Air Dispersion Evaluation Report for Happy Valley South RFI Site, Santa Susana Field Laboratory, Ventura County, California

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2 Appendix E Air Dispersion Evaluation Report for Happy Valley South RFI Site, Santa Susana Field Laboratory, Ventura County, California Prepared for The Boeing Company December 2014

3 Contents Section Page Abbreviations and Acronyms... v 1 Introduction Synopsis of Approach Happy Valley South RFI Site Characteristics Wind Impacts Source Characteristics Evaluation of Air Dispersion HVS Buildings Results and Conclusions Works Cited Figures E.1-1 E.2-1 E.3-1 E.3-2 E.3-3 E.3-4 Attachment Site Layout Wind Rose at Happy Valley South Location Cumulative Particle Deposition Contours for Six Representative Sources Air Dispersion Modeling Results Metals Data Happy Valley South Air Dispersion Modeling Results Dioxins/Furans Data Happy Valley South Air Dispersion Modeling Results PAHs Data Happy Valley South E-1 Soil Calculations for Energetics Testing Sources ES BAO DRAFT iii

4 Acronyms and Abbreviations Boeing DTSC g/g HMX HVS MWH PAH RCRA RDX RFI SCL SSFL The Boeing Company California Environmental Protection Agency, Department of Toxic Substances Control gram per gram 1,3,5,7-tetranitro-1,3,5,7-tetrazocane Happy Valley South Montgomery Watson Harza polycyclic aromatic hydrocarbon Resource Conservation and Recovery Act 1,3,5-trinitroperhydro-1,3,5-triazine Resource Conservation and Recovery Act facility investigation soil characterization level Santa Susana Field Laboratory ES BAO DRAFT v

5 SECTION 1 Introduction The Santa Susana Field Laboratory (SSFL) is located approximately 30 miles northwest of downtown Los Angeles, California, in the southeast corner of Ventura County. The SSFL occupies approximately 2,850 acres of hilly terrain with approximately 1,100 feet of topographic relief. The Boeing Company (Boeing) predecessors began SSFL operations in the 1940s. The SSFL was divided into four administrative areas based on ownership and operations (Areas I, II, III, and IV) and includes undeveloped land areas to both the north and south, as shown on Figure E.1-1. Principal operations in Areas I, II, and III included research, development, and testing of rocket engines and propulsion systems by Boeing and National Aeronautics and Space Administration. Principal operations in Area IV included energy technology research for the United States Department of Energy. The northern and southern undeveloped lands of the SSFL are owned by Boeing and were not used for industrial activities. The Boeing Happy Valley South (HVS) Resource Conservation and Recovery Act (RCRA) facility investigation (RFI) site is located in the eastern portion of SSFL in Administrative Area I in Boeing RFI Subarea 1A South. The operational area of the HVS RFI site is approximately 12.7 acres. The HVS RFI site was used as a solid propellants test and research facility that operated from the mid-1950s to Air dispersion modeling of six Boeing sources that are representative of the range of Boeing operations at SSFL has been performed to predict patterns of deposition onto the soil and to determine whether previous soil sampling data are sufficient to evaluate the extent of the potential soil contamination through the air dispersion/deposition pathway (CH2M HILL, 2013a-d, 2014a-b). In cases where it was determined that previous soil sampling data are not sufficient, the modeling results aided in the identification of proposed soil sampling locations. The impact footprints from the six sources were calculated using the CALPUFF/CALMET modeling methodology (CH2M HILL 2013a-d, 2014a-b). This methodology projects a detailed terrain elevation grid and a 3-dimensional wind field over the entire footprint of the SSFL and can be applied to other sources to identify possible sampling locations to assess deposition impacts to soil. This methodology is described in Air Dispersion Evaluation Approach for Other Boeing Sources at the Santa Susana Field Laboratory, Ventura County, California (CH2M HILL, 2014c). This document presents the results of the air dispersion evaluation for the HVS RFI site based on the air dispersion modeling results for similar sources and presents the potential spatial distribution of chemical constituent deposition to soil from former testing activities at the HVS RFI site. The site layout and HVS RFI site location are shown on Figure E Synopsis of Approach The goal of the air dispersion evaluation is to provide insight on the locations where pollutants from combustion sources might be deposited onto the ground and to guide the selection of surface soil sample locations to identify potential deposition impacts from former HVS operations. The previously completed modeling of worst-case air emissions sources has shown that the deposition impacts to soil are localized, as discussed further in this report. The potential impacts at other Boeing sources, such as the energetics or motor testing performed at the HVS buildings, are not expected to be greater than the modeled soil impacts for the worst-case air emissions sources. The same modeling approach has been used to assess other emissions sources, such as energetics testing at former HVS buildings, taking into consideration local winds and topography (CH2M HILL, 2014c). This air dispersion evaluation approach was used to identify possible sampling locations around other sources such as energetics testing at HVS to assess deposition impacts to soil. Other sources considered for evaluation of air deposition are paired with representative source types; the pairing for energetics testing at HVS are discussed in Section 3. The pairings are based on similarity of operations and air emissions characteristics. The following steps are used to apply the results from the representative sources: ES BAO 1-1 DRAFT

6 SECTION 1 INTRODUCTION Evaluate nearby wind rose extracted from the model and topography at the source locations. Identify potential effects of local topography to surface wind flow direction by running the CALPUFF/CALMET model at the location of the other source under study (for example, solid propellants testing at HVS). Use the emissions characteristics of the representative source for this evaluation (for example, the detonation activities at the Building 359 RFI site 1 as representative of worst-case emissions at the HVS buildings). The chemical groups evaluated for each representative and other source are shown in the Air Dispersion Evaluation Approach for Other Boeing Sources at the Santa Susana Field Laboratory, Ventura County, California (CH2M HILL, 2014c). For example, constituents emitted from energetics testing at the Building 359 RFI site (the representative source) are metals, dioxins/furans, and polycyclic aromatic hydrocarbons (PAHs). If the other source under study is the energetics testing performed at HVS, then the constituents evaluated for this source will be metals, dioxins/furans, and PAHs, the same as for Building 359. Prepare deposition contours based on CALPUFF/CALMET modeling results with the representative source emissions placed onto the location of the other source under study. Extract from CALMET a wind rose at the location of the other source under study. Obtain the maximum deposition flux of particulate matter for use in calculating chemical concentrations in soil around the location of the other source under study. Assess potential air deposition impacts: If appropriate data are available, scale the maximum deposition flux from the representative source to the other source under study prior to calculating the chemical concentrations in soil that are expected to result from deposition. Evaluate the distance that modeled deposition impacts to soil decrease to concentrations below corresponding soil characterization levels (SCLs). Compare deposition contours with existing surface soil sampling results and identify data gaps, if any. Where needed based on the evaluation presented above, surface soil sampling locations and target analytes will be proposed in RFI site-specific work plans. 1 Note that the Other Sources approach technical memorandum (CH2M HILL, 2014c) identified the Area I Burn Pit as a representative source for the HVS buildings. Further review of the sources pointed to selection of the Building 359 emissions as a better representative source. This deviation from the other sources air dispersion approach is discussed further in Section ES BAO DRAFT

7 SECTION 2 Happy Valley South RFI Site Characteristics 2.1 Wind Impacts A wind rose for HVS, presented on Figure E.2-1, was generated by extracting hourly CALMET-processed surface meteorological data from the meteorological grid cell closest to the source location. As demonstrated on Figure E.2-1, winds at HVS blow predominantly from the west-northwest and eastsoutheast at typical speeds ranging from about 1 to 11 knots, with a 5-year average hourly wind speed of about 4.2 knots. Higher wind speeds ranging from about 11 to 21 knots constitute no more than 6 percent of winds at HVS. Approximately 2.9 percent of all winds at HVS are considered calm, with speeds less than 1 knot. 2.2 Source Characteristics Operations were documented at the HVS RFI site from the mid-1950s to The HVS RFI Site was used as a solid propellants test and research facility, involving perchlorate, 1,3,5,7-tetranitro-1,3,5,7-tetrazocane (HMX) and 1,3,5-trinitroperhydro-1,3,5-triazine (RDX) (MWH, 2009). Three sources were modeled at this site: Former Building 1372 was used for military flare research and development from 1965 to the 1970s and for gun and solid propellants research and development and small rocket motors testing from the 1970s to In 2002, Building 1372 was demolished and the foundation removed with 2 foot of soil below it to reduce the release of perchlorate to surface water. The Solid Propellant Test Pad at former Building 1745 was the site of testing of small motors with highenergy propellants. Building 1745 was demolished in The former Motor Test Pad at Building 1706 was a propellant test area used for testing beryllium as a solid propellant in 1- and 10-pound sizes, from 1969 to Other chemicals reportedly used in this area included perchlorate, metals, and high-energy fuels such as nitrogen tetraoxide and monomethyl hydrazine. Building 1706 was demolished in Note that the Air Dispersion Evaluation Approach for Other Boeing Sources at the Santa Susana Field Laboratory, Ventura County, California (CH2M HILL, 2014c) had originally identified the Area I Burn Pit as the representative source for the HVS buildings. Based on further review of emissions sources during this evaluation, particularly the identification of HMX and RDX as potential emissions sources, pointed to Building 359 emissions as more representative of the emissions from the HVS buildings. Information is not available regarding the number or frequency of testing or detonation activities at these sites. ES BAO 2-1 DRAFT

8 SECTION 3 Evaluation of Air Dispersion A recommended approach for air dispersion modeling was developed for Boeing as part of the comprehensive data quality objectives for the RFI at the SSFL. That recommended approach was documented in a technical memorandum included as Appendix B to the Comprehensive Data Quality Objectives Report (CH2M HILL, 2013e), which was approved by the California Environmental Protection Agency, Department of Toxic Substances Control (DTSC) in 2013 (DTSC, 2013). Six sources were selected for modeling because they are considered representative of large buoyant area source types (large rocket engine testing, open burning/open detonation disposal, and energetics testing) and large point sources (incineration). These representative sources are: Canyon: Rocket Engine Testing Happy Valley North: Incineration Building 359: Energetics Testing Area I Burn Pit: Open Burning Bowl: Rocket Engine Testing System Testing Laboratory IV: Rocket Engine Testing The previously completed modeling of these air emissions sources has shown that the deposition impacts to soil are localized (Figure E.3-1). The potential impacts at other Boeing sources, such as the energetics and motor testing sources at HVS, are not expected to be greater than the modeled soil impacts for these worstcase air emissions sources (CH2M HILL, 2014c). The air emissions source at HVS were paired with the most appropriate of the representative sources based on similarity of operations and air emissions characteristics. The emissions from the representative source was applied to the HVS sources to identify possible sampling locations to assess deposition impacts to soil. This evaluation process is discussed for the HVS emission sources in the following section. 3.1 HVS Buildings Information is not available describing operating conditions (that is, frequency, duration, or numbers of tests) for testing or detonation activities at Buildings 1372, 1745, or Therefore, emissions from the Building 359 detonation trenches were applied to four locations at these three buildings. The air dispersion modeling methodology and results for Building 359 are presented in a separate air dispersion modeling report (CH2M HILL, 2014b). The following summarizes the information available regarding detonation activities at Building 359. Energetic research using solid propellants was conducted in Building 359 from 1950 to Testing was conducted in four test cells positioned along the northern side of the building. Solid propellants used at the building included perchlorate and other energetic compounds such as HMX and RDX (MWH, 2009). The dimensions of the test cell were 5 feet long, 10 feet wide, and 6.5 feet tall (MWH, 2009). The chemical constituents in emissions from combustion of RDX, HMX, and perchlorate are considered to be reasonably similar, such that RDX could be used as a surrogate for emissions from the other energetic materials. Information was unavailable for the amount of energetic material used per test at Building 359. For purposes of developing conservative emissions estimates, it was estimated that the maximum amount of mass that would be used for this type of testing would be 15 pounds of RDX per testing event; an assumption that was used for Building 359 and has been applied here for the HVS buildings. A 15-pound mass of RDX was considered not to produce damaging blast effects (for example, overpressure that would produce building damage) at a distance of 1/8- to 1/4-mile away. The assumption was that the quantities of energetics detonated in the test stands likely were much lower than the assumed mass used in these emissions calculations. ES BAO 3-1 DRAFT

9 SECTION 3 EVALUATION OF AIR DISPERSION Emissions testing of open detonation of energetics reportedly did not detect dioxins/furans at a detection limit of 2x10-11 gram per gram (g/g). However, emissions testing of open burning of energetics waste indicate that dioxins/furans may be emitted from burning of ammonium perchlorate (Mitchell and Suggs, 1998). Dioxins/furans were consequently considered in evaluating potential air deposition associated with energetics testing at Building 359, and at Buildings 1372, 1745 and The specific congeners are highersubstituted furans (hexa, hepta, and octofurans). The representative minimum quantitation limit emission factor for dioxins/furans is 2x10-10 g/g. This emission factor was used to calculate dioxin/furan concentrations in shallow soil from modeled deposition, as is further discussed in Attachment E-1. Diethylphthalate is the only semivolatile organic compound found in detonation of energetic material, and it was found to be associated with items that were either known to contain phthalates or were likely to contain them. Materials used at the Buildings 1372, 1745 and 1706 locations are not known to contain phthalates. Further, consistent with detonation theory, no semivolatile organic compounds attributable to molecular rearrangement reactions of the energetic molecule were found (Mitchell and Suggs, 1998). PAHs were assessed using emission factors that were based on the detection limits in the emissions testing. Benzo(a)pyrene was used as a surrogate for all carcinogenic PAHs in calculating soil concentrations because it has the lowest SCL. Using benzo(a)pyrene provided a conservative assessment of potential deposition impacts from carcinogenic PAHs (see Attachment F-1). The highest emission factor for carcinogenic PAHs is 9.8 x 10-7 g/g for benzo(a)anthracene, which is conservatively based on the detection limit during emissions testing. This emission factor was used to calculate PAH concentrations in shallow soil from modeled deposition. Metals emissions are principally associated with open detonation (Mitchell and Suggs, 1998). The metals reported in emissions testing include aluminum, barium, cadmium, copper, lead, titanium, and zinc. Metals selected for evaluating potential deposition impacts based on emission testing data for energetic materials and prior investigation results include aluminum, barium, copper, lead, and zinc. Representative minimum quantitation limit emission factors obtained from Mitchell and Suggs, 1998, were used to calculate metals concentrations in soil from modeled deposition, as shown in Attachment E-1. In addition, beryllium reportedly was used in testing at Building Therefore, an additional calculation for beryllium was included in Attachment E-1. Beryllium emissions were not estimated for open burning/open detonation operations and are not included in Mitchell and Suggs, Therefore, the emission factor for aluminum in aluminized ammonium perchlorate propellant was used to estimate emissions of beryllium, and resulting concentrations in soil from operations in Building The modeled deposition pattern for the HVS building locations, as determined using CALPUFF and based on emissions from the representative source area, are shown on Figures E.3-2 through E.3-4. The contours shown on Figure E.3-2 through E.3-4 represent 75 percent, 50 percent, 25 percent, and 15 percent of the maximum deposition flux, respectively, and therefore, the maximum concentrations in soil. As shown on Figures E.3-2 through E.3-4, burning operations produce the highest deposition fluxes and concentrations in soil closest to the source location, with progressively lower fluxes and concentrations at greater distances from the source. Figures E.3-2, E.3-3, and E.3-4 also present the analytical data for soil samples in the upper 2 feet of soil for metals, dioxins/furans, and PAHs, respectively. Calculated concentrations of these constituents in soil from deposition of particulates from energetic testing emissions are shown in Attachment E-1, along with comparisons with SCLs. Based on these calculations, the concentrations of analytes in soil modeled at the point of maximum impact fall below background levels for metals and below SCLs for dioxin/furans and PAHs. While dioxin/furan emissions reportedly not detected during open detonation testing, dioxin/furan concentrations in soil were assessed using a conservative emission factor based on open burning of perchlorate waste, which likely overstates emissions from open detonation. Modeled dioxin/furan concentrations in soil were lower than the SCL, even with the use of this conservative emission factor. 3-2 ES BAO DRAFT

10 SECTION 4 Results and Conclusions The disposal of energetic materials by detonation was reportedly performed at the HVS RFI Site, potentially producing particulate emissions to the air. This could have resulted in the deposition of metals, dioxins/furans, and PAHs onto the surrounding surface soil. As discussed in the Air Dispersion Evaluation Approach for Other Boeing Sources at the Santa Susana Field Laboratory, Ventura County, California technical memorandum (CH2M HILL, 2014c), emissions data associated with a representative modeled source (energetics testing source at the Building 359 RFI site) were used in the CALPUFF modeling performed for the HVS locations. These emissions were modeled using CALPUFF to account for local flows and topography to assess impacts to soil near the buildings in the HVS RFI Site. The modeled concentrations in soil were compared with the existing surface soil sampling data. The results from this comparison indicate that maximum impacts to soil from the chemicals of interest (metals, dioxins/furans, and PAHs) fall well below background levels or SCLs. The maximum estimated concentrations in soil fall below these thresholds. Based on a review of the distribution of surface soil samples previously collected within the modeled depositional area surrounding HVS buildings (Figures F.3-2, F.3-3, and F.3-4), additional sampling has been proposed to further assess potential air deposition impacts to soil. As described in the HVS South 2 nd iteration work plan (MWH, 2014), two sample locations have been proposed to address potential air deposition impacts related to the former energetic material testing activities at Building These locations are proposed northwest and west of former Building These proposed samples will be analyzed for PAHs, dioxins/furans, and metals. Additionally, six sample locations have been proposed to address potential air deposition impacts related to mixed-open detonation and small rocket motor testing activities at Buildings 1745 and These locations are within the contour with the highest maximum modelled deposition impacts, and in stepout locations to the north, west, south, and east of the contour with the highest maximum modeled impacts. The stepout locations will be placed on hold pending the results of sampling within the highest max contours. These proposed samples will be analyzed for PAHs, dioxins/furans, and metals. ES BAO 4-1 DRAFT

11 SECTION 5 Works Cited California Environmental Protection Agency, Department of Toxic Substances Control Letter. Final Master RCRA Facility Investigation Data Gap Work Plan and Final Comprehensive Data Quality Objectives Report for the Santa Susana Field Laboratory, Ventura County, California. March 15. CH2M HILL. 2013a. Air Dispersion Modeling Report for Santa Susana Field Laboratory, Canyon RFI Site, Ventura County, California. (Appendix D of the Addendum to the Master RCRA Facility Investigation Data Gap Work Plan, Santa Susana Field Laboratory, Ventura County, California, Boeing RFI Subarea 1A South, Canyon RFI Site). September. CH2M HILL. 2013b. Air Dispersion Modeling Report for Santa Susana Field Laboratory, Area I Burn Pit RFI Site, Ventura County, California. (Appendix E to the Addendum to Master RCRA Facility Investigation Data Gap Work Plan, Santa Susana Field Laboratory, Ventura County, California, Boeing RFI Subarea 1B Southwest, Area I Burn Pit RFI Site). December. CH2M HILL. 2013c. Air Dispersion Modeling Report for Santa Susana Field Laboratory, Bowl Area RFI Site, Ventura County, California. (Appendix D to the Addendum to Master RCRA Facility Investigation Data Gap Work Plan, Santa Susana Field Laboratory, Ventura County, California, Boeing RFI Subarea 1B North, Bowl RFI Site). October. CH2M HILL. 2013d. Air Dispersion Modeling Report for Santa Susana Field Laboratory, Systems Test Laboratory IV RFI Site, Ventura County, California. (Appendix D to the Addendum to Master RCRA Facility Investigation Data Gap Work Plan, Santa Susana Field Laboratory, Ventura County, California, Boeing RFI Subarea 5/9 South, STL-IV). April. CH2M HILL. 2013e. Recommended Approach for Air Dispersion Modeling, Boeing RCRA Facility Investigation Project, Santa Susana Field Laboratory, California. (Appendix B of the Comprehensive Data Quality Objectives, RCRA Facility Investigation, Santa Susana Field Laboratory, Ventura County, California). March. CH2M HILL. 2014a. Air Dispersion Modeling Report for Santa Susana Field Laboratory, Happy Valley North (HVN) RFI Site, Ventura County, California. (Appendix D to the Addendum to Master RFI Data Gap Work Plan Iteration 2, Boeing RFI Subarea 1A Central, Happy Valley North RFI Site, Santa Susana Field Laboratory, Ventura County, California). April 18. CH2M HILL. 2014b. Air Dispersion Modeling Report for Santa Susana Field Laboratory, Building 359 (B359) RFI Site, Ventura County, California. (Appendix D to the Addendum to Master RFI Data Gaps Work Plan Iteration 2, Boeing RFI Subarea 1A Central, B359 RFI Site, Santa Susana Field Laboratory, Ventura County, California). April 18. CH2M HILL. 2014c. Air Dispersion Evaluation Approach for Other Boeing Sources at the Santa Susana Field Laboratory, Ventura, California. September. MWH Group 1A Northeastern Portion of Area I RCRA Facility Investigation Report, Santa Susana Field Laboratory, Ventura County, California. Volume VII RFI Site Reports, Appendix F, Happy Valley South (Area I AOC). February. MWH Addendum to the Master RFI Data Gaps Work Plan Iteration 2, Boeing RFI Subarea 1A South, HVS RFI Site, Santa Susana Field Laboratory, Ventura County, California. October Mitchell, W.J. and J.C. Suggs Emission Factors for the Disposal of Energetic Materials by Open Burning and Open Detonation (OB/OD). EPA/600/R-98/103. August. ES BAO 5-1 DRAFT

12 Figures

13 VICINITY MAP UNDEVELOPED LAND NASA UNDEVELOPED LAND AREA III AREA II AREA I AREA IV UNDEVELOPED LAND UNDEVELOPED LAND UNDEVELOPED LAND AREA IV EEL STP-3 Compound A STL-IV ECL Silvernale AREA III Boeing RFI Subarea 5/9 North AREA II Boeing RFI Subarea 1B North CTL-V CTL-III R-1 Pond LF AREA I Bowl Area A1 AF APTF Impoundment 1 BS HVN Canyon IL HVS B1 Boeing RFI Subarea 1A South Boeing RFI Subarea 1A North Boeing RFI Subarea 1A Central Happy Valley South LEGEND DOE AOC Boundary NASA AOC Boundary RFI Group Boundary Administrative Boundary Ponds Boeing RFI Site Paved Road Dirt Road Unpaved trail Boeing RFI Subarea 5/9 South Area I Burn Pit Boeing RFI Subarea 1B Southwest Perimeter Pond Boeing RFI Subarea 1B Southeast UNDEVELOPED LAND Boeing RFI Subarea 10 $ ,500 Feet 1 in = 1,500 ft FIGURE E.1-1 Site Layout Air Dispersion Modeling Report for the Happy Valley South RFI Site Santa Susana Field Laboratory, Ventura County, California SCO K:\BOEING\362070\MAPFILES\2013\DQO\CANYON\ADM\CANYON_SUBAREAS.MXD DDODS 9/4/2013 5:13:54 PM

14 FIGURE E.2-1 Wind Rose at Happy Valley South Location Air Dispersion Evaluation Report for the Happy Valley South, Santa Susana Field Laboratory Ventura County, California ES BAO DRAFT

15 LEGEND Percentage of Maximum Deposition 15% 25% 50% 75% Basemap Building - Existing!!!!!!!!!!!!!!! Structure RFI Group Boundary Administrative Boundary RFI Site - Boeing B1 IL A1 STP-3 Compound A Silvernale ECL HWCT R-1 Pond LF AF HVN CN BS HVS NOTE 1. The contours represent the fine grid modeling of TSP deposition for each site. The fine grid for each site extends 3.5 km in each direction from the modeled emission source(s). 2. For each modeled site the percentages of the maximum impact are based on the modeled maximum 5-year average for that individual site. 3. The AIBP contours are for the diesel and dunnage scenario only. This scenario was characterized as a detonation not a burn for modeling purposes. STL-IV CTL-V CTL-III Bowl Area Area I Burn Pit Perimeter Pond $ ,500 Feet 1 in = 1,540 ft FIGURE E.3-1 Cumulative Particle Deposition Contours for Six Representative Sources Air Dispersion Approach for Happy Valey South RFI Site Santa Susana Field Laboratory, Ventura County, California SCO K:\BOEING\362070\MAPFILES\2014\DQO\SITEWIDE_ADM\CUMULATIVEPARTICLE_AIRDISPERSIONMODELING.MXD FESQUER 6/25/2014 8:21:21 AM

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19 Attachment E-1 Soil Calculations for Energetics Testing Sources

20 Attachment E-1a. Evaluation of Modeled Soil s Chemical Characterization Level in Soil (ug/kg) Modeled Maximum in Soil (ug/kg) Bldg 1372 Bldg 1745 Bldg 1706 Aluminum 37,900, Barium 203, Beryllium 1,424 NA NA Copper 42, Lead 33, Zinc 153, Dioxins/Furans PAHs NA - not applicable, not an emission from this source.

21 Attachment E-1b Calculation of Hypothetical Soil s from Air Deposition (HVS Building 1372) Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation" 3. half lives for all metals are set at 1E+08 days Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 40 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Parameters: s calculated from 1/2 life in soil (t_1/2): 1E+08 days (essentially infinite) Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Calculations: Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Aluminum 1.92E E E E Max Value 1.44E E E E % 9.60E E E E % Fraction of metals is scaled from: 4.80E E E E % PM emission factor (0.181) 2.88E E E E % Metal emission factor: Aluminum Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Barium Barium 1.92E E E E Max Value Copper E E E E % Lead E E E E % Zinc Page 1 of 4

22 4.80E E E E % 2.88E E E E % Operational Scaling hrs Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Burn event duration 0.03 hr/event Copper 1.92E E E E Max Value number burn event/day 0.05 event/day 1.44E E E E % days/year days/yr 9.60E E E E % years 5.00 yr 4.80E E E E % Duration of burn events 2.90 hr 2.88E E E E % Scaled deposition flux Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Lead 1.92E E E E Max Value 1.44E E E E % 9.60E E E E % 4.80E E E E % 2.88E E E E % Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Zinc 1.92E E E E Max Value 1.44E E E E % 9.60E E E E % 4.80E E E E % 2.88E E E E % Page 2 of 4

23 Calculation of Hypothetical Soil s from Air Deposition (HVS Buildling 1372) Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation", which includes precursors for poly aromatic hydrocarbon formation 2. Calculations were developed using benzo(a)pyrene as a surrogate Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 40 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Parameters: s calculated from 1/2 life in soil (t_1/2): 429 days (1.18 yr) Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Calculations: - based on carbon black PAH Soil (ug/kg) Fraction of PAH in - (ug/m 2 -yr) - based PAH particulate based on PAH on PAH Benzo(a)pyrene 1.92E E E Max Value 1.44E E E % 9.60E E E % 4.80E E E % 2.88E E E % 38.7 ug/kg - suburban resident RBSL for B(a)P Recommended half life in soil from OEHHA for PAHs PAH emission factor -9.8e-7 (Mitchell and Suggs) PM Emission factor Page 3 of 4

24 Calculation of Hypothetical Soil s from Air Deposition (HVS Building 1372) Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation", which includes precursors for dioxin/furan formation Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 40 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Parameters: s calculated from 1/2 life in soil (t_1/2): 7300 days (10 yr) Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Calculations: Chemical Fraction of dioxin - based on dioxins (ug/m 2 -yr) - based on dioxins Dioxin Soil (ug/kg) Dioxin/Furan 1.92E E E E Max Value 1.44E E E E % 9.60E E E E % 4.80E E E E % 2.88E E E E % ug/kg - lowest eco RBSL for 2,3,7,8-TCDD Recommended half life in soil from OEHHA for dioxins dioxin emission factor -2e-10 (Mitchell and Suggs) PM Emission factor Page 4 of 4

25 Attachment E-1c Calculation of Hypothetical Soil s from Air Deposition (HVS Building 1745) Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation" 3. half lives for all metals are set at 1E+08 days Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 40 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Parameters: s calculated from 1/2 life in soil (t_1/2): 1E+08 days (essentially infinite) Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Calculations: Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Aluminum 1.12E E E E Max Value 8.39E E E E % 5.59E E E E % Fraction of metals is scaled from: 2.80E E E E % PM emission factor (0.181) 1.68E E E E % Metal emission factor: Aluminum Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Barium Barium 1.12E E E E Max Value Copper E E E E % Lead E E E E % Zinc Page 1 of 4

26 2.80E E E E % 1.68E E E E % Operational Scaling hrs Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Burn event duration 0.03 hr/event Copper 1.12E E E E Max Value number burn event/day 0.05 event/day 8.39E E E E % days/year days/yr 5.59E E E E % years 5.00 yr 2.80E E E E % Duration of burn events 2.90 hr 1.68E E E E % Scaled deposition flux Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Lead 1.12E E E E Max Value 8.39E E E E % 5.59E E E E % 2.80E E E E % 1.68E E E E % Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Zinc 1.12E E E E Max Value 8.39E E E E % 5.59E E E E % 2.80E E E E % 1.68E E E E % Page 2 of 4

27 Calculation of Hypothetical Soil s from Air Deposition (HVS Buildling 1745) Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation", which includes precursors for poly aromatic hydrocarbon formation 2. Calculations were developed using benzo(a)pyrene as a surrogate Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 40 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Parameters: s calculated from 1/2 life in soil (t_1/2): 429 days (1.18 yr) Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Calculations: - based on carbon black PAH Soil (ug/kg) Fraction of PAH in - (ug/m 2 -yr) - based PAH particulate based on PAH on PAH Benzo(a)pyrene 1.12E E E Max Value 8.39E E E % 5.59E E E % 2.80E E E % 1.68E E E % 38.7 ug/kg - suburban resident RBSL for B(a)P Recommended half life in soil from OEHHA for PAHs PAH emission factor -9.8e-7 (Mitchell and Suggs) PM Emission factor Page 3 of 4

28 Calculation of Hypothetical Soil s from Air Deposition (HVS Building 1745) Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation", which includes precursors for dioxin/furan formation Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 40 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Parameters: s calculated from 1/2 life in soil (t_1/2): 7300 days (10 yr) Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Calculations: Chemical Fraction of dioxin - based on dioxins (ug/m 2 -yr) - based on dioxins Dioxin Soil (ug/kg) Dioxin/Furan 1.12E E E E Max Value 8.39E E E E % 5.59E E E E % 2.80E E E E % 1.68E E E E % ug/kg - lowest eco RBSL for 2,3,7,8-TCDD Recommended half life in soil from OEHHA for dioxins dioxin emission factor -2e-10 (Mitchell and Suggs) PM Emission factor Page 4 of 4

29 Attachment E-1d Calculation of Hypothetical Soil s from Air Deposition (HVS Building 1706) Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation" 3. half lives for all metals are set at 1E+08 days Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 40 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Parameters: s calculated from 1/2 life in soil (t_1/2): 1E+08 days (essentially infinite) Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Calculations: Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Aluminum 1.09E E E E Max Value 8.14E E E E % 5.43E E E E % Fraction of metals is scaled from: 2.71E E E E % PM emission factor (0.181) 1.63E E E E % Metal emission factor: Aluminum Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Barium Barium 1.09E E E E Max Value Copper E E E E % Lead E E E E % Zinc Page 1 of 4

30 2.71E E E E % 1.63E E E E % Operational Scaling hrs Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Burn event duration 0.03 hr/event Copper 1.09E E E E Max Value number burn event/day 0.05 event/day 8.14E E E E % days/year days/yr 5.43E E E E % years 5.00 yr 2.71E E E E % Duration of burn events 2.90 hr 1.63E E E E % Scaled deposition flux Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Lead 1.09E E E E Max Value 8.14E E E E % 5.43E E E E % 2.71E E E E % 1.63E E E E % Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Zinc 1.09E E E E Max Value 8.14E E E E % 5.43E E E E % 2.71E E E E % 1.63E E E E % Page 2 of 4

31 Calculation of Hypothetical Soil s from Air Deposition (HVS Buildling 1706) Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation", which includes precursors for poly aromatic hydrocarbon formation 2. Calculations were developed using benzo(a)pyrene as a surrogate Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 40 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Parameters: s calculated from 1/2 life in soil (t_1/2): 429 days (1.18 yr) Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Calculations: - based on carbon black PAH Soil (ug/kg) Fraction of PAH in - (ug/m 2 -yr) - based PAH particulate based on PAH on PAH Benzo(a)pyrene 1.09E E E Max Value 8.14E E E % 5.43E E E % 2.71E E E % 1.63E E E % 38.7 ug/kg - suburban resident RBSL for B(a)P Recommended half life in soil from OEHHA for PAHs PAH emission factor -9.8e-7 (Mitchell and Suggs) PM Emission factor Page 3 of 4

32 Calculation of Hypothetical Soil s from Air Deposition (HVS Building 1706) Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation", which includes precursors for dioxin/furan formation Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 40 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Parameters: s calculated from 1/2 life in soil (t_1/2): 7300 days (10 yr) Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Calculations: Chemical Fraction of dioxin - based on dioxins (ug/m 2 -yr) - based on dioxins Dioxin Soil (ug/kg) Dioxin/Furan 1.09E E E E Max Value 8.14E E E E % 5.43E E E E % 2.71E E E E % 1.63E E E E % ug/kg - lowest eco RBSL for 2,3,7,8-TCDD Recommended half life in soil from OEHHA for dioxins dioxin emission factor -2e-10 (Mitchell and Suggs) PM Emission factor Page 4 of 4

33 Attachment E-1e Calculation of Hypothetical Soil s from Air Deposition (HVS Building 1706) - Beryllium Assumptions: 1. Based on combustion modeling, particulate emissions consist of "open detonation" 3. half lives for all metals are set at 1E+08 days Methodology: 1. es are converted to soil concentrations using the equation presented in EPA combustion guidance (EPA 530-R and EPA 600/R-98/137) 2. Calculation performed using Equation 4-1 in EPA 600/R-98/137: ( 1 exp ( k t) ) Dep C S = Z ρ k Cs = soil concentration, ug/kg (calculated value) Dep = deposition flux (ug/m 2 -yr) (see table) k = soil loss constant (yr -1 ) (see below) t = deposition time (yr) 5 years Z = soil mixing depth (m) 0.15 m (6 inches) ρ = soil bulk density (kg/m3) 1500 kg/m3 Fraction of metals is scaled from: Parameters: PM emission factor (0.181) s calculated from 1/2 life in soil (t_1/2): 1E+08 days (essentially infinite) Metal emission factor: Source: Cal-EPA OEHHA Technical Support Document for Exposure Assessment and Stochastic Analysis, Final, August 2012 (Appendix G) Soil loss constant calculation: k = 0.693/t_1/2 Beryllium Calculations: Metal Fraction of metal (ug/m 2 -yr) Metal Soil (ug/kg) Beryllium 1.09E E E E Max Value 8.14E E E E % 5.43E E E E % Operational Scaling 2.71E E E E % hrs 1.63E E E E % Burn event duration 0.03 hr/event number burn event/day 0.05 event/day days/year days/yr years 5.00 yr Duration of burn events 2.90 hr Scaled deposition flux Page 1 of 1