant across age groups. This difference results in rise in the systematic sensitivity ranking of these variables.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 16 

### Exhibit 9

. Comparison in the Elastici ties In Lifetime Risk in the Correlated and Uncorr e lated Analyses Assuming a 5% Decrease in the Input Variables

Elasticity in the Correlated Analysis Maximum

Elasticity in Uncorrelated Analysis Age Group of

Maximum Elasticity in Uncorrelated Analysis

B enzo[a]pyrene Dairy Ingestion 0.34 0.11 Child 1

- 2

Exp. Fruit Ingestion 0.22 0.10 Adult Body Weight

- 0.17

- 0.06 Child 1

- 2 Exp. Veg. Ingestion 0.17 0.09 Adult Soil Ingestion 0.12 0.05 Child 1

- 2 Beef Ingestion 0.07 0.03 Adult Fish Ingestion 0.04 0 .02 Adult Poultry Ingestion 0.02 0.01 Adult Pro. Fruit Ingestion 0.01 < 0.01 Adult Egg Ingestion 0.01 < 0.01 Adult Pork Ingestion < 0.01 < 0.01 Adult Prot. Veg. Ingestion < 0.01 < 0.01 Adult Root Veg. Ingestion < 0.01 < 0.01 Adult

2,3,7,8

- T CDD Body Weight

- 0.59

- 0.45 Adult

Fish Ingestion 0.56 0.43 Adult Dairy Ingestion 0.32 0.20 Child 1

- 2 Beef Ingestion 0.09 0.06 Adult Pork Ingestion 0.01 0.01 Adult Soil Ingestion < 0.01 < 0.01 Adult Exp. Fruit Ingestion < 0.01 < 0.01 Adult
Ex p. Veg. Ingestion < 0.01 < 0.01 Adult Root Veg. Ingestion < 0.01 < 0.01 Adult Poultry Ingestion < 0.01 < 0.01 Adult Egg Ingestion < 0.01 < 0.01 Adult Pro. Fruit Ingestion < 0.01 < 0.01 Adult Prot. Veg. Ingestion < 0.01 < 0.01 Adult



### Overall, how ever, th ese differences represent a modest percent change in the lifetime risk values and indicate that accounting for the assumed correlation between the body weights and ingestion rates throughout an individual's lifetime does not significantly influence the model's predicted risks. For the other ingestion rates, the lifetime risks are not very sensitive to the parameters when the inputs are decreased by 5%, and accounting for the correlations between the variables does not affect this conclusion.

1.1.5 Comparison of Scenarios Using Site-Specific and Screening Threshold Meteorological Data

For RTR, the screening threshold emission levels were calculated using a conservative and hypothetical exposure scenario for a farm homestead. If the modeling scenario has been configured as intended, the substitution of site-specific data will nearly always result in a lower (or equal) exposure and risk estimate. To inform the degree of conservatism associated withAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 17 

### the baseline meteorological inputs, three additional analyses were conducted in which observed (site-specific) meteorology data were used in place of the meteorological values set for thescreening threshold scenario. The three locations were selected to take advantage of readilyavailable TRIM.FaTE meteorological data. Exhibit 10 compares some of the summary statistics for the three meteorological data sets with those used for the screening threshold scenario. 4



### Exhibit 10

. Summary of Site

- specific Meteorological Data Parameters

Parameter (units a ) Screening Scenario b Site 1 c Site 2 c Site 3 c

Average air temperature (K) 298 291.9 284.7 283.5 Average horizontal wind speed (m/s) 2.8 4.4 4 3 Annual precipitation (m/yr) 1.5 1.1 1.1 1.1 Average urban mixing heig ht (m) 710 1,087 1,225 861

a K = Kelvin, m/s = meters/second, m/yr = meters per year, m = meters
b Values listed for the baseline scenario indicate the fixed value used in the baseline screening scenario

. c Site

- specific values a re arithmetic averages of single or multi year data sets ; Site 1 = 1989

– 1993; Site 2 = 1994; Site 3 = 1990

– 1995

.


### The results of using these three site-specific meteorological data sets on the risk or hazard quotient for each PB- HAP are summarized in Exhibit 11 . The results indicate that the wind direction

–

and specifically how often the wind blows from the source toward the hypothetical watershed, or toward due east

– is an important influence on the estimat ed media concentrations and ingestion exposures. For the three data sets used in this analysis, the largest decrease in risk or hazard quotient was observed for Site 1. This finding is consistent with the underlying patterns in wind direction and their relationship to the locations where exposure is assumed to occur. Exhibit 12 shows that wind direction towards due east occurs less than two percent of the time for this location, reinforcing the conclusion that a limited wind flow directly from the source to the watershed will decrease contamination. These results suggest that using meteorological data more representative of a specific site will decrease the estimated risk or hazard quotient by as much as an order of magnitude for the hypothetical receptor represented.

Exhibit 11 . Percent Change in Risk or Hazard Quotient Using Site

- specific Meteorological Data

Screening Threshold Site 1 Site 2 Site 3

Risk or HQ a % Ch b Risk or HQ a % Ch b Risk or

HQ a % Ch b

Benzo[a]pyrene c 1.00E

- 06 1.05E

- 07

- 89% 2.43E

- 07

- 76% 2.19E

- 07

- 78%
2,3,7,8

- TCDD c 1.00E

- 06 8.39E

- 08

- 92% 3.76E

- 07

- 62% 2.56E

- 07

- 74%

Cadmium d 1.00 0.07

- 93% 0.14

- 86% 0.15

- 85% Divalent Mercury d 1.00 0.08

- 92% 0.19

- 81% 0.18

- 82% Methyl Mercury d 0.56 0.02

- 97% 0.06

- 90% 0.05

- 91%

a HQ is the ha zard quotient for a child aged 1

- 2.
b % Ch Is the percent change in the risk or hazard quotient relative to the screening threshold calculations.

c Percent change in lifetime risk.
d Percent change in the hazard quotient for a child age 1 to 2.

4 Exhibit does not include a measure of the frequency and average of wind directions, which can be illustrated with a wind rose but cannot be effectively characterized with a single value.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 18 

### Exhibit 12

. The Wind Speed and the Direction Toward Which the Wind is Blowing for All Conditions for Site 1Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 19 

### Exhibit 13 . Variables Included in the Systematic Sensitivity Analysis

Variable Name Variable Description

TRIM.FaTE Variables
AirTemp Ambient Air Temperature AlgaeCarbonCont Carbon Content of Algae in Pond AlgaeDensity Density of Algae in Pond AlgaeGrowthRate Growth Rate of Algae in Pond AlgaeRadius Radius of Single Algae in Pond
Biomass Bio mass in Pond for all Aquatic Species
ChlorideConc Water

- Chloride Concentration ChlorophyllConc Water

- Chlorophyll Concentration
EmissionRate Emission Rate of all PBHAP s EroRate Erosion Rate for all Parcels
FishMass Fish Body Weight for all Aquatic Sp ecies HorizWindSpeed Horizontal Wind Speed MixHeight Mixing Height
Rain Annual Rainfall
RootSoilAir Root Soil

- Fraction Air
RootSoilOCC Root Soil

- Organic Carbon Fraction RootSoilpH Root Soil

- pH
RootSoilSand Root Soil

- Fraction Sand
RootSoilVertVe l Root Soil

- Average vertical velocity of water (percolation)
RootSoilWat Root Soil

- Fraction Water
RunoffRate Total Water Runoff Rate SedDepVel

, SedRusVel Sediment Deposition Velocity and Resuspension Velocity

SedOCC Sediment

- Organic Carbon Fraction SedpH Sediment

- pH SedPorosity Sediment Porosity
SedSand Sediment

- Fraction Sand StackHeight Stack Height
SurfSoilAir Surface Soil

- Fraction Air
SurfSoilOCC Surface Soil

- Organic Carbon Fraction SurfSoilpH Surface Soil

- pH SurfSoilSand Surface Soil

- Fraction Sand
SurfSoilVertVel Surface Soil

- Average vertical velocity of water (percolation)
SurfSoilWater Surface Soil

- Fraction Water SurfWatTemp Water Temperature WatFractSand Water

- Fraction Sand
WatOCC Water

- Organic Carbon Fraction WatpH Wate r

- pH
WatRetTime Rentention Time in Pond WatSuspSed Water

- Suspended Sediment ConcentrationAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 20 

### Exhibit 13 . Variables Included in the Systematic Sensitivity Analysis

Variable Name Variable Description

MIRC Farm Food Chain Variables

100

- MAF_ef 100

- Moisture adjustment factor, Exposed Fruit
100

- MAF_ev 100

- Moisture adjustment factor, Exposed Vegetable
100

- M AF_pf 100

- Moisture adjustment factor, Protected Fruit
100

- MAF_pv 100

- Moisture adjustment factor, Protected Vegetable
100

- MAF_rv 100

- Moisture adjustment factor, Root Vegetable Ba_beef PBHAP

- specific biotransfer factor, Beef Ba_dairy PBHAP

- specific biotransfer factor, Dairy Ba_egg PBHAP

- specific biotransfer factor, Eggs Ba_pork PBHAP

- specific biotransfer factor, Pork Ba_poultry PBHAP

- specific biotransfer factor, Poultry Br_AG_produce_ef Plant

- soil PBHAP bioconcentration factor, Exposed Fruit
Br _AG_produce_ev Plant

- soil PBHAP bioconcentration factor, Exposed Vegetables Br_AG_produce_fo Plant

- soil PBHAP bioconcentration factor, Forage Feed Br_AG_produce_gr Plant

- soil PBHAP bioconcentration factor, Grain Feed Br_AG_produce_pf Plant

- soil PBHAP bi oconcentration factor, Protected Fruit Br_AG_produce_pv Plant

- soil PBHAP bioconcentration factor, Protected Vegetable Br_AG_produce_si Plant

- soil PBHAP bioconcentration factor, Silage Feed Br_AG_rootveg Plant

- soil PBHAP bioconcentration factor, Root Veg etables
Bs a ,b Soil bioavailability factor for livestock
Bv_AG Air

- to

- plant biotransfer factor for aboveground produce for vapor

- phase

PBHAP in air C_FishT3 Concentration of PBHAP in whole fish for T3 fish C_FishT4 Concentration of PBHAP in whole fish for T4 fish C_Soil Concentration of PBHAP in soil from contaminated area
Ca Average annual total PBHAP concentration in air Cs_root_zone_feed Average soil concentration in contaminated area used to grow animal feed Cs_root_zone_ produce Average PBHAP c oncentration in soil at root

- zone depth in produce

- growing

area Cs_S_animal_ ingest PBHAP concentration in surface soil in contaminated area where livestock feed
Drdp Average annual dry deposition of particle

- phase PBHAP Drwp Average annual wet deposi tion of particle

- phase PBHAP
Fv b ,c Fraction of airborne PBHAP in vapor phase
Fw Fraction of wet deposition that adheres to plant surfaces
Kds PBHAP

- specific soil/water partition coefficient Kp_ef Plant surface loss coefficient, Exposed Fruit Kp_ev P lant surface loss coefficient, Exposed Vegetable Kp_fo Plant surface loss coefficient, Forage Kp_si Plant surface loss coefficient, Silage L1_beef Loss type 1, Beef L1_ExpFruit Loss type 1, Exposed Fruit L1_ExpVeg Loss type 1, Exposed Vegetable L1_Fi sh Loss type 1, Fish L1_pork Loss type 1, PorkAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 21 

### Exhibit 13 . Variables Included in the Systematic Sensitivity Analysis

Variable Name Variable Description
L1_poultry Loss type 1, Poultry L1_ProFruit Loss type 1, Protected Fruit L1_ProVeg Loss type 1, Protected Vegetable L1_RootVeg Loss type 1, Root Vegetable L2_beef Loss type 2, Beef L2_ExpFruit Loss type 2, Exposed Fruit L2_Fish Loss type 2, Fish L2_pork Loss type 2, Pork L2_poultry Loss type 2, Poultry L2_RootVeg Loss type 2, Root Vegetable
MF d,e Mammalian metabolism factor

_a Density of air Qp_fo_beef Quantity of forage plant type eaten per animal per day, Beef Qp_fo_dairy Quantity of forage plant type eaten per animal per day, Dairy Qp_gr_beef Quantity of grain plant type eaten per animal per day, Beef Qp_gr_dairy Quan tity of grain plant type eaten per animal per day, Dairy Qp_gr_egg Quantity of grain plant type eaten per animal per day, Eggs Qp_gr_pork Quantity of grain plant type eaten per animal per day, Pork Qp_gr_poultry Quantity of grain plant type eaten per an imal per day, Poultry Qp_si_beef Quantity of silage plant type eaten per animal per day, Beef Qp_si_dairy Quantity of silage plant type eaten per animal per day, Dairy Qp_si_pork Quantity of silage plant type eaten per animal per day, Pork Qs_beef Quan tity of soil eaten by the animal each day, Beef Qs_dairy Quantity of soil eaten by the animal each day, Dairy Qs_egg Quantity of soil eaten by the animal each day, Eggs Qs_pork Quantity of soil eaten by the animal each day, Pork Qs_poultry Quantity of soil eaten by the animal each day, Poultry RCF PBHAP

- specific root concentration factor for tubers and root produce Rp_ef Interception fraction of the edible portion of plant, Exposed Fruit Rp_ev Interception fraction of the edible portion of plant, Exp osed Vegetable Rp_fo Interception fraction of the edible portion of plant, Forage Rp_si Interception fraction of the edible portion of plant, Silage Tp_ef Length of plant exposure to deposition per harvest, Exposed Fruit Tp_ev Length of plant exposure to deposition per harvest, Exposed Vegetable Tp_fo Length of plant exposure to deposition per harvest, Forage Tp_si Length of plant exposure to deposition per harvest, Silage VG_AG_ef f,g Empirical correction factor, Exposed Fruit VG_AG_ev f,g Empirica l correction factor, Exposed Vegetable VG_AG_fo a,b Empirical correction factor, Forage VG_AG_si Empirical correction factor, Silage VG_rootveg f,g Empirical correction factor, Root Vegetable Yp_ef Yield or standing crop biomass, Exposed Fruit Yp_ev Y ield or standing crop biomass, Exposed Vegetable Yp_fo Yield or standing crop biomass, Forage Yp_si Yield or standing crop biomass, SilageAttachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 22 

### Exhibit 13 . Variables Included in the Systematic Sensitivity Analysis

Variable Name Variable Description
MIRC Ingestion and Body Weight Variables
BW_adlt Body weight, Adult 20

- 70 BW_ch1 Body weight, Child 1

- 2 BW_ch2 Body weight, Child 3

- 5 BW_ch3 Body Weight, Child 6

- 11 BW_ch4 Body Weight, Child 12

- 19 EF_beef a,b Exposure factor, Beef EF_dairy a,b Exposure factor, Dairy EF_egg a,b Exposure factor, Eggs EF_ExpFruit a,b Exposure factor, Exposed Fruit EF_ExpVeg a,b Exposure factor, Exposed Vegetables EF_Fish a,b Exposure factor, Fish EF_pork a,b Exposure factor, Pork EF_poultry a,b Exposure factor, Poultry EF_ProFruit a,b Exposure factor, Protected Fruit EF_ProVeg a,b Exposure factor, Protected Vegetables EF_R ootVeg a,b Exposure factor, Root Vegetables EF_Soil a,b Exposure factor, Soil EF_water a,b Exposure factor, Water F_fo_beef a,b Fraction of forage plant type from contaminated area used to grow feed, Beef F_fo_dairy a,b Fraction of forage plant type fr om contaminated area used to grow feed, Dairy F_gr_beef a,b Fraction of grain plant type from contaminated area used to grow feed, Beef F_gr_dairy a,b Fraction of grain plant type from contaminated area used to grow feed, Dairy F_gr_egg a,b Fraction of grain plant type from contaminated area used to grow feed, Eggs F_gr_pork a,b Fraction of grain plant type from contaminated area used to grow feed, Pork F_gr_poultry a,b Fraction of grain plant type from contaminated area used to grow feed, Poultry F_s i_beef a,b Fraction of silage plant type from contaminated area used to grow feed, Beef F_si_dairy a,b Fraction of silage plant type from contaminated area used to grow feed, Dairy F_si_pork a,b Fraction of silage plant type from contaminated area used t o grow feed, Pork F_T3 Fraction of fish intake that is from T3 F_T4 Fraction of fish intake that is from T4 FC_beef a,b Fraction contaminated, Beef FC_dairy a,b Fraction contaminated, Dairy FC_egg a,b Fraction contaminated, Eggs FC_ExpFruit a,b Fract ion contaminated, Exposed Fruit FC_ExpVeg a,b Fraction contaminated, Exposed Vegetable FC_Fish a,b Fraction contaminated, Fish FC_pork a,b Fraction contaminated, Pork FC_poultry a,b Fraction contaminated, Poultry FC_ProFruit a,b Fraction contaminated, Protected Fruit FC_ProVeg a,b Fraction contaminated, Protected Vegetable FC_RootVeg a,b Fraction contaminated, Root Vegetable FC_Soil a,b Fraction contaminated, Soil IR_beef_adlt Ingestion rate, Beef, Adult 20

- 70 IR_beef_ch1 Ingestion rate, Beef, Chi ld 1

- 2Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 23 

### Exhibit 13 . Variables Included in the Systematic Sensitivity Analysis

Variable Name Variable Description
IR_beef_ch2 Ingestion rate, Beef, Child 3

- 5 IR_beef_ch3 Ingestion rate, Beef, Child 6

- 11 IR_beef_ch4 Ingestion rate, Beef, Child 12

- 19 IR_dairy_adlt Ingestion rate, Dairy, Adult 20

- 70 IR_dairy_ch1 Ingestion rate, Dairy, Child 1

- 2 IR_dairy_ch2 Ingestion rate, Dairy, Child 3

- 5 IR_dairy_ch3 Ingestion rate, Dairy, Child 6

- 11 IR_dairy_ch4 Ingestion rate, Dairy, Child 12

- 19 IR_egg_adlt Ingestion rate, Eggs, Adult 20

- 70 IR_egg_ch1 Ingestion rate, Eggs, Child 1

- 2 IR_egg_ch2 Ingestion rate, Eggs, C hild 3

- 5 IR_egg_ch3 Ingestion rate, Eggs, Child 6

- 11 IR_egg_ch4 Ingestion rate, Eggs, Child 12

- 19 IR_ExpFruit_adlt Ingestion rate, Exposed Fruit, Adult 20

- 70 IR_ExpFruit_ch1 Ingestion rate, Exposed Fruit, Child 1

- 2 IR_ExpFruit_ch2 Ingestion rate, Expo sed Fruit, Child 3

- 5 IR_ExpFruit_ch3 Ingestion rate, Exposed Fruit, Child 6

- 11 IR_ExpFruit_ch4 Ingestion rate, Exposed Fruit, Child 12

- 19 IR_ExpVeg_adlt Ingestion rate, Exposed Vegetable, Adult 20

- 70 IR_ExpVeg_ch1 Ingestion rate, Exposed Vegetable, Chi ld 1

- 2 IR_ExpVeg_ch2 Ingestion rate, Exposed Vegetable, Child 3

- 5 IR_ExpVeg_ch3 Ingestion rate, Exposed Vegetable, Child 6

- 11 IR_ExpVeg_ch4 Ingestion rate, Exposed Vegetable, Child 12

- 19 IR_Fish_adlt Ingestion rate, Fish, Adult 20

- 70 IR_Fish_ch1 Inges tion rate, Fish, Child 1

- 2 IR_Fish_ch2 Ingestion rate, Fish, Child 3

- 5 IR_Fish_ch3 Ingestion rate, Fish, Child 6

- 11 IR_Fish_ch4 Ingestion rate, Fish, Child 12

- 19 IR_pork_adlt Ingestion rate, Pork, Adult 20

- 70 IR_pork_ch1 Ingestion rate, Pork, Child 1

- 2 IR_pork_ch2 Ingestion rate, Pork, Child 3

- 5 IR_pork_ch3 Ingestion rate, Pork, Child 6

- 11 IR_pork_ch4 Ingestion rate, Pork, Child 12

- 19 IR_poultry_adlt Ingestion rate, Poultry, Adult 20

- 70 IR_poultry_ch1 Ingestion rate, Poultry, Child 1

- 2 IR_poultry

_ch2 Ingestion rate, Poultry, Child 3

- 5 IR_poultry_ch3 Ingestion rate, Poultry, Child 6

- 11 IR_poultry_ch4 Ingestion rate, Poultry, Child 12

- 19 IR_ProFruit_adlt Ingestion rate, Protected Fruit, Adult 20

- 70 IR_ProFruit_ch1 Ingestion rate, Protected Fruit , Child 1

- 2 IR_ProFruit_ch2 Ingestion rate, Protected Fruit, Child 3

- 5 IR_ProFruit_ch3 Ingestion rate, Protected Fruit, Child 6

- 11 IR_ProFruit_ch4 Ingestion rate, Protected Fruit, Child 12

- 19 IR_ProVeg_adlt Ingestion rate, Protected Vegetable, Adult 20

- 70 IR_ProVeg_ch1 Ingestion rate, Protected Vegetable, Child 1

- 2Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 24 

### Exhibit 13 . Variables Included in the Systematic Sensitivity Analysis

Variable Name Variable Description
IR_ProVeg_ch2 Ingestion rate, Protected Vegetable, Child 3

- 5 IR_ProVeg_ch3 Ingestion rate, Protected Vegetable, Child 6

- 11 IR_ProVeg_ch4 Ingestion rate, Protected Vegetable, Child 12

- 19 IR_RootVeg_adlt Ingestion rate, Root Vegetable, Adult 20

- 70 IR_RootVeg_ch1 Ingestion rate, Root Vegetable, Child 1

- 2 IR_RootVeg_ch2 Ingestion rate, Root Vegetable, Child 3

- 5 IR_RootVeg_ch3 Ingestion rate, Root Vegetable, Child 6

- 11 IR_RootVeg_ch4 Inges tion rate, Root Vegetable, Child 12

- 19 IR_Soil_adlt Ingestion rate, Soil, Adult 20

- 70 IR_Soil_ch1 Ingestion rate, Soil, Child 1

- 2 IR_Soil_ch2 Ingestion rate, Soil, Child 3

- 5 IR_Soil_ch3 Ingestion rate, Soil, Child 6

- 11 IR_Soil_ch4 Ingestion rate, Soil , Child 12

- 19 IR_water_adlt Ingestion rate, Water, Adult 20

- 70 IR_water_ch1 Ingestion rate, Water, Child 1

- 2 IR_water_ch2 Ingestion rate, Water, Child 3

- 5 IR_water_ch3 Ingestion rate, Water, Child 6

- 11 IR_water_ch4 Ingestion rate, Water, Child 12

- 19

a Values cannot be increased by 5% because the variable has an upper bound.

b Values cannot be increased by 50% because the variable has an upper bound.

c Values can only be increased by 5% for 2,3,7,8

– TCDD and Benzo[a]Pyrene because the variable has an upper bound.

d Values can only be increased by 5% for Benzo[a]Pyrene because the variable has an upper bound.

e Values can only be increased by 50% for Benzo[a]Pyrene because the variable has an upper bound.

f Values can only be increased by 5% for Benzo[a ]Pyrene, 2,3,7,8

- TCDD, and methyl mercury because the variable has an upper bound.

g Values can only be increased by 5% for Benzo[a]Pyrene, 2,3,7,8

- TCDD, and methyl mercury because the variable has an upper bound.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 25 

### Exhibit 14 . Elasticities and Rankings for the Variables with the Highest Elasticities for Benzo[a]Pyrene

Name of Variable Changed Variable Definition Variable Category a Elasticity of Risk for Input

Variable Perturbation Ranking of Elasticity for Input Variable P erturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%
MixHeight Mixing Height TRIM

- 1.97

- 1.05

- 0.95

- 0.66 1 1 2 2
EmissionRate Emission Rate of all Chemicals TRIM 1.00 1.00 1.00 1.00 3 2 1 1 HorizWindSpeed Horizontal Wind Speed TRIM

- 1.74

- 0.97

- 0.88

- 0.63 2 3 3 3
Rain Annual Rainfall TRIM 0.63 0.63 0.63 0.63 5 4 4 4
Drwp Average annual wet deposition of

particle

- phase chemical FFC 0.45 0.45 0.45 0.45 6 5 5 5

Fw Fraction of wet deposition that

adheres to plant surfaces FFC 0.45 0.45 0.45 0.45 7 6 6 6

MF M ammalian metabolism factor FFC 0.41 0.41 0.41 0.41 9 7 7 7
Yp_fo Yield or standing crop biomass, Forage FFC

- 0.69

- 0.36

- 0.33

- 0.23 4 8 10 12

Rp_fo Interception fraction of the edible

portion of plant, Forage FFC 0.34 0.34 0.34 0.34 10 9 8 8

Ba_dairy Ch emical

- specific biotransfer factor, Dairy FFC 0.34 0.34 0.34 0.34 12 10 9 9
EF_dairy Exposure factor, Dairy Ing./BW 0.34 0.34 N/A N/A 13 11 FC_dairy Fraction contaminated, Dairy Ing./BW 0.34 0.34 N/A N/A 14 12
Drdp Average annual dry deposition of

p article

- phase chemical FFC 0.30 0.30 0.30 0.30 16 13 11 10

Qp_fo_dairy Quantity of forage plant type

eaten per animal per day, Dairy FFC 0.29 0.29 0.29 0.29 18 14 12 11

F_fo_dairy Fraction of forage plant type

obtained from contaminated area used to grow feed, Dairy Ing./BW 0.29 0.29 N/A N/A 17 15

Kp_fo Plant surface loss coefficient, Forage FFC

- 0.34

- 0.25

- 0.24

- 0.19 11 16 13 15

Yp_ef Yield or standing crop biomass, Exposed Fruit FFC

- 0.43

- 0.23

- 0.20

- 0.14 8 17 16 17

100

- MAF_ef 100

- Moisture adju stment factor, Exposed Fruit FFC 0.22 0.22 0.22 0.22 22 18 14 13
EF_ExpFruit Exposure factor, Exposed Fruit Ing./BW 0.22 0.22 N/A N/A 20 19Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 26 

### Exhibit 14 . Elasticities and Rankings for the Variables with the Highest Elasticities for Benzo[a]Pyrene

Name of Variable Changed Variable Definition Variable Category a Elasticity of Risk for Input

Variable Perturbation Ranking of Elasticity for Input Variable P erturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%

FC_ExpFruit Fraction contaminated, Exposed Fruit Ing./BW 0.22 0.22 N/A N/A 21 20

Rp_ef Interception fraction of the edible

portion of plant, Exposed Fruit FFC 0.21 0.21 0.21 0.21 23 21 15 14

Kp_ef Plant surface loss coefficient, Exposed Fruit FFC

- 0.27

- 0.19

- 0.17

- 0.13 19 22 17 18

Yp_ev Yield or standing crop biomass,

Exposed Vegetable FFC

- 0.33

- 0.17

- 0.16

- 0 .11 15 23 19 21

100

- MAF_ev 100

- Moisture adjustment factor, Exposed Vegetable FFC 0.17 0.17 0.17 0.17 26 24 18 16

EF_ExpVeg Exposure factor, Exposed Vegetables Ing./BW 0.17 0.17 N/A N/A 27 25

FC_ExpVeg Fraction contaminated, Exposed Vegetable Ing./BW 0.17 0.17 N/A N/A 28 26

Rp_ev Interception fraction of the edible

portion of plant, Exposed Vegetable FFC 0.16 0.16 N/A N/A 29 27

Kp_ev Plant surface loss coefficient,

Exposed Vegetable FFC

- 0.21

- 0.14

- 0.13

- 0.10 24 28 20 25

C_Soil Concentration o f chemical in soil

from contaminated area FFC 0.12 0.12 0.12 0.12 31 29 21 19
EF_Soil Exposure factor, Soil Ing./BW 0.12 0.12 N/A N/A 32 30 FC_Soil Fraction contaminated, Soil Ing./BW 0.12 0.12 N/A N/A 33 31 IR_dairy_ch1 Ingestion rate, Dairy, Child 1

- 2 Ing./BW 0.11 0.11 0.11 0.11 34 32 22 20
IR_ExpFruit_adlt Ingestion rate, Exposed Fruit, Adult 20

- 70 Ing./BW 0.10 0.10 0.10 0.10 35 33 23 23

Tp_fo Length of plant exposure to

deposition per harvest, Forage FFC 0.17 0.10 0.09 0.06 25 34 26 31
IR_dair y_adlt Ingestion rate, Dairy, Adult 20

- 70 Ing./BW 0.10 0.10 0.10 0.10 36 35 24 24 L2_ExpFruit Loss type 2, Exposed Fruit FFC

- 0.10

- 0.10

- 0.10

- 0.10 37 36 25 26

a FFC refers to farm food chain variables and Ing./BW refers to ingestion and body weight var iables.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 27 

### Exhibit 15 . Elasticities and Rankings for the Variables with the Highest Elasticities for 2,3,7,8

- TCDD

Name of Variable Changed Variable Definition Variable Category a Elasticity of Risk for Input

Variable Pertu rbation Ranking of Elasticity for Input Variable Perturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%
MixHeight Mixing Height TRIM

- 1.99

- 1.05

- 0.95

- 0.67 1 1 2 2
EmissionRate Emission Rate of all Chemicals TRIM 1.00 1.00 1.00 1.00 3 2 1 1 HorizWindSpeed Ho rizontal Wind Speed TRIM

- 1.80

- 0.96

- 0.87

- 0.61 2 3 3 3 FC_Fish Fraction contaminated, Fish Ing./BW 0.56 0.56 N/A N/A 8 4 EF_Fish Exposure factor, Fish Ing./BW 0.56 0.56 N/A N/A 7 5 BW_adlt Body weight, Adult 20

- 70 Ing./BW

- 0.86

- 0.45

- 0.41

- 0.29 4 6 6 11
C_FishT4 Concentration of chemical in whole fish for T4 fish FFC 0.43 0.43 0.43 0.43 9 7 4 5
IR_Fish_adlt Ingestion rate, Fish, Adult 20

- 70 Ing./BW 0.43 0.43 0.43 0.43 10 8 5 6
MF Mammalian metabolism factor FFC 0.43 0.43 N/A N/A 11 9
SurfWat Temp Water Temperature TRIM 0.32 0.39 0.41 0.53 16 10 7 4 WatOCC Water

- Organic Carbon Fraction TRIM

- 0.62

- 0.38

- 0.35

- 0.25 5 11 9 14
SedDepVel Sediment Deposition Velocity and Resuspension Velocity TRIM 0.28 0.36 0.39 0.30 20 12 8 8

Ba_dairy Chemical

- specific biotransfer factor, Dairy FFC 0.32 0.32 0.32 0.32 13 13 10 7
EF_dairy Exposure factor, Dairy Ing./BW 0.32 0.32 N/A N/A 14 14 FC_dairy Fraction contaminated, Dairy Ing./BW 0.32 0.32 N/A N/A 15 15
F_T3 Fraction of fish intake that is from T3 Ing./BW

- 0.30

- 0.30

- 0.30

- 0.30 17 16 12 10

F_T4 Fraction of fish intake that is from T4 Ing./BW 0.30 0.30 0.30 0.30 18 17 11 9

Yp_fo Yield or standing crop biomass, Forage FFC

- 0.56

- 0.30

- 0.27

- 0.19 6 18 15 19

Rp_fo Interception fraction of the edible

portion of plant, Forage FFC 0.28 0.28 0.28 0.28 19 19 13 12

Drdp Average annual dry deposition of

particle

- phase chemical FFC 0.28 0.28 0.28 0.28 22 20 14 13

WatSuspSed Water

- Suspended Sediment Concentration TRIM

- 0.37

- 0.25

- 0.24

- 0.19 12 21 16 18Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 28 

### Exhibit 15 . Elasticities and Rankings for the Variables with the Highest Elasticities for 2,3,7,8

- TCDD

Name of Variable Changed Variable Definition Variable Category a Elasticity of Risk for Input

Variable Pertu rbation Ranking of Elasticity for Input Variable Perturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%

Q p_fo_dairy Quantity of forage plant type

eaten per animal per day, Dairy FFC 0.23 0.23 0.23 0.23 24 22 17 15

F_fo_dairy Fraction of forage plant type

obtained from contaminated area used to grow feed, Dairy Ing./BW 0.23 0.23 N/A N/A 23 23

Kp_fo Plant s urface loss coefficient, Forage FFC

- 0.28

- 0.21

- 0.20

- 0.16 21 24 19 21
IR_dairy_adlt Ingestion rate, Dairy, Adult 20

- 70 Ing./BW 0.20 0.20 0.20 0.20 25 25 18 16
Rain Annual Rainfall TRIM 0.20 0.20 0.20 0.19 26 26 20 17 SurfSoilAir Surface Soil

- Fraction Air TRIM 0.13 0.14 0.15 0.17 29 27 21 20
C_FishT3 Concentration of chemical in whole fish for T3 fish FFC 0.13 0.13 0.13 0.13 28 28 22 22

Cs_S_animal_ing est Chemical concentration in

surface soil in contaminated area where livestock feed FFC 0.12 0.12 0 .12 0.12 31 29 23 23

Bs Soil bioavailability factor for livestock FFC 0.12 0.12 N/A N/A 30 30

Ba_beef Chemical

- specific biotransfer factor, Beef FFC 0.09 0.09 0.09 0.09 33 31 24 24
EF_beef Exposure factor, Beef Ing./BW 0.09 0.09 N/A N/A 34 32 FC_be ef Fraction contaminated, Beef Ing./BW 0.09 0.09 N/A N/A 35 33
Tp_fo Length of plant exposure to

deposition per harvest, Forage FFC 0.14 0.08 0.08 0.05 27 34 25 29

Qs_dairy Quantity of soil eaten by the

animal each day, Dairy FFC 0.07 0.07 0.07 0.07 38 35 26 25

a FFC refers to farm food chain variables and Ing./BW refers to ingestion and body weight variables.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 29 

### Exhibit 16 . Elasticities and Rankings for the Variables with the Highest Elasticities for Cadmium

Name of Varia ble Changed Variable Definition Variable Category a Elasticity of Risk for Input

Variable Perturbation Ranking of Elasticity for Input Variable Perturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%
MixHeight Mixing Height TRIM

- 1.92

- 1.03

- 0.93

- 0.66 1 1 2 3 HorizWindSpeed Horizontal Wind Speed TRIM

- 1.92

- 1.03

- 0.93

- 0.66 2 2 3 4
EmissionRate Emission Rate of all Chemicals TRIM 1.00 1.00 1.00 1.00 3 3 1 1
Rain Annual Rainfall TRIM 0.78 0.75 0.74 0.71 4 4 4 2
Cs_root_zone_pr oduce Average chemical concentrat ion

in soil at root

- zone depth in produce

- growing area FFC 0.63 0.63 0.63 0.63 5 5 5 5

Br_AG_produce_ pf Plant

- soil chemical

bioconcentration factor, Protected

Fruit FFC 0.39 0.39 0.39 0.39 7 6 6 8

IR_ProFruit_ch1 Ingestion rate, Protected Fruit, Child 1

- 2 Ing./BW 0.39 0.39 0.39 0.39 10 7 7 9
EF_ProFruit Exposure factor, Protected Fruit Ing./BW 0.39 0.39 N/A N/A 8 8
FC_ProFruit Fraction contaminated, Protected Fruit Ing./BW 0.39 0.39 N/A N/A 9 9

100

- MAF_pf 100

- Moisture adjustment factor, Protected Fruit FFC 0.39 0.39 0.39 0.39 11 10 8 7
BW_ch1 Body weight, Child 1

- 2 Ing./BW

- 0.54

- 0.28

- 0.26

- 0.18 6 11 11 13
EroRate Erosion Rate for all Parcels TRIM

- 0.31

- 0.27

- 0.26

- 0.24 12 12 10 10 SurfWatTemp Water Temperature TRIM 0.17 0.27 0.30 0.54 16 13 9 6 IR_Fish_ch1 Ingestion rate, Fish, Child 1

- 2 Ing./BW 0.19 0.19 0.19 0.19 15 14 12 12 EF_Fish Exposure factor, Fish Ing./BW 0.19 0.19 N/A N/A 13 15 FC_Fish Fraction contaminated, Fish Ing./BW 0.19 0.19 N/A N/A 14 16 SurfSoilAir Surface Soil

- Frac tion Air TRIM 0.15 0.17 0.17 0.19 19 17 13 11 L1_ProFruit Loss type 1, Protected Fruit FFC

- 0.16

- 0.16

- 0.16

- 0.16 18 18 14 14
C_FishT3 Concentration of chemical in whole fish for T3 fish FFC 0.15 0.15 0.15 0.15 21 19 15 15

WatRetTime Rentention Time in Pond TRIM 0.16 0.15 0.14 0.13 17 20 17 16
SedDepVel Sediment Deposition Velocity and Resuspension Velocity TRIM 0.10 0.13 0.14 0.07 30 21 16 32Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 30 

### Exhibit 16 . Elasticities and Rankings for the Variables with the Highest Elasticities for Cadmium

Name of Varia ble Changed Variable Definition Variable Category a Elasticity of Risk for Input

Variable Perturbation Ranking of Elasticity for Input Variable Perturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%

100

- MAF_ev 100

- Moisture adjustment factor, Exposed Vegetable FFC 0.11 0.11 0.11 0.11 23 22 18 18

IR_ExpVeg _ch1 Ingestion rate, Exposed Vegetable, Child 1

- 2 Ing./BW 0.11 0.11 0.11 0.11 26 23 19 19

EF_ExpVeg Exposure factor, Exposed Vegetables Ing./BW 0.11 0.11 N/A N/A 24 24

FC_ExpVeg Fraction contaminated, Exposed Vegetable Ing./BW 0.11 0.11 N/A N/A 25 25

F_T3 Fraction of fish intake that is from T3 Ing./BW 0.11 0.11 0.11 0.11 28 26 20 20

F_T4 Fraction of fish intake that is from T4 Ing./BW

- 0.11

- 0.11

- 0.11

- 0.11 29 27 21 21

SurfSoilOCC Surface Soil

- Organic Carbon Fraction TRIM 0.15 0.10 0.10 0.08 20 28 22 25

SurfSoilVertVel Surface Soil

- Average vertical

velocity of water (percolation) TRIM

- 0.11

- 0.10

- 0.10

- 0.09 27 29 23 22
SurfSoilpH Surface Soil

- pH TRIM 0.13 0.09 0.09 0.07 22 30 25 31

a FFC refers to farm food chain variables and Ing./BW refer s to ingestion and body weight variables.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 31 

### Exhibit 17 . Elasticities and Rankings for the Variables with the Highest Elasticities for Divalent Mercury

Name of Variable Changed Variable Definition Variable Category a Elastici ty of Risk for Input

Variable Perturbation Ranking of Elasticity for Input Variable Perturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%

EmissionRate Emission Rate of all Chemicals TRIM 1.00 1.00 1.00 1.00 5 1 1 1 MixHeight Mixing Height TRIM

- 1.73

- 0.97

- 0. 89

- 0.63 1 2 2 3 HorizWindSpeed Horizontal Wind Speed TRIM

- 1.73

- 0.97

- 0.89

- 0.63 2 3 3 4
EroRate Erosion Rate for all Parcels TRIM

- 1.27

- 0.77

- 0.71

- 0.52 3 4 5 7
Rain Annual Rainfall TRIM 0.76 0.74 0.74 0.71 6 5 4 2 BW_ch1 Body weight, Child 1

- 2 Ing ./BW

- 1.17

- 0.61

- 0.56

- 0.39 4 6 8 8
C_Soil Concentration of chemical in soil

from contaminated area FFC 0.56 0.56 0.56 0.56 7 7 6 5
EF_Soil Exposure factor, Soil Ing./BW 0.56 0.56 N/A N/A 8 8 FC_Soil Fraction contaminated, Soil Ing./BW 0.56 0.56 N/A N/A 9 9 IR_Soil_ch1 Ingestion rate, Soil, Child 1

- 2 Ing./BW 0.56 0.56 0.56 0.56 10 10 7 6
Cs_root_zone_pr oduce Average chemical concentration

in soil at root

- zone depth in produce

- growing area FFC 0.33 0.33 0.33 0.33 11 11 9 9

Br_AG_produce_ pf Plant

- s oil chemical

bioconcentration factor, Protected

Fruit FFC 0.15 0.15 0.15 0.15 12 12 10 10

IR_ProFruit_ch1 Ingestion rate, Protected Fruit, Child 1

- 2 Ing./BW 0.15 0.15 0.15 0.15 15 13 11 11

100

- MAF_pf 100

- Moisture adjustment factor, Protected Fruit FFC 0.15 0.15 0.15 0.15 16 14 12 12
EF_ProFruit Exposure factor, Protected Fruit Ing./BW 0.15 0.15 N/A N/A 13 15
FC_ProFruit Fraction contaminated, Protected Fruit Ing./BW 0.15 0.15 N/A N/A 14 16

SurfSoilAir Surface Soil

- Fraction Air TRIM 0.11 0.13 0.1 3 0.15 17 17 13 13

Br_AG_rootveg Plant

- soil chemical

bioconcentration factor, Root Vegetables FFC 0.11 0.11 0.11 0.11 18 18 14 15

IR_RootVeg_ch1 Ingestion rate, Root Vegetable, Child 1

- 2 Ing./BW 0.11 0.11 0.11 0.11 21 19 15 16Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 32 

### Exhibit 17 . Elasticities and Rankings for the Variables with the Highest Elasticities for Divalent Mercury

Name of Variable Changed Variable Definition Variable Category a Elastici ty of Risk for Input

Variable Perturbation Ranking of Elasticity for Input Variable Perturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%

100

- MAF_rv 100

- Moisture adjustment factor, Root Vegetable FFC 0.11 0.11 0.11 0.11 23 20 16 17
EF_RootVeg Exposure factor, Root Vegetables Ing./BW 0.11 0.11 N/A N/A 19 21
FC_RootVeg Fraction contaminated, Root Vegetable Ing./BW 0.11 0.11 N/A N/A 20 22

VG_rootveg Empirical c orrection factor, Root Vegetable FFC 0.11 0.11 N/A N/A 22 23

Cs_S_animal_ing est Chemical concentration in

surface soil in contaminated area where livestock feed FFC 0.08 0.08 0.08 0.08 25 24 17 18

Bs Soil bioavailability factor for livestock FFC 0.08 0 .08 N/A N/A 24 25
L1_ProFruit Loss type 1, Protected Fruit FFC

- 0.06

- 0.06

- 0.06

- 0.06 26 26 19 19
SedDepVel Sediment Deposition Velocity and Resuspension Velocity TRIM 0.02 0.05 0.06 0.11 48 27 18 14

Ba_egg Chemical

- specific biotransfer factor, Eggs FFC 0.05 0.05 0.05 0.05 27 28 20 20
IR_egg_ch1 Ingestion rate, Eggs, Child 1

- 2 Ing./BW 0.05 0.05 0.05 0.05 30 29 21 21 EF_egg Exposure factor, Eggs Ing./BW 0.05 0.05 N/A N/A 28 30 FC_egg Fraction contaminated, Eggs Ing./BW 0.05 0.05 N/A N/A 29 31

Q s_egg Quantity of soil eaten by the

animal each day, Eggs FFC 0.05 0.05 0.05 0.05 31 32 22 22

Ba_poultry Chemical

- specific biotransfer factor, Poultry FFC 0.03 0.03 0.03 0.03 32 33 23 23
IR_poultry_ch1 Ingestion rate, Poultry, Child 1

- 2 Ing./BW 0.03 0.03 0.03 0.03 35 34 24 24 EF_poultry Exposure factor, Poultry Ing./BW 0.03 0.03 N/A N/A 33 35 FC_poultry Fraction contaminated, Poultry Ing./BW 0.03 0.03 N/A N/A 34 36
Qs_poultry Quantity of soil eaten by the

animal each day, Poultry FFC 0.03 0.03 0.03 0.03 36 37 25 25

a FFC refers to farm food chain variables and Ing./BW refers to ingestion and body weight variables.Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 33 

### Exhibit 18 . Elasticities and Rankings for the Variables with the Highest Elasticities for Methyl Mercur y

Name of Variable Changed Variable Definition Variable Category a Elasticity of Risk for Input

Variable Perturbation Ranking of Elasticity for Input Variable Perturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%

SedDepVel Sediment Deposition Velocity and Res uspension Velocity TRIM 0.78 1.56 2.01 3.67 9 1 1 1
BW_ch1 Body weight, Child 1

- 2 Ing./BW

- 1.91

- 1.00

- 0.91

- 0.64 1 2 3 4
EmissionRate Emission Rate of all Chemicals TRIM 1.00 1.00 1.00 1.00 5 3 2 2 IR_Fish_ch1 Ingestion rate, Fish, Child 1

- 2 Ing./BW 0. 90 0.90 0.90 0.90 8 4 4 3 FC_Fish Fraction contaminated, Fish Ing./BW 0.90 0.90 N/A N/A 7 5 EF_Fish Exposure factor, Fish Ing./BW 0.90 0.90 N/A N/A 6 6 MixHeight Mixing Height TRIM

- 1.02

- 0.70

- 0.66

- 0.51 3 7 5 8 HorizWindSpeed Horizontal Wind Spee d TRIM

- 1.01

- 0.70

- 0.65

- 0.51 4 8 6 9
Rain Annual Rainfall TRIM 0.70 0.64 0.63 0.60 10 9 7 6
C_FishT4 Concentration of chemical in whole fish for T4 fish FFC 0.55 0.55 0.55 0.55 12 10 8 7

EroRate Erosion Rate for all Parcels TRIM

- 0.57

- 0.45

- 0.43

- 0.3 5 11 11 10 11 SedPorosity Sediment Porosity TRIM

- 0.30

- 0.40

- 0.43

- 0.60 15 12 9 5
C_FishT3 Concentration of chemical in whole fish for T3 fish FFC 0.36 0.36 0.36 0.36 13 13 11 10
SurfWatTemp Water Temperature TRIM

- 0.22

- 0.22

- 0.22

- 0.21 18 14 12 12

F _T3 Fraction of fish intake that is from T3 Ing./BW

- 0.19

- 0.19

- 0.19

- 0.19 19 15 13 13

F_T4 Fraction of fish intake that is from T4 Ing./BW 0.19 0.19 0.19 0.19 20 16 14 14

WatSuspSed Water

- Suspended Sediment Concentration TRIM

- 0.32

- 0.18

- 0.16

- 0.12 1 4 17 15 16

SurfSoilAir Surface Soil

- Fraction Air TRIM 0.14 0.14 0.15 0.15 21 18 16 15
WatRetTime Rentention Time in Pond TRIM 0.23 0.14 0.13 0.09 17 19 17 17

FishMass Fish Body Weight for all Aquatic Species TRIM 0.10 0.07 0.07 0.06 22 20 19 19

Runoff Total Water Runoff Rate TRIM 0.07 0.07 0.07 0.07 23 21 18 18
C_Soil Concentration of chemical in soil

from contaminated area FFC 0.05 0.05 0.05 0.05 24 22 20 20Attachment 3 to Technical Support Document for TRIM-Based Multipathway Screening Scenario for RTR 3- 34 

### Exhibit 18 . Elasticities and Rankings for the Variables with the Highest Elasticities for Methyl Mercur y

Name of Variable Changed Variable Definition Variable Category a Elasticity of Risk for Input

Variable Perturbation Ranking of Elasticity for Input Variable Perturbation

- 50%

- 5% 5% 50%

- 50%

- 5% 5% 50%
IR_Soil_ch1 Ingestion rate, Soil, Child 1

- 2 Ing./BW 0.05 0.05 0.05 0.05 27 23 21 21 EF_Soil Exposure factor, Soil Ing./BW 0.05 0.05 N/A N/A 25 24 FC_Soil Fraction contaminated, Soil Ing./BW 0.05 0.05 N/A N/A 26 25
Cs_root_zone_pr oduce Average chemical concentration

in soil at root

- zone depth in produce

- growing area FFC 0.04 0.04 0.04 0.04 28 26 22 22

100

- MAF_pf 100

- Moisture adjustment factor, Protected Fruit FFC 0.03 0.03 0.03 0.03 33 27 25 23

Br_AG_produce_ pf Plant

- soil chemical

bioconcentration factor, Protected

Fruit FFC 0.03 0.03 0.03 0.03 29 28 23 24

IR_ProFruit_ch1 Ingestion rate , Protected Fruit, Child 1

- 2 Ing./BW 0.03 0.03 0.03 0.03 32 29 24 25

a FFC refers to farm food chain variables and Ing./BW refers to ingestion and body weight variables.