Third Set of EPA Completeness Comments 1

THIRD SET OF EPA COMPLETENESS COMMENTS FOR CRA 2014

3-C-1. Assumed Plutonium Oxidation State. The Pu oxidation state assumed for Performance 

Assessment (PA) is important because significantly higher brine solubilities are predicted for 

Pu(III) than for Pu(IV). In Appendix SOTERM Section 3.6.2, results from recent long-term 

experiments with aqueous Pu and iron are presented in which the predominant long term aqueous 

oxidation state was Pu(III). Other recent studies also have indicated that Pu(IV) is reduced to 

Pu(III) in the presence of reduced iron (Altmaier et al. 2009, Felmy et al. 2011, Felmy et al. 

2012, Kirsch et al. 2011). Plymale et al. (2012) determined that Pu(IV) solids in contact with 

solutions containing chelating agents such as EDTA can undergo reductive dissolution to Pu(III) 

by either biotic or abiotic mechanisms. Appendix SOTERM states that “The predominance of 

Pu(III) at long times provides a strong data point on the reducing conditions that iron creates 

under WIPP-relevant conditions, but does not account for radiolytic impacts on Eh, and the 

effects of organic complexation which will stabilize Pu(IV) relative to Pu(III).” Assuming that 

radiolysis will affect the Pu oxidation state in WIPP repository brines conflicts with the peerreviewed Chemical Conditions conceptual model assumption that radiolysis will not affect the 

oxidation-reduction conditions in the repository (SCA 2008). In addition, EDTA, which is 

present in the WIPP inventory, has been shown to cause reduction of Pu(IV) to Pu(III) rather 

than to stabilize Pu(IV) (e.g., Boukhalfa et al. 2007, Plymale et al. 2012). 

Currently, Pu(III) is the assumed oxidation state for 50% of PA realizations and Pu(IV) is the 

assumed oxidation state for the other 50% of PA realizations. Because of recent data showing 

that Pu(IV) reduction to Pu(III) may be more likely than previously assumed, DOE must provide 

an assessment of all currently available data relevant to the assumed Pu oxidation state for PA.

If the current Pu oxidation states assumption is inconsistent with the available data, DOE must 

provide an analysis that supports a higher proportion of Pu(III) in the PA realizations and include 

this higher proportion of Pu(III) in PA. 

Altmaier, M., V. Neck, J. Lützenkirchen and T. Fanghänel. 2009. Solubility of plutonium in 

MgCl2 and CaCl2 solutions in contact with metallic iron. Radiochimica Acta 97:187-192. 

Boukhalfa, H., G.A. Icopini, S.D. Reilly, and M.P. Neu. 2007. Plutonium (IV) reduction by the 

metal-reducing bacteria Geobacter metallireducins GS15 and Shewanella oneidensis MR1. 

Applied and Environmental Microbiology 73:5897-5903.

Felmy, A.R., D.A. Moore, K.M. Rosso, O. Qafoku, D. Rai, E.C. Buck and E. S. Ilton. 2011. 

Hetrogeneous reduction of PuO2 with Fe(II): importance of the Fe(III) reaction product. 

Environmental Science and Technology 45:3952-3958.

Felmy, A.R., D.A. Moore, C.I. Pearce, S.D. Conradson, O. Qafoku, E.C. Buck, K.M. Rosso and 

E.S. Ilton. 2012. Controls on soluble Pu concentrations in PuO2/Magnetite Suspension. 

Environmental Science and Technology 46:11610-11617.
Third Set of EPA Completeness Comments 2

Kirsch, R., D. Fellhauer, M. Altmaier, V. Neck, A. Rossberg, T. Fanghänel, L. Charlet and A.C. 

Scheinost. 2011. Oxidation state and local structure of plutonium reacted with magnetite, 

mackinawite and chukanovite. Environmental Science and Technology 45:7267-7274. 

Plymale A.E., V.L. Bailey, J.K. Fredrickson, S.M. Heald, E.C. Buck, L. Shi, Z. Wang, C.T. 

Resch, D.A. Moore and H. Bolton. 2012. Biotic and abiotic reduction and solubilization of 

Pu(IV)O2•H2O(am) as affected by anthraquinone-2,6-disulfonate (AQDS) and 

ethylenediaminetetracetate (EDTA). Environmental Science and Technology 46:2132-2140.

SCA (S. Cohen and Associates). 2008. Verification of the Waste Isolation Pilot Plant Chemistry 

Conceptual Models. Prepared for the U.S. Environmental Protection Agency Office of Radiation 

and Indoor Air, September 2008.

3-C-2. Boron Species in WIPP Brine. The Compliance Certification Application (CCA) and 

CRA-2004 refer to the presence of boric acid [B(OH)3] in WIPP brine. However, the CRA-2009 

(Appendix SOTERM, Table SOTERM-2) and CRA-2014 (Appendix SOTERM, Table 

SOTERM-4) indicate that “boron species will be present in brine as boric acid, hydroxyl 

polynuclear forms (B3O3(OH)4

-

), and/or borate forms (e.g., B4O7

2-

).” Borkowski et al. (2010a) 

indicates that tetraborate is present in WIPP brine and Borkowski et al. (2010b) determined the 

stability complex and Pitzer coefficients for the neodymium(III)-tetraborate aqueous species. 

Lucchini (2013) refers to tetraborate in WIPP brines during comparisons of measured and 

modeled brine compositions. Consequently, there appears to have been an evolution in the 

assumed boron species in WIPP brines since the CCA. Because complexation by tetraborate has 

been identified as important for actinide(III) speciation in WIPP brines (Borkowski et al. 2010b), 

DOE must identify all expected chemical constituents that contain boron species in WIPP brines. 

The basis for that determination must be included. 

Borkowski, M., J.-F. Lucchini, M.K. Richmann and D.T. Reed. 2010a. Actinide(III) Solubility in 

WIPP Brine: Data Summary and Recommendations. Los Alamos National Laboratory, LCOACP-08, Rev 0. 

Borkowski, M., M. Richmann, D.. Reed and Y. Xiong. 2010b. Complexation of Nd(III) with 

Tetraborate Ion and Its Effect on Actinide(III) Solubility in WIPP Brine. Radiochimica Acta 

98:577-582.

Lucchini, J.-F. 2013. WIPP Actinide-Relevant Brine Chemistry. Los Alamos National 

Laboratory, LCO-ACP-15, Rev. 0.

3-C-3. Adequacy of EQ3/6 Database. The actinide solubility and aqueous speciation data in the 

EQ3/6 database DATA0.FM1 was last updated using data available in 2002 (Giambalvo 2003, 

Nowak 2005). Since 2002, relevant data have been developed in investigations carried out by 

WIPP investigators and by outside researchers. The absence of an update to the EQ3/6 database 

despite more than a decade of potentially relevant new data leads to the following observations:
Third Set of EPA Completeness Comments 3

 In CRA-2014 Appendix SOTERM Sections 3.3 and 3.7, DOE reviewed the chemistry of 

thorium and americium, respectively, including data that has become available since the 

last EQ3/6 database update. However, these data (such as Neck et al. 2002, Neck et al. 

2003, Altmaier et al. 2004, Altmaier et al. 2005, Altmaier et al. 2006, Borkowski et al. 

2012, Neck et al. 2009) were not used to revise the EQ3/6 database. 

 Xiong (2011) experimentally determined the solubilities of natural and synthetic 

hydromagnesite samples and calculated a different solubility for synthetic 

hydromagnesite than the solubility in the EQ3/6 database. An assessment was not 

provided in the CRA of the possible effects of this different solubility on CO2 fugacities,

calculated pH values and actinide solubilities in WIPP repository brines.

 Borkowski et al. (2010) determined the stability constant for the neodymium-tetraborate 

aqueous species and also calculated Pitzer ion-interaction parameters. These data were 

not incorporated into the EQ3/6 database, even though WIPP brines contain borate, boric 

acid or hydroxyl polynuclear species and complexation of the +III actinides by 

tetraborate could increase solubilities modeled for PA. 

 Thakur et al. (2014) determined a β0

101 for AmEDTA-

(20.55) that differs from the value 

in DATA0.FM1 (18.97). Because AmEDTAis the predominant Am(III) aqueous species 

in WIPP brines, the β0

101 for AmEDTAcould significantly affect aqueous Am speciation 

and solubilities, but the revised value was not included in the EQ3/6 database.

DOE maintained at the time of the CRA-2009 PABC that the effects of not updating the EQ3/6 

database with new data available at that time were conservative, because higher actinide 

solubilities would be predicted using the unrevised database. However, the cumulative effects of 

the new data that are now available may be non-conservative and must be quantitatively 

evaluated. DOE must: 1) carry out and document a thorough review of all available +III and +IV 

actinide aqueous speciation and solubility data and hydromagnesite solubility data; 2) use the 

results of this review to defensibly update the EQ3/6 database; and 3) use this revised database to 

recalculate the actinide solubilities and associated uncertainty distributions for PA. DOE must 

provide the documentation of these components as part of the CRA. 

Altmaier, M., V. Neck and T. Fanghänel. 2004. Solubility and colloid formation of Th(IV) in 

concentrated NaCl and MgCl2 solution. Radiochimica Acta 92:537-543. 

Altmaier, M., V. Neck, M.A. Denecke, R. Yin and T. Fanghänel. 2006. Solubility of 

ThO2•xH2O(am) and the formation of ternary Th(IV) hydroxide-complexes in NaHCO3-Na2CO3

solutions containing 0-4 M NaCl. Radiochimica Acta 94:495-500.

Altmaier, M., V. Neck, R. Müller and T. Fanghänel. 2005. Solubility of ThO2•xH2O(am) in 

carbonate solution and the formation fo ternary Th(IV) hydroxide-carbonate complexes. 

Radiochimica Acta 93:83-92.
Third Set of EPA Completeness Comments 4

Borkowski, M., M. Richmann, D.T. Reed and Y. Xiong. 2010. Complexation of Nd(III) with 

tetraborate ion and its effect on actinide(III) solubility in WIPP brine. Radiochimica Acta 

98:577-582.

Borkowski, M., M. Richmann and J.F. Lucchini. 2012. Solubility of An(IV) in WIPP brine: 

thorium analog studies in WIPP simulated brine. Los Alamos National Laboratory LCO-ACP17.

Giambalvo, E.R. 2003. Release of FMT Database FMT_021120.CHEMDAT. Memorandum to 

L.H. Brush, March 10, 2003, ERMS 526372.

Neck, V., M. Altmaier, R. Müller, A. Bauer, T. Fanghänel and J.I. Kim. 2003. Solubility of 

crystalline thorium dioxide. Radiochimica Acta 91:253-262.

Neck, V., M. Altmaier, T. Rabung, J. Lützenkirchen and T. Fanghänel. 2009. Thermodynamics 

of trivalent actinides and neodymium in NaCl, MgCl2, and CaCl2 solutions: solubility, 

hydrolysis, and ternary Ca-M(III)-OH complexes. Pure and Applied Chemistry 81:1555-1568.

Neck, V., R. Müller, M. Bouby, M. Altmaier, J. Rothe, M.A. Denecke, and J.I. Kim. 2002. 

Solubility of Amorphous Th(IV) Hydroxide-Application of LIBD to Determine the Solubility 

Product and EXAFS for Aqueous Speciation. Radiochimica Acta 90:485-494.

Nowak, E.J. 2005. Recommended Change in the FMT Thermodynamic Data Base. 

Memorandum to L.H. Brush, April 1, Sandia National Laboratories, Carlsbad, New Mexico, 

ERMS 539227.

Thakur, P., Y. Xiong, M. Borkowski and G.R. Choppin. 2014. Improved thermodynamic model 

for interaction of EDTA with trivalent actinides and lanthanide to ionic strength of 6.60 m. 

Geochimica et Cosmochimica Acta 133:299-312.

Xiong, Y. 2011. Experimental determination of solubility constant of hydromagnesite (5424) in 

NaCl solutions up to 4.4 m at room temperature. Chemical Geology 284:262-269.

3-C-4. Exclusion of Experimental Data with Borate from Am(III) Solubility Uncertainty 

Analysis. Brush and Domski (2013) used their Criterion G-9 to select data for the actinide 

solubility uncertainty analysis; Criterion G-9 specifies that experimental solubility data should be 

excluded if the solutions contained dissolved elements or species for which μ0/RT 1data or Pitzer 

parameters were not included in the EQ3/6 database (DATA0.FM1). The application of this 

criterion was reasonable when the experiments included species that are not present in the WIPP 

repository, for example, when it was used to exclude the Th(IV) experimental data of Colás et al. 

(2011) because of gluconate in the experimental solutions. However, Brush and Domski (2013) 

 

1 The μ0

/RT value is used in the FMT database, but log K is used in the EQ3/6 database, so Criterion G-9 should cite 

the log K value
Third Set of EPA Completeness Comments 5

used the presence of borate in GWB and ERDA-6 to exclude solubility data that were obtained in

mildly basic WIPP brines. The undeclared assumption for this exclusion would be an admission 

that the current Am(III) model is inadequate for predicting solubilities in WIPP brines at 

anticipated repository pcH values. A revised uncertainty analysis for Am(III) must be performed 

by DOE after the following items have been completed: 1) The Am(III)-tetraborate stability 

constant and Pitzer parameter data have been incorporated and other appropriate updates have 

been made to the EQ3/6 database (which satisfy Comments 3-C-3 and 3-C-4) and, 2) Solubility 

data obtained in mildly basic WIPP brines, such as the Khalili et al. (1994) solubility results have

be included in the database. 

Brush L.H., and P.S. Domski. 2013. Uncertainty analysis of actinide solubilities for the WIPP 

CRA-2014 PA, Rev. 1. Supersedes ERMS 559278.

Colás, E., M. Grivé, I. Roho and L. Duro. 2011. Solubility of ThO2•xH2O(am) in the presence of 

gluconate. Radiochimica Acta 99:269-273.

Khalili, F.I., V. Symeopoulos, J.-F. Chen and G.R. Choppin. 1994. Solubility of Nd in brine. 

Radiochimica Acta 66/67:51-55.

3-C-5. Am(III) Solubility Uncertainty Distribution. Brush and Domski (2013) used 172 

solubility measurements to determine the Am(III) solubility uncertainty distribution:

 109 values from Borkowski et al. (2009)

 56 values from Neck et al. (2009)

 6 values from Runde and Kim (1995)

 1 value from Rao et al. (1999)

Consequently, the majority of the solubility measurements used to calculated the Am(III) 

solubility uncertainty distribution were from Borkowski et al. (2009). Brush and Domski (2013) 

established Criterion G7 for the selection of data for actinide solubility uncertainty analysis;

Criterion G7 states that experimental results should be included only if the solubility-controlling 

solid phase was characterized. As previously noted during review of the PABC-2009 (EPA 

2010), inclusion of the Nd(III) solubility data from Borkowski et al. (2009) in the uncertainty 

analysis is inconsistent with Criterion G7 because only indirect means were used to characterize 

the solid phases. In fact, modeling calculations carried out during the PABC-2009 review 

predicted different solid phases than those indirectly determined under some conditions (EPA 

2010). As previously observed in the Technical Support Document for the CRA-2009 PABC 

(EPA 2010), including the Borkowski et al. (2009) data in the uncertainty evaluation 

significantly decreased the mean concentration of the +III actinides used in PA and will lead to 

non-conservative predicted +III actinide concentrations. DOE must exclude the Borkowski et al. 

(2009) data when the Am(III) uncertainty distribution is recalculated after completion of the 

EQ3/6 database update (see Comment 3-C-3, above).
Third Set of EPA Completeness Comments 6

Borkowski, M., J.-F. Lucchini, M.K. Richmann and D.T. Reed. 2009. Actinide (III) Solubility in 

WIPP Brine, Data Summary and Recommendations. Los Alamos National Laboratory, LCOACP-08, LA-14360.

Brush L.H., and P.S. Domski. 2013. Uncertainty analysis of actinide solubilities for the WIPP 

CRA-2014 PA, Rev. 1. Supersedes ERMS 559278.

EPA (U.S. Environmental Protection Agency). 2010. Technical Support Document for Section 

194.24, Evaluation of the Compliance Recertification Actinide Source Term, Backfill Efficacy 

and Culebra Dolomite Distribution Coefficient Values (Revision1), Docket A-98-49, Item II-B1-

25, November 2010.

Neck , V., M. Altmaier, T. Rabung, J. Lützenkirchen and T. Fanhänel. Thermodynamics of 

trivalent actinides and neodymium in NaCl, MgCl2, and CaCl2 solutions: Solubility, hydrolysis, 

and ternary Ca-M9III)-OH complexes. Pure and Applied Chemistry 81:1555-1568. 

Rao, L., D. Rai, A.R. Felmy and C.F. Novak. 1999. Solubility of NaNd(CO3)3•6H2O(c) in mixed 

electrolyte (Na-Cl-CO3-HCO3) and synthetic brine solutions. In Actinide Speciation in High 

Ionic Strength Media: Experimental and Modeling Approaches to Predicting Actinide Speciation 

and Migration in the Subsurface. Proceedings of an American Chemical Society Symposium on 

Experimental and Modeling Studies of Actinide Speciation in Non-Ideal Systems. Held August 

26-28, 1996 in Orlando, Florida. Eds. D.T. Reed, S.B. Clark and L. Rao. Kluwer 

Academic/Plenum Publishers, pp. 153-169.

Runde, W., and J.I. Kim. 1995. Untersuchungen der Übertragbarkeit von Labordaten Natürliche 

Verhältnisse: Chemisches Verhalten von Drei- und Fünfwertigem Americium in Salinen NaClLösungen (Study of the Extrapolability of Laboratory Data to Natural Conditions: Chemical 

Behavior of Trivalent and Pentavalent Americium in Saline NaCl Solutions). RCM-01094, 

Institute for Radiochemistry, Technical University of Munich, Munich, Federal Republic of 

Germany, ERMS 241862.

3-C-6. Magnesite Formation from MgO Carbonation. Clayton (2013, Section 2.7) states that 

“In the event that CO2 generation is occurring, but brucite is not available in BRAGFLO 

simulations, MgO will be converted directly to magnesite.” EPA has reviewed the potential for 

magnesite formation in the WIPP repository directly from MgO and has repeatedly determined

that hydromagnesite should be assumed to form instead of magnesite (EPA 1998, SCA 2008, 

EPA 2010). Correctly including the formation of hydromagnesite instead of magnesite will 

decrease the amount of water in the water balance calculations, which could significantly impact 

the amount of water in the repository. DOE must assess the effects on the water balance of 

incorrectly assuming magnesite formation instead of hydromagnesite in PA simulations when 

brucite was not available. DOE must also provide an assessment of the effects of this assumption

when combined with the other assumptions summarized in Completeness Comment 2-C-3

(Edwards 2015) that also increase the amount of brine calculated for the water balance. 
Third Set of EPA Completeness Comments 7

Clayton, D.J. 2013. Justification of Chemistry Parameters for Use in BRAGFLO for AP-164, 

Rev. 1. Sandia National Laboratories, ERMS 599466.

Edwards, J.D. 2015. Second Set of CRA 2014 Completeness Questions, U.S. Environmental 

Protection Agency Radiation Protection Division, Letter to J.R. Franco, U.S. Department of 

Energy Carlsbad Field Office, February 27, 2015.

EPA (U.S. Environmental Protection Agency). 2010. Technical Support Document for Section 

194.24, Evaluation of the Compliance Recertification Actinide Source Term, Backfill Efficacy 

and Culebra Dolomite Distribution Coefficient Values (Revision1), Docket A-98-49, Item II-B1-

25, November 2010.

3-C-7. Lead Inventory, Gas Generation and Water Balance. In past WIPP performance 

assessments, lead corrosion has been assumed to have insignificant effects on gas generation 

because of the relatively small amount of lead in the packaging and waste inventory (EPA 2010). 

However, use of shielded containers to emplace some RH waste may significantly increase the 

amount of lead in the repository. Van Soest (2012) provided only the RH packaging material 

lead inventory and this value has decreased since PAIR-2008. Please provide an estimate of the 

total lead that will be in the WIPP repository (waste lead plus packaging material) and the basis 

for that estimate, taking into account the expected increased lead from shielded containers. Based 

on this total lead inventory, DOE must assess whether lead corrosion may significantly affect gas 

generation and repository water balance.

Van Soest, G.D. 2012. Performance Assessment Inventory Report -2012. INV-PA-12, Revision 

0, LA-UR-12-26643.

3-C-8. Incorrect Reference to Felmy et al. (1996) and Clark and Tait (1996). Appendix 

SOTERM, Section 3.6.1.1 states that “Clark and Tait (Clark and Tait 1996) and Felmy et al. 

(Felmy et al. 1996) have experimentally observed the reduction of Pu(VI) carbonates by either 

Fe0or Fe2+ to Pu(IV). However, the Felmy et al. citation refers to a study of thorium(IV) hydrous 

oxide solubility and Clark and Tait (1996) indicate that plutonium(VI) chloride complexes were 

reduced to plutonium(V) by Fe0or Fe2+. Please provide the correct references. 

Clark, D.L., and C.D. Tait. 1996. Memorandum to Sandia WIPP Records Center 

(Subject:SWCF-A: 1.1.10.1.1: NQ: Actinide Source Term: LANL Monthly Reports). Sandia 

National Laboratories, WIPP Central File A: WBS 1.1.10.1.1. WPO 31106. 

Felmy, A.R., D. Rai, S.M. Sterner, M.J. Mason and N.J. Hess. 1996. Thermodynamic models for 

highly charged aqueous species: solubility of Th(IV) hydrous oxide in concentrated NaHCL3 and 

Na2CO3 solutions. Sandia National Laboratories, ERMS 240226.

3-C-9. Intrinsic Colloid Parameter Values. The concentration (CONCINT) used for intrinsic 

plutonium colloids in either the Pu(III) or Pu(IV) oxidation state in the actinide source term 
Third Set of EPA Completeness Comments 8

model was 1 × 10-9 M in the CCA PAVT, the CRA-2004 PABC and the CRA-2009 PABC. This 

intrinsic plutonium colloid concentration was an upper limiting value based on the detection 

limit in experiments conducted for the CCA (CCA Appendix SOTERM). The revised intrinsic 

colloid enhancement parameters used in the CRA-2014 PA do not appear to be bounding values. 

For example, the revised value of CONCINT for thorium(IV) is based on a single experimental 

data point (pcH 9.1) selected from a group of experiments because this particular experiment had 

the lowest concentration and was deemed closest to long-term equilibrium (Reed et al. 2013). In 

addition, the revised americium(III) CONCINT value is 4 × 10-9 M based on the average 

concentration in ERDA-6 experiments, even though higher concentrations were observed in 

GWB experiments. DOE must demonstrate that all of the CONCINT parameters used in PA

represent upper bounding values based on the available experimental data. 

3-C-10. Phase 5 Solubility in DATA0.FM1. EQ3/6 database version DATA0.FMT.R1 was

reviewed and accepted during the EQ3/6 code evaluation (SCA 2011, Appendix A). The 

database used for the WIPP CRA-2014 EQ3/6 actinide solubility calculations was DATA0.FM1 

(DATA0.FMT.R2). Xiong (2011) documented that the only difference between 

DATA0.FMT.R1 and DATA0.FM1 is the addition of data for magnesium chloride hydroxide 

hydrate [Mg3Cl(OH)5•4H2O, Phase 5], citing Xiong et al. (2010) as the data source. Both Xiong 

et al. (2009) and Xiong et al. (2010) report a log K of 43.21 ± 0.33 at 25oC for the reaction:

Mg3Cl(OH)5•4H2O + 5H+ = 3Mg2+ = 9H2O(l) + ClHowever, the data for this solid in DATA0.FM1 includes a log K at 25oC of 42.96. DOE must

explain this small difference between the log K values in the documentation and the database.

SCA. (S. Cohen and Associates). 2011. EQ3/6 Computer Code Evaluation. Prepared for U.S. 

Environmental Protection Agency Office of Radiation and Indoor Air. Draft March 2011. 

Xiong, Y.-L. 2011. Release of EQ3/6 Database DATA0.FM1. Email to J.J. Long, March 9, 

2011. ERMS 555152.

Xiong, Y.-L., H.-R. Deng, M. Nemer and S. Johnsen. 2009. Thermodynamic Data for Phase 5 

(Mg3Cl(OH)5•4H2O) Determined from Solubility Experiments. Memorandum to L. Brush, 

Sandia National Laboratories, May 18, 2009. ERMS 551294.

Xiong, Y.-L., H.-R. Deng, M. Nemer and S. Johnsen. 2010. Experimental determination of the 

solubility of magnesium chloride hydroxide hydrate (Mg3Cl(OH)5•4H2O, phase 5) at room 

temperature, and its importance to nuclear waste isolation in geological repositories in salt 

formations. Geochimica et Cosmochimica Acta 74:4605-4611. 

3-C-11. Appendix SOTERM Typographical Errors/Errata. Section SOTERM-3.6.1.3, Page 

SOTERM-67, line 3: Section SOTERM-3.5.1.1 and Section SOTERM-3.5.1.2 should be Section 

SOTERM-3.6.1.1 and Section SOTERM-3.6.1.2
Third Set of EPA Completeness Comments 9

Appendix SOTERM, Section SOTERM-6.0 References: The correct date for the following 

reference is 2010: Reed, D.T., J.-F. Lucchini, M. Borkowski, and M.K. Richmann. 20092010. 

Reduction of Higher Valent Plutonium by Iron under Waste Isolation Pilot Plant (WIPP)-

Relevant Conditions: Data Summary and Recommendations. LCO-ACP-09, LANL\ACRSP 

Report. Los Alamos, NM: Los Alamos National Laboratory.