LEGAL NOTICE l%is report was preparedby BattelleMemorialInstitute (Battelle)as an accountof sponsoredresearchactivities. Neither Clientnor Battelle nor any person actingon behalf of eitheM AKEs ANY WARIUNTY OR REPRESENTATION, EXPRESS OR IMPLIED, with respect to the accuracy, completeness, or usefulness of the informationcontainedin this repom or that the use of any information,apparatus, process, or compositiondisclosed in this report may not iniiinge privately om"ed rights; or Assumes any liabilitieswith respectto the use ofi or for damagesresultingfromthe use ot any information,apparatus,process,or composition disclosedin this report.

No abstract

Waste from Hanford underground storage tank 241-AN-107 is a candidate low-activity waste (LAW) for Envelope C. Envelope C wastes require pretreatment to remove radioactive Sr and TRU (along with cesium and technetium) before immobilization. The baseline pretreatment process planned for Sr/TRU removal was precipitation with added strontium and iron. However, studies have shown that the Sr/Fe precipitates were very difficult to filter. An alternative treatment being evaluated uses permanganate instead of iron. Permanganate treatment has been shown to be effective for decontaminating waste from Hanford Tank SY-101.Battelle conducted small-scale experiments with archived AN-107 waste over a period of about three months to determine the effectiveness of the permanganate treatment process. These tests showed that permanganate treatment alone would provide adequate TRU removal, however, permanganate alone would not provide adequate Sr removal. The preferred Sr/TRU removal process involved addition of strontium and permanganate. Test conditions that provided adequate Sr/TRU decontamination were identified. These test conditions were fimther evaluated with a 1-L batch of archived AN-107, which provided a large enough volume of waste to conduct crossflow filtration studies. These tests showed that Sr/TRU removal could be accomplished by addition of a strontium solution followed by permanganate solution. The resulting precipitate could be removed effectively by crossflow filtration.The original target sodium concentration for AN-107 diluted feed was 7.7M. The waste was fi,u-ther diluted and additional caustic added before Sr/TRU precipitation. The target concentrations for the treated waste were 6.OM sodium, 1.OMfree hydroxide, 0.075M strontium, and 0.05M permanganate. Approximately 1.4-L of AN-107 diluted feed were treated. Decontamination of strontium-90 and TRU (Am-241) in the supematant was greater than needed to meet the immobilized low-activity waste (ILAW) requirements (less than 100 nCi/g TRU and less than 20 Ci/m3 Sr-90 in the final ILAW). The stronium-90 decontamination factor (DF) was consistently greater than 50 and the Am-241 DF greater than 25. The target DFs were 10 for Sr-90 and 5 for Am-241. These DFs include the contribution from the removal of the entrained solids although this was relatively small. The removal of the entrained solids accounted for about 8V0of the DF for Sr-90 and about 17°/0of the DF for the alpha emitters.Crossflow filtration tests with archived AN-107 showed that the entrained solids could not be readily removed from AN-107 waste prior to Sr/TRU treatment, However, the filterability, as determined by filter flux rate, increased by an order of magnitude after the treatment process. For AN-107 diluted feed, crossflow filtration tests were conducted in the Cell Unit Filter (CUF) system with the Sr/TRU precipitated waste only. Results showed that the treated waste could be effectively filtered by crossflow filtration. A parametric study was conducted with relatively low, 1.9 wt'?/0, initia...

*Elevationis the distancefromthe tmskbottomto the mouth of the samplebottle. The entire contents of each sample container were transfemed to a 1-L jaq the net mass transferred was calculated by difference from the fill and empty container masses.b The 860-g (659.8-mL) AP-1 01 composite was sealed and stirred for 54 minutes using a magnetic stir bar. A 10l-mL subsample was transferred to a glass bottle and sealed. For subsequent precipitatiordcrystallization testing at reduced temperature. Portions of the remaining composite material were used for subsequent analyses. The composite sample did not show signs of phase separation or precipitation. The overall sample processing is summarized in Figure 2.1. 2.2 Sample Digestion for Analysis After sample homogenization, the AP-101 composite sub-samples were delivered directly to the laboratories for various measurements including mercury, cyanide, hydroxide, tritium, total organic carbon, total inorganic carbon, ammoni~ion chromatography (inorganic and organic ions), 14C, pertechnetate, 79Se,and gamma spectrometry. The AP-101 composite density (see Table 3.5) was determined in the Shielded Analytical Laboratory (SAL). The SAL processed 5-mL aliquots in triplicate according to PNL-ALO-128, HNOS-HC1Acid Extraction of Liquids for Metals Analysis Using a Dry-Block Heater, for subsequent ICP and ICP/MS analyses. The acid extracted solutions were brought to a nominal 25-mL volume and absolute volumes determined based on final solution weights and densities. This acid digestion resulted in a solution with a small amount of white floating particulate. The floating particulate were removed by filtration. The filtrates were analyzed by ICP and ICP/MS. Along with the samples, the SAL processed a reagent blank, a toxicity characteristic leach protocol (TCLP)-metals spiked blank, and TCLP-metals spiked sample. The TCLP metals spike included Ag,

No abstract