ML20213C527

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Ensr Corporation, Conceptual Site Model (Revision - 01). Part 3 of 4
ML20213C527
Person / Time
Site: 07000925
Issue date: 10/31/2006
From: David Ferguson
AECOM, ENSR Corp
To:
Office of Nuclear Material Safety and Safeguards, Tronox
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ML20213C536 List:
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04020-044
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    ,n SO4 > Cl), and is a calcium bicarbonate type water.

    The second type of groundwater, which is similar to Sandstone C groundwater, is represented by wells 02W07, 02W23, and 02W36 in the BA #1 Area and wells T-72 and T-74 in the Western Alluvial Area.

    This groundwater is characterized by its relatively high TDS and sulfate content (SO4 > HCO3 > Cl), and is categorized as a calcium/magnesium sulfate water. The presence of this Sandstone C groundwater in the floodplain alluvium provides geochemical evidence that Sandstone C discharges to the alluvium close to the Cimarron River.

    The third type of groundwater is represented by 02W10 in the transitional zone of the BA #1 Area. This groundwater is characterized by relatively high magnesium content (Mg > Ca > Na+K) and is categorized as a magnesium bicarbonate water. This type of groundwater is isolated in the southeast quadrant of the BA #1 Area where massive clay and silt deposits are present as discussed in Section 2.3.1 (Detailed Stratigraphic Correlations at Cimarron - BA #1 Area) of this report. This groundwater is in essence a bicarbonate water, as in the Sandstone A and B groundwater, but with elevated Mg content that differentiates it from shallow sandstone groundwater. Given the geological setting, this type of groundwater is likely to be in equilibrium with clay minerals.

    No groundwater samples from the alluvium exhibited the chemical characteristics of Cimarron River water. Cimarron River water is categorized as a sodium chloride type water with chloride content significantly higher than sulfate and bicarbonate.

    As discussed in Section 4.3, there is a spatial correlation between water type and geological setting within the alluvium.

    4.3 Area-specific Geochemical Considerations 4.3.1 BA #1 Area The spatial distribution of TDS, sulfate, chloride, and bicarbonate alkalinity in Sandstone B and the alluvium within the BA #1 Area are illustrated in Figures 4-3 through Figure 4-6.

    Low TDS (less than 500 mg/L) groundwater was observed in the southern portion of the uplands in Sandstone B and several wells in the transitional zone immediately adjacent to the uplands (Figure 4-3).

    From southeast to northwest, groundwater TDS concentration increases from less than 500 mg/L to more than 1,000 mg/L.

    The spatial distribution of sulfate in the BA #1 Area (Figure 4-4) is similar to that of TDS, with groundwater from Sandstone B in the uplands having the lowest sulfate content (less than 10 mg/L). Higher sulfate concentration (greater than 300 mg/L) groundwater is predominantly in the northwest quadrant of the BA

    1. 1 Area. The higher observed sulfate concentrations are apparently associated with groundwater from Sandstone C.

    The chloride concentration is low (less than 20 mg/L) in most Sandstone B groundwater and the alluvium in the southeastern portion of the BA #1 Area (Figure 4-5). Most of the wells have chloride concentrations less than 80 mg/L. Compared to the chloride content of the Cimarron River, which was reported as 3,600 mg/L in 1986 at the Guthrie Gage, the alluvium has less than 5 percent of the chloride concentration of the river, suggesting that the impact of the river on the alluvium is not significant in the areas where groundwater samples were collected.

    Report No. 04020-044 (Revision 01) 4-5 October 18, 2006

    ENSR AECOM The alkalinity in groundwater ranges from 192 mg/L to 677 mg/L in the BA #1 Area. There is no clear trend in the distribution of alkalinity throughout the area and localized high concentrations (greater than 500 mg/L) were observed at multiple locations (Figure 4-6). In general, the alkalinity content in the northeastern half of the area appears to be higher than in the southwestern half. Alkalinity will be an important factor to be considered during the design of any remediation system due to its buffering capacity.

    In the BA#1 Area, nitrate and fluoride have been detected only at low concentrations, typically consistent with background. Therefore, there is little to no impact to groundwater from these constituents in this area.

    There are three distinct types of groundwater in the BA #1 Area, including calcium bicarbonate water, calcium sulfate water, and magnesium bicarbonate water. Groundwater samples from the uplands are of the calcium bicarbonate type, while the alluvium samples contain all three types of water. Figure 4-7 presents the respective areas of the site where each water type is located. The magnesium-rich groundwater (represented by 02W10) is concentrated in the southeast portion of the alluvium in the transitional zone (area within blue line), the calcium bicarbonate water (Sandstone B groundwater, represented by TMW-2, 02W29, and 02W44) is distributed in the middle and northeast portion of alluvium (area between blue and orange colored lines), and the sulfate water (possibly an indication of water being contributed from Sandstone C represented by 02W24) is isolated in the northwest portion of the alluvium (areas within orange line). These three distinct types of groundwater form three segregated water-quality zones in the alluvium from southeast to northwest.

    The spatial distribution of the different groundwater types can be attributed to the geologic environment where each groundwater type is in equilibrium. As discussed in Section 2.2 (Stratigraphy of the Cimarron Site) of this report, the alluvium can be divided into two zones, a clayey transitional zone and a sandy alluvium zone, with the approximate division along the line from monitor wells 02W03 to 02W13. The transitional zone is underlain by Sandstone B or Mudstone Band receives recharge mostly from Sandstone B. Therefore, groundwater in the transitional zone exhibits the geochemical signature of Sandstone B water. The sandy alluvium, in contrast, is underlain by various portions of Mudstone Band Sandstone C and receives recharge from both Sandstones Band C. Consequently, the alluvium has the geochemical signatures of both Sandstone B and Sandstone C water. The magnesium-rich groundwater is almost exclusively associated with clay-or silt-rich sediments.

    In Figure 4-7, the Stiff diagrams of the groundwater samples from the high-magnesium and high-sulfate zones are relatively uniform with little changes in shape and sizes. This is because the groundwater within these two zones has seen limited mixing with groundwater from other sources. However, groundwater samples from the calcium bicarbonate zone (area between the blue and the orange zones) show a gradual change in Stiff diagrams from the upland to the sandy alluvium. In the uplands, the Stiff diagram (TMW-2) is small (low TDS) and has roughly equal width and length. As the groundwater moves to the transitional zone, the Stiff diagram (02W29) begins to take on an elongated shape with notable increases in calcium and bicarbonate concentrations. Farther away from the uplands into the sandy alluvium, the Stiff diagram (02W44) is "stretched" even longer (associated with an increase in TDS concentrations). These changes in Stiff diagrams occurred without significant changes in the basic pattern of the Stiff diagrams or the relative concentrations of the major cations and anions. This indicates that the calcium bicarbonate water in the transitional zone and sandy alluvium originates from Sandstone B and is re-equilibrated with the geological materials in the alluvium. Evidence of mixing is apparent along borderlines between two water type zones.

    Report No. 04020-044 (Revision 01) 4-6 October 18, 2006

    ENSR AECOM Piper diagrams provide a visual means to compare the chemistry of water samples. Figure 4-8 presents a Piper diagram (Piper, 1944) of groundwater in the BA #1 Area and Cimarron River water (USGS, 1960-1986). Also plotted is Sandstone C groundwater from the western portion of the Cimarron Site for comparison. Major cations (Ca, Mg, and Na+K) are plotted on the left triangle while major anions (HCO3+CO3, SO4, and Cl) are plotted on the right triangle. Data points in the diamond are projected from the two triangles. As shown in the diagram, the river water is a sodium chloride type, with the data points grouped at the Na+K and Cl corners of the triangles. The average chloride to sulfate ratio of the river water is equal to 6. Typical Sandstone B groundwater is grouped at the HCO3+CO3 corner, whereas Sandstone C groundwater is at the SO4 corner. Data points from the sandy alluvium are spread in the middle section between HCO3+CO3 and SO4, indicating possible mixing of Sandstone B and Sandstone C groundwaters.

    4.3.2 Western Upland Area Groundwater geochemical parameters were evaluated during the August/September 2004 groundwater sampling event in the monitor wells in the Western Upland Area.

    The Stiff diagrams of representative groundwater samples from the Western Upland Area are illustrated in Figure 4-1. The patterns of Sandstone A and 1206 Seep water are both characterized by low TDS with bicarbonate being the dominant anion. The geochemical signature of this groundwater is very similar to the Sandstone B groundwater in the BA #1 Area, indicating the influence of precipitation.

    In the Western Upland Area, fluoride and nitrate have been detected at concentrations above background.

    The highest concentrations have been detected in the vicinity of the former U Ponds. However, because of remedial actions taken, uranium concentrations are no longer elevated in this area, and therefore they are not included in this report..

    4.3.3 Western Alluvial Area TDS concentrations are generally high throughout the Western Alluvial Area. Near the escarpment, TDS is in the range of 800 to 1,890 mg/L, but within the area with uranium impacts exceeding 180 pCi/L, TDS is in the range of 700 to 2,140 mg/L. At well T-82, the TDS concentration is 923 mg/L.

    The alkalinity concentration ranges from 230 to 438 mg/L, with calcium concentrations ranging from 144 to 406 mg/L and magnesium concentrations ranging from 29 to 84 mg/L. Sulfate concentrations ranged from 54 to 822 mg/Lacross the Western Alluvial Area.

    Nitrate and fluoride are present at concentrations above background in Seeps 1206 and 1208, and in the Western Alluvium. However, their distribution is not coincident with the uranium distribution.

    The Stiff diagrams of representative groundwater samples from the Western Alluvial Area are presented in Figure 4-2. There are two distinct types of water pattern in the alluvium.

    The first type of groundwater, represented by well T-64, has a Stiff diagram in a fairly symmetrical shape.

    This groundwater is characterized by relatively low TDS content with bicarbonate content being higher than sulfate and chloride and is categorized as a calcium bicarbonate water. The pattern and TDS range of this groundwater are similar to groundwaters from Sandstone A in the uplands and Sandstone B in the BA #1 Area. Therefore, this groundwater is likely to be from Sandstone A and B with its chemistry influenced by infiltrating rain precipitation.

    Report No. 04020-044 (Revision 01) 4-7 October 18, 2006

    ENSR AECOM The second type of groundwater is represented by wells T-72 and T-74. This groundwater is characterized by high TDS content with sulfate concentration greater than bicarbonate and chloride and is categorized as a calcium sulfate water. Chloride concentration can be higher than bicarbonate and sodium higher than magnesium in some samples. The geochemical signature of this groundwater is almost identical to that of Sandstone C groundwater, suggesting some contribution from Sandstone C into the alluvium.

    The spatial distribution of water types in the Western Alluvial Area is presented in Figure 4-9. A typical Sandstone C water from well 1332 is also shown for comparison. Of the 20 groundwater samples evaluated in the alluvium, eight exhibit the signature of Sandstone A and B groundwater (bicarbonate water), with the remaining showing the characteristics of Sandstone C groundwater (sulfate water).

    Generally, bicarbonate water predominates in areas adjacent to the escarpment whereas sulfate water is more abundant in areas away from the uplands.

    Comparisons of geochemical characteristics of groundwaters from the Western Upland Area and the Western Alluvial Area are graphically illustrated in Figure 4-10. As can be seen from this Piper Diagram, Sandstone A groundwater clusters at the bicarbonate corner while Sandstone C groundwater clusters at the sulfate corner, with groundwater in the alluvium spreading across the entire spectrum between the two groundwaters. Apparently, groundwater in the alluvium is from Sandstones A, B, and C with various degrees of mixing among them.

    4.4 Uranium Impacts to Groundwater 4.4.1 Geochemistry of Uranium Uranium (U) has 14 isotopes, with the atomic mass of these isotopes ranging from 227 to 240. Naturally occurring uranium typically contains 99.283 percent U 238, 0.711 percent U 235, and 0.0054 percent U 234.

    Uranium can exist in the U3+, U4+, U5+, and U6+ oxidation states, of which the U4+ and U6+ states are the most common states found in the environment.

    The chemical behavior of U4+ and U6+ is influenced by a variety of reactions including dissolution, precipitation, complexation, and sorption. These reactions are affected by the redox conditions, solution pH, water chemistry, and mineral-water interactions. The U4

    + species are sparingly soluble in aqueous solutions (less than 30 micrograms per liter [µg/L]) and tend to precipitate out under anoxic (reduced) conditions. U 6

    + species, in contrast, are fairly soluble and are responsible for the mobilization of uranium in oxidized conditions.

    In natural groundwater, U 6

    + can be transported in various aqueous species depending on the pH and groundwater composition. In the absence of carbonate, U6+ in the form of uranyl ion (UO2)2+

    predominates at pH below 5. At pH values between 5 and 9, the U6

    + hydrolytic species (UO2(OH)2 °)

    predominates. U6

    + has a strong tendency to form complexes with carbonate. In solutions where dissolved carbon dioxide is present, the neutral uranyl carbonate species (UO2CO3) predominates in the pH range between 5 and 6.5. Anionic uranyl dicarbonate (UO2(CO3)/-) and uranyl tricarbonate (UO2(CO3h4-) species predominate in the pH ranges between 6.5 to 8.5 and above 8.5, respectively.

    U6

    + is readily adsorbed onto an aquifer matrix or single-phase mineral, resulting in a reduction of its mobility in groundwater. Aqueous pH and water chemistry are the two most important factors controlling the adsorption for a given matrix. Groundwater pH affects not only uranium speciation, but also its adsorption onto aquifer materials. Generally a surface is positively charged at lower pH and negatively charged at higher pH. Therefore, lower pH favors the adsorption of anionic species such as uranyl Report No. 04020-044 (Revision 01) 4-8 October 18, 2006

    I ENSR i AECOM dicarbonate while higher pH facilitates adsorption of cationic species such as uranyl ion. The optimum pH values for uranium adsorption appear to be in the range between 5 and 8.

    The composition and concentration of ionic species in the groundwater will affect the speciation of uranium and the adsorption as well. Uranium adsorption in low-TDS water is relatively high and tends to decrease as TDS increases due to competition for adsorption sites from other constituents. Sulfate, for instance, is likely to interfere with the adsorption of uranyl dicarbonate and its removal at pH values above 6 if adsorption or ion exchange is utilized to treat uranium-impacted water.

    In an effort to understand the form of uranium that is being transported in groundwater and the propensity of uranium for adsorption under the Cimarron Site's conditions, speciation of uranium in groundwater was calculated using the geochemical model MINTEQA2 (USEPA Version 4.02, 2000). This information is useful in evaluating the fate and transport of uranium at the site and for design of a treatment system where the operating conditions are highly dependent on the speciation of uranium.

    MINTEQA2 is an equilibrium geochemical model that computes metal speciation in aqueous solutions, Developed by US EPA, this model is capable of calculating the equilibria among dissolved, adsorbed, solid, and gas phases. MINTEQA2 includes an extensive database of reliable thermodynamic data that allows for solving a broad range of problems encountered in a natural aqueous system. Input data required by the model consist of chemical analyses of total dissolved concentration for the components of interest. Field measured parameters such as pH and Eh can also be input to the model to specify equilibrium conditions, but are not necessary since these values can be calculated by the model.

    Analytical data of geochemical parameters (major cations, anions, ferrous and ferric iron, nitrate, fluoride, and silica) and uranium concentrations of selected groundwater samples obtained from September 2004 sampling event were input into the MINTEQA2 model to compute the uranium speciation. The samples selected included 02W01, 02W02, 02W04, 02W19, 02W21, 02W24, 02W31, 02W4 7, TMW-09, 1315R, 1314, and 1321, which are representatives of different TDS, sulfate, bicarbonate alkalinity, and uranium concentrations of groundwater across the site. Evaluation of these samples provide insight into the effects of the TDS, sulfate, and alkalinity on uranium speciation. Field measured temperature and pH values were used in all model runs. Eh values were not used in the model, as it was assumed that uranium in the site groundwater is in the 6+ valent state. This assumption is supported by the relatively high uranium concentrations and the presence of ferric iron oxides in the aquifer.

    The MINTEQA2 model results indicate that uranyl dicarbonate (UO2(CO3)/-) and uranyl tricarbonate (UO2(CO3)3 4-) are the predominant uranium species expected in groundwater at the site. The relative abundance of these two species depends on solution pH and bicarbonate alkalinity. Generally, the higher range of pH values and bicarbonate alkalinity concentrations favor the formation of uranyl tricarbonate.

    For most groundwater at the site; however, the concentration of uranyl dicarbonate is about two times higher than the uranyl tricarbonate species based on geochemical modeling. Other uranium aqueous species including uranyl carbonate and hydrolytic species may also be present, but in minor amounts (less than 2 percent), suggesting that the groundwater at the site has sufficient bicarbonate alkalinity to complex uranium. Sulfate was found to have no effect on the speciation of uranium at the site at the concentrations detected at the Cimarron Site.

    Report No. 04020-044 (Revision 01) 4-9 October 18, 2006

    I ENSR l AECOM I

    The estimated range of historical background concentrations of uranium observed in each of the water-bearing units is as follows:

    Sandstone A:

    Sandstone B:

    1.0 to 19.8 pCi/L (based on 7 wells);

    0.6 to 3.9 pCi/L (based on 5 wells);

    Sandstone C:

    4.6 to 43.6 pCi/L (based on 6 wells); and Alluvial floodplain:

    5.1 to 35.6 pCi/L (based on 9 wells).

    These estimated uranium background concentrations are an update to the previous calculations presented in the document titled "Groundwater Quantity and Quality in Vicinity of Cimarron Corporation's Former Nuclear Fuel Fabrication Facility, Crescent, Oklahoma" 1997, and new well selections provided by Cimarron Corporation hydrogeologists.

    4.4.2 BA #1 Area Monitoring wells installed in 1985 detected uranium immediately downgradient (to the north) of the four trenches in the BA #1 Area. The impacted groundwater was found in Sandstone B (which underlies the trenches) and was subsequently found to continue northward into the alluvial floodplain. The origin of the groundwater impacts was likely the four trenches, but the timing of the migration of uranium from the trenches into Sandstone B is uncertain. The monitoring wells installed in 1985 detected a plume of uranium, with concentrations of total uranium up to 2,500 pCi/L, suggesting that the uranium began migrating in groundwater prior to 1985.

    When uranium leached from the former disposal trenches, it was carried into Sandstone B, where it migrated north toward the alluvium driven by the local hydraulic gradient. Groundwater flow velocity in Sandstone B is anticipated to be relatively high because of the steep hydraulic gradient in Sandstone B.

    Once the groundwater reached the interface between the sandstone and the alluvial deposits at the buried escarpment, it refracted to the northwest under the influence of a mass of low-permeability clayey material to the northeast of the escarpment. This low permeability material interrupted the northern flow of Sandstone B groundwater and forced it to flow along a southeastern-northwestern trending paleochannel filled with higher permeability sandy material between the sandstone and the clayey materials in the transitional zone. Flow in the sandy paleochannel was uninterrupted until the groundwater encountered a clay-rich barrier in an area between TMW-9 and 02W01 as discussed in Section 2.3.1 (Detailed Stratrigraphic Correlations at Cimarron - BA #1 Area) of this report. This clay-rich barrier affects the migration of uranium both by virtue of its lower permeability and its increased adsorption potential. After the uranium-impacted groundwater migrated through the clay-rich barrier, its flow continued to be slowed by the extremely flat gradient in the sandier alluvial materials, as shown in Figure 3-4.

    The spatial distribution of uranium in the BA #1 Area is illustrated in Figure 4-11. As is shown, the uranium concentration varied from background levels to over 4,000 pCi/L based on the August/September 2004 groundwater monitoring data. The uranium plume, defined as uranium concentration exceeding the site-specific groundwater release criteria of 180 pCi/L, has an elongated shape, with the southern portion trending from southeast to northwest and the northern portion from south to north. The orientation and distribution of the plume coincides with the location of the paleochannel, discussed in Section 2.3.1 (Detailed Stratrigraphic Correlations at Cimarron - BA #1 Area) of this report, indicating that the migration of uranium near the escarpment may be influenced by the paleochannel. In areas farther away from the uplands, the movement of uranium is affected by the regional groundwater gradient resulting in its movement toward the Cimarron River channel.

    Report No. 04020-044 (Revision 01) 4-10 October 18, 2006

    ENSR AECOM A comparison of the groundwater monitoring data from the August/September 2004 sampling event (Figure 4-11) and the August 2002 (Figure 4-12) event revealed some changes in the uranium distribution between the two data sets. The main differences are:

    The highest observed uranium concentration has decreased from 5,035 pCi/L (TMW-09) during 2002 to 4,387 pCi/L in 2004 The area containing groundwater above 2,000 pCi/L total uranium appears to have advanced and spread out.

    The plume's leading edge has shifted toward the east relative to its 2002 location and there is little advancement to the north towards the Cimarron River.

    Figures 4-11 and 4-12 were developed for comparative purposes, and provide a means for comparing the uranium data from two groundwater sampling events.

    Based on data of only two site-wide sampling events, it is difficult to determine whether the spatial variation of the plume is statistically significant. However, there are seven wells (TMW-13, 02W04, 02W07, 02W08, 02W19, 02W43, and 02W62) in the northern portion of the plume that have more than four quarters' data available. For those wells the Mann-Kendall statistics was calculated to evaluate whether the concentration fluctuation was random or directional. The analysis indicated that except for one well (02W19) which showed an upward trend, there is no clear trend associated with the data in other wells, suggesting the concentration variations in those wells were random.

    4.4.3 Western Upland Area The BA #3 Area was excavated, surveyed by Cimarron and the NRC, and backfilled with clean soil prior to 1994. At the Seep 1206 sample collection point, the elevated uranium concentration in a sample collected in 1985 appeared to be spatially related to the BA #3 Area.

    Historically, samples designated as being collected from the 1206 Seep were in fact collected from a pool of accumulated surface water near the escarpment. This Seep 1206 sampling location is identified in Figures 2-3, 2-8, 3-3, and 4-13 and represents, a location where water accumulates from a number of seeps along the escarpment.

    Since 2003, total uranium concentrations observed in samples from the 1206 Seep collection point appear to be declining. In 2002, uranium values were in the range of 150 to 170 pCi/L. By March 2003, the reported values were around 200 pCi/L. In June 2003, the uranium values sharply declined to approximately 100 pCi/L. In January 2004, the uranium concentration subsequently increased to values around 180 pCi/L. Since that time, the uranium concentrations in samples from the collection pool have been steadily declining and are currently in the range of 100 pCi/L.

    Because of the potential for the evapoconcentration of uranium in the surface water collection pools, the concentrations of uranium observed at this location may not be representative of the actual groundwater in this area. This suspicion is supported by the data from wells in the proximity of this area (wells 1354, 1355, 1357, and 1358), which have uranium concentrations below 5 pCi/L. A monitor well located downgradient of 1357 and 1358 may be better suited to evaluate impacts from the BA #3 Area.

    Three wells in the BA #3 Area (1351, 1352, and 1356) have also exhibited unexpected fluctuations in uranium concentrations. Observed uranium concentrations in these three wells have fluctuated in the range of 67 pCi/L to 725 pCi/L over the last two years of groundwater monitoring (2003-2005).

    Report No. 04020-044 (Revision 01) 4-11 October 18, 2006

    ENSR AECOM Uranium and water quality data from the AugusUSeptember 2004 groundwater sampling event for the Western Upland Area is presented in Figure 4-14.

    4.4.4 Western Alluvial Area The uranium impacts detected in the Western Alluvial Area above the site-specific groundwater release criteria of 180 pCi/L extend from near the base of the escarpment northward toward the Cimarron River, apparently originating where the western pipeline entered the alluvium north of the former Sanitary Lagoons. Uranium and water quality data from the AugusUSeptember 2004 groundwater sampling event for the Western Alluvial Area is presented in Figure 4-15.

    The observed impacts parallel the trace of the former West Pipeline Corridor that was used to discharge wastewater to the Cimarron River from 1966 to 1970. This pipeline and associated soils exceeding 30 pCi/g were removed in 1985, and the corridor backfilled with clean soil.

    Concentrations of uranium detected in the Western Alluvial Area wells are generally in the range of 150 to 250 pCi/L. Concentrations in most wells have not varied to any noticeable degree over the past 2 years of sampling. Wells near the escarpment, mainly wells T-62 and T-64 are the main exceptions. The groundwater impacts in the Western Alluvial Area are not typical of a plume in the sense that a plume has a continuing source and represents a moving and changing zone of dissolved uranium in groundwater; rather, the groundwater impacts in the Western Alluvial Area are the result of downward seepage (i.e., no horizontal flow component) of uranium from a former pipeline that leaked uranium-bearing wastewater during the operational period of the Cimarron facility.

    Two groundwater monitoring wells were installed in the Western "transition" area; one in the 1206 drainage (MWWA-09) and the other in the alignment where the former west pipeline was located (MWWA-03). Soil borings were sampled and analyzed for total U during installation of the wells; values ranged between 2.4 to 7.68 + or - ~1.1 (pCi/g) for soils from MWWA-03 and MWWA-09. Groundwater samples yielded 268 pCi/L (MWWA-09) and 1110 pCi/L (MWWA-03). It is possible that the pipeline leak has impacted both soil and groundwater near MWWA-03, and seepage from Burial Area #3 has impacted both soil and groundwater near MWWA-09.

    4.4.5 Surface Water The Cimarron River is relatively saline due to contributions in the northwest part of Oklahoma from Permian evaporite beds. The water quality of the Cimarron River is presented in Table 4-2 and was summarized from Adams and Bergman (1994) and data available on the USGS National Water Information System (NWIS) water data website. The TDS concentration of the Cimarron River water decreases from the Waynoka gage southeast to the Guthrie gage, which is located 10 miles east of the Cimarron Site. Similarly, sodium, chloride, and sulfate concentrations also decrease. This is due to the decreasing influence of Permian-age evaporite beds on the river chemistry and the greater influence of runoff from farmed areas and sewage outfalls. In the area of the Cimarron Site, which lies between the Dover and Guthrie gages, the Cimarron River can be expected to have TDS in the range of 8,000 to 12,000 mg/L, chloride between 3,600 and 5,700 mg/L, sulfate between 650 and 780 mg/L, sodium ranging from 1,900 to 3,400 mg/L, and alkalinity (bicarbonate) in the range of 200 mg/L. This water chemistry is very distinct from the groundwater chemistry of the alluvial floodplain. Based on the Secondary Maximum Concentration Limits (MCLs) recommended by the United States Environmental Protection Agency (USEPA) for drinking water, this water is considered non-potable.

    Report No. 04020-044 (Revision 01) 4-12 October 18, 2006

    ENSR AECOM Samples collected from the Cimarron River in June 1997 exhibited a mean total uranium concentration of 8.1 pCi/L at the upstream sample location, and 7.3 pCi/L at sample location 1202 downstream of the Cimarron site. (Cimarron Decommissioning Plan Groundwater Evaluation Report for Cimarron Corporation's Former Nuclear Fuel Fabrication Facility, Crescent, Oklahoma, July, 1998).

    Report No. 04020-044 (Revision 01) 4-13 October 18, 2006

    Table 4-1 A Water Bearing Well ID Unit Burial Area #1 02W01 Alluvial 02W02 Alluvial 02W03 Alluvial 02W04 Alluvial 02W0S Alluvial 02W06 Alluvial 02W07 Alluvial 02W08 Alluvial 02W09 Alluvial 02W10 Alluvial 02W11 Alluvial 02W12 Alluvial 02W13 Alluvial 02W14 Alluvial 02W15 Alluvial 02W16 Alluvial 02W17 Alluvial 02W18 Alluvial 02W19 Alluvial 02W20 Alluvial 02W21 Alluvial 02W22 Alluvial 02W23 Alluvial 02W24 Alluvial 02W25 SS B 02W26 Alluvial 02W27 SS B 02W28 Alluvial Report No. 04020-044 (Revision 01) t/S Dissolved Oxygen1 (mgll) 1.5 1.1 5.9 1.5 1.0 1.1 1.5 1.6 2.0 1.7 1.4 1.7 1.9 2.2 1.5 1.5 ber 2004 G d

    Nitrate2*3 pH1 (mgll) 0.3 7.2 0.1 7.4 0.1 7.1 7.1 0.118 7.0 0.2 7.1 4.6 7.2 0.1 7.1 0.1 7.3 0.1 7.2 0.1 7.1 0.1 7.1 0.1 6.9 0.1 7.1 0.1 7.2 0.1 7.1 0.1 7.1 0.1 7.1 0.1 7.1 7.1 7.1 7.0 6.9 7.0 7.0 7.2 7.1 7.2 M

    Redox Potential1 Uranium2 Calcium2 (mv)

    (pCill)

    (mgll) 271 4150 127 14 692.3 89.3 64 3779 132 224 1789.8 171 216 2542 182 218 3462 179 279 732.4 171 82 120.0 182 200 1.8 61.3 3.2 91.5 29.0 177 43.7 125 30.5 142 113.7 155 195 59.8 226 24.3 254 228 39.8 218 124 744.7 167 799.3 141 48 1.5 80.8 5.6 205 8.6 210 228 7.2 209 120 117.2 213 62 13.2 93 2.186 63.7 153.5 135 300 77 4-14 ENSR I AF(OM Total Bicarbonte Total Dissolved Chloride2*3 Magnesium2 Sodium2 Sulfate2*3 Alkalinity2*3 Alkalinity2*3 Solids2 (mall)

    (mall)

    (mgll)

    (mgll)

    (mgll)

    (mgll)

    (mall) 22.3 42.3 36.8 81.4 432 433 535 24.7 40.8 78.3 46.3 450 451 719 31.2 61.2 60.3 85.6 555 556 1220 47.7 84.9 90.6 433 452 454 1160 150 113 170 283 673 677 1360 62.1 67.5 91.5 273 512 513 1050 40.1 59.5 75.3 320 426 427 519 23.2 56 52.7 281 545 550 581 18.5 55.1 24.2 29 378 379 590 26.4 73.7 39.4 56.7 489 492 1330 38.3 60.3 70.5 279 527 534 699 22.3 50.5 50.8 131 463 465 661 18.7 44.3 33.4 95.1 501 502 920 35.3 59.7 84.7 195 553 556 1530 86.8 94.3 115 629 355 359 1440 49 77.5 67.5 626 346 347 1240 56.3 65 63.4 475 346 347 1090 35.2 49.1 66.6 328 410 411 1010 40.3 56.7 77.7 175 479 481 832 19.3 51.9 23.5 53.7 347 347 475 23.8 52.3 49 458 192 192 1030 41.4 65.6 58.3 478 352 353 1130 34.7 52.4 51.1 510 261 262 1160 50.6 65 58.8 520 325 326 1200 2.46 21.6 15.7 10.3 240 240 358 19.6 54.7 24 25.5 352 353 442 23.2 60.3 66.4 59.7 282 283 629 21 60.8 27.9 31.7 389 390 496 October 18, 2006

    Table 4-1 A -

    Water Bearing Well ID Unit 02W29 Alluvial 02W30 SS B 02W31 Alluvial 02W32 Alluvial 02W33 Alluvial 02W34 Alluvial 02W35 Alluvial 02W36 Alluvial 02W37 Alluvial 02W38 Alluvial 02W39 Alluvial 02W40 SS B 02W41 SS B 02W42 SS B 02W43 Alluvial 02W44 Alluvial 02W45 Alluvial 02W46 Alluvial 02W47 SS B 02W50 SS B 02W51 SS B 02W52 SS B 02W53 SS B 02W62 Alluvial 1314 SS B 1315R SS B 1316R SS B TMW-01 SS B TMW-02 SS B Report No. 04020-044 (Revision 01) t/S ber 2004 G Dissolved Oxygen1 Nitrate2*3 (mg/L)

    (mg/L) 1.8 0.9 0.1 3.7 1.9 2.4 3.6 0.1 1.3 0.451 6.9 1.2 2.47 6.2 4.5 M

    C Redox pH1 Potential1 Uranium2 Calcium2 (mv)

    (pCi/L)

    (mg/L) 7.3 271 1845 106 6.9 457.4 146 7.2 570.5 76.4 7.1 413.3 117 6.9 7.5 237 7.1 4.0 101 7.0 167 133 7.0 91 92.9 190 7.0 433 152 7.0 101.9 150 7.2 264 1209.7 95.8 7.2 290 1577 103 7.2 250 965.9 87.3 7.0 238 130.7 108 7.1 169.9 202 7.0 157.8 133 7.1 61 120.6 214 7.3 1377.4 109 6.7 375.8 121 7.4 3.5 72.5 7.6 274 5.4 57.4 7.4 1.9 60.9 7.1 76.7 130 7.0 5.5 130 7.3 1.8 66.4 6.8 273 1793 183 6.9 151.7 152 6.7 190 1198.8 148 7.6 219 2.5 53.4 4-15 ENSR I AFCOM Total Bicarbonte Total Dissolved Chloride2*3 Magnesium2 Sodium2 Sulfate2*3 Alkalinity2*3 Alkalinity2*3 Solids2 (mg/L)

    (mg/L)

    (mg/L)

    (mg/L)

    (mall)

    (mg/L)

    (mg/L) 7.83 35.3 15.1 22 330 331 441 59.2 49.1 35.2 43.2 448 449 656 18.6 59 26.9 36.3 479 481 499 31 63.7 61 124 378 379 707 55.3 75.6 67.2 558 266 267 1310 24.7 20.1 44.2 45.8 298 299 463 85.7 39.2 75.3 139 298 299 731 75.7 61.2 78.2 424 303 305 1140 122 76.1 163 191 618 622 1120 64.5 72.8 130 130 564 566 984 9.5 35.4 15.5 19.1 372 374 391 7.01 38.2 12 23.3 373 374 437 6.17 31.2 12.6 16.3 368 369 389 2.8 27.2 13.7 19 341 342 426 57 69.5 74.5 521 364 366 1240 58.3 60.6 81.5 132 586 588 924 198 57 139 396 447 449 1330 27.1 66.6 55.9 72.8 543 545 686 10.3 48 13 29.3 473 474 535 16.4 26.9 22 8.47 277 278 369 2.2 18.9 11.9 23.3 229 230 254 15.6 22.4 19.2 7.75 361 363 322 117 53.3 86.6 184 420 422 911 62 29.9 66.4 123 404 406 691 15.9 22 16.7 6.89 240 241 303 22.5 70.9 30.1 102 628 629 816 11.8 46.7 20.1 30.5 222 222 611 6.99 52.5 14.6 95 443 443 635 5.23 19.5 18.4 11.5 234 235 254 October 18, 2006

    Table 4-1 A

    Water Bearing Well ID Unit TMW-05 Alluvial TMW-06 Alluvial TMW-07 Alluvial TMW-08 SS B TMW-09 Alluvial TMW-13 Alluvial TMW-17 SSC TMW-18 SS B TMW-21 SS B TMW-23 SSC TMW-24 Alluvial TMW-25 SS B Minimum Alluvial Maximum Alluvial Minimum SS B Maximum SS B Minimum SSC Maximum SSC Western UI,land Area 1206 Surface 1331 SSA 1332 SSC Report No. 04020-044 (Revision 01) t/S ber 2004 G d

    Dissolved Oxygen1 Nitrate2*3 pH1 (mall)

    (mall) 0.9 7.1 1.3 7.3 1.0 7.2 3.7 7.0 6.9 7.2 6.9 7.1 5.9 7.1 7.2 0.7 6.9 7.2 0.7 0.1 6.9 TMW-24 02W37 TMW-24 5.9 4.6 7.4 02W03 02W07 02W02 1.2 6.7 1315R 02W47 6.9 7.6 02W51 02W51 6.9 TMW-17 7.2 TMW-23 "T-

    .,*........,~ y*--.

    ~ ~-,*,~

    2.9 3.91 7.3 7.1 7.4 M

    C Redox Potential1 Uranium2 Calcium2 (mv)

    (pCi/l)

    (mall) 84 2.5 95.3 35 2.5 95.3

    -9 26.8 93.9 262 3066 94.3 4387 127 4096 136 4.7 161 12.4 311 312 116.2 149 7.9 173 22 28.8 186 179.2 67

    -9 1.5 61.3 TMW-07 02W20 02W09 279 4387 254 02W07 TMW-09 02W16 62 1.782 53.4 02W25 1314 TMW-02 312 3066 311 TMW-21 TMW-08 TMW-18 4.67 161 TMW-17 TMW-17 7.9 173 TMW-23 TMW-23 259 109.0 97.8 82.2 32.2 4-16 ENSR I AFCOM Total Bicarbonte Total Dissolved Chloride2*3 Magnesium2 Sodium2 Sulfate2*3 Alkalinity2*3 Alkalinity2*3 Solids2 (mgll)

    (mgll)

    (mgll)

    (mgll)

    (mgll)

    (mall)

    (mall) 25.7 66.9 35.5 57.4 506 508 607 27.2 61.6 33.9 67.1 522 524 559 21.6 55.4 40 40.1 490 492 542 I

    18.6 47.1 19.5 21.6 411 412 491 16 39 28.6 76.6 422 424 566 73 89.2 120 181 264 264 1010 23.3 45 40.9 301 320 321 830 285 113 183 799 251 251 2060 8.72 55.5 29.6 30.1 586 588 616 101 46.1 115 332 325 326 987 149 74.1 90.8 252 480 481 1120 22.8 16.7 7.83 20.1 15.1 19.1 192 192 391 02W29 02W33 02W29 02W39 02W21 02W21 02W39 198 113 170 629 673 677 1530 02W45 02W15 02W05 02W15 02W05 02W05 02W14 2.2 18.9 11.9 6.89 222 222 254 02W51 02W51 02W51 1314 1316R 1316R 02W51 285 113 183 799 628 629 2060 TMW-18 TMW-18 TMW-18 TMW-18 1315R 1315R TMW-18 23.3 45 40.9 301 320 321 830 TMW-17 TMW-17 TMW-17 TMW-17 TMW-17 TMW-17 TMW-17 101 46.1 115 332 325 326 987 TMW-23 TMW-23 TMW-23 TMW-23 TMW-23 TMW-23 TMW-23 6.41 35.8 30.6 31.5 402 407 518 October 18, 2006

    Table 4-1 A Water Bearing Well ID Unit 1334 SSA 1348 SSA 1349 SSA 1350 SSA 1351 SSA 1352 SSA 1353 SSA 1354 SSA 1355 SSA 1356 SSA 1357 SSA 1358 SSA 1359 SSA 1360 SSA Minimum SSA Maximum SSA Western Alluvial Area T-58 Alluvial T-62 Alluvial T-63 Alluvial T-64 Alluvial Report No. 04020-044 (Revision 01) t/Seot ber 2004 G Dissolved Oxygen1 Nitrate2*3 (mg/L)

    (mg/L) 5.6 1.3 16.8 1.9 10.5 1.1 44.8 1.8 80.9 1.2 5.0 14.7 2.0 166.0 79.6 3.9 19.3 1.4 57.0 3.4 26.2 1.1 21.1 1.1 0.2 1.1 0.2

    1350, 1360 1360 5.6 166.0 1334 1354 3.6 2.7 1.2 1.9 dwater Monit D

    c*

    Redox pH1 Potential1 Uranium2 Calcium2 (mv)

    (pCi/L)

    (mg/L) 7.2 219 13.3 72.5 7.3 233 136.7 24.7 7.2 215 43.5 79.5 7.3 269 35.6 82.8 7.0 266 67.2 115 7.0 247 736 137 7.1 177 78.6 7.0 262 3.1 197 7.5 2.4 69.3 7.0 244 269.7 109 7.1 286 2.4 83.6 7.4 264 1.2 65.9 7.1 258 26.1 90.6 7.2 262 86.8 30.8 7.0 177 1.2 24.7 1356 1353 1358 1348 7.5 286 736 197 1355 1357 1352 1354 7.1 338 26.4 144 7.1 335 416.3 167 6.8 249 54.6 221 7.2 327 835.6 119 4-17 ENSR I AFCOM s*

    C Total Bicarbonte Total Dissolved Chloride2*3 Magnesium2 Sodium2 Sulfate2*3 Alkalinity2*3 Alkalinity2*3 Solids2 (mg/L)

    (mg/L)

    (mg/L)

    (mg/L)

    (mg/L)

    (mg/L)

    (mg/L) 38.3 48.3 31.5 324 325 461 3.72 9.13 15.3 20.2 277 278 206 7.43 27.7 48.1 45.1 309 310 457 4.38 28.8 24.4 22.2 261 262 564 3.6 45 20.1 20.1 251 251 704 6.2 31 47.2 24.4 295 297 527 5.39 23.4 21.9 20.7 256 256 400 6.52 86.7 23 11.1 288 289 1310 3.58 23 14.5 12 176 176 720 9.93 35.1 12.9 36.5 324 326 498 3.81 30.6 16.5 12.9 245 246 533 3.09 22.1 18.8 15.9 203 203 464 6.45 30.3 24.8 30.1 288 289 559 6.19 11.3 10.8 36.5 357 358 1010 3.09 9.13 10.8 11.1 176 176 206 1358 1348 1360 1354 1355 1355 1348 9.93 86.7 48.3 45.1 357 358 1310 1356 1354 1334 1349 1360 1360 1354 19.2 47.8 35.3 182 229 230 843 18.6 69.6 57.5 73.1 405 406 1040 29 83.3 69.2 59.2 351 352 1720 46.3 50.5 73.1 106 405 406 818 October 18, 2006

    Table 4-1 A

    t/Seot ber 2004 G dwater Monit Data. c*

    Well ID T-65 T-66 T-67 T-68 T-69 T-70R T-72 T-73 T-74 T-75 T-76 T-77 T-78 T-79 T-81 T-82 Minimum Maximum NOTES:

    Water Dissolved Redox Bearing Oxygen1 Nitrate2*3 pH1 Potential1 Uranium2 Unit (mgll)

    (mgll)

    (mv)

    (pCill)

    Alluvial 1.8 7.1 318 178.5 Alluvial 1.8 7.1 322 105.2 Alluvial 1.2 39.0 7.0 263 197.7 Alluvial 1.8 7.1 311 107.0 Alluvial 1.3 7.0 315 49.6 Alluvial 1.4 7.2 290 200.9 Alluvial 1.8 7.1 288 119.9 Alluvial 1.4 7.1 283 11.6 Alluvial 2.4 7.2 307 20.6 Alluvial 1.1 7.1 263 278.7 Alluvial 1.3 7.1 282 206.6 Alluvial 1.0 7.0 267 231.7 Alluvial 1.9 7.1 279 23.76 Alluvial 1.1 7.2 298 231.2 Alluvial 2.3 7.1 286 20.21 Alluvial 1.4 7.1 261 103.8 Alluvial 1.0 39.0 6.8 249 11.6 T-77 T-67 T-63 T-63 T-73 Alluvial 3.6 39.0 7.2 338 835.6 T-58 T-67 T-74 T-58 T-64 1 - Data collected in the field and provided by the Cimarron Hydrogeologic Staff.

    2 - Analyzed by off-site laboratory (General Engineering Labs, Charleston, SC).

    Calcium2 (mgll) 171 297 193 198 235 120 259 114 241 248 152 293 289 125 101 145 101 T-81 297 T-66 Site. C

    t. Oklah Chloride2*3 Magnesium2 Sodium2 (mall)

    (mall)

    (mall) 18.9 63.4 52.9 75.8 84.3 121 29 57.1 80.4 150 58.6 158 55 72.3 93.4 29 39.7 51.4 112 73.6 124 54.2 45.5 54.7 124 65.8 111 200 73.8 187 25 52.4 57.5 70.9 83.3 348 319 72.4 289 81.8 38.4 95 48.5 35 60.3 120 43.7 120 18.6 35 35.3 T-62 T-81 T-58 319 84.3 348 T-78 T-66 T-77 3 - Off-site laboratory data has been QA/QC reviewed and qualified. Qualifier flags have been removed for presentation purposes.

    Report No. 04020-044 (Revision 01) 4-18 ENSR I AFCOM Total Bicarbonte Total Dissolved Sulfate2*3 Alkalinity2*3 Alkalinity2*3 Solids2 (mall)

    (mall)

    (mgll)

    (mgll) 94.2 437 438 1030 734 266 267 1890 205 373 377 988 426 373 374 1400 543 293 294 1550 171 341 342 674 653 298 299 1650 83 330 331 629 609 373 374 1440 675 314 315 1700 138 389 390 869 104 369 372 749 822 292 294 2140 197 373 374 828 54.6 372 374 542 232 388 390 923 54.6 229 230 542 T-81 T-58 T-58 T-81 822 437 438 2140 T-78 T-65 T-65 T-78 October 18, 2006

    ENSR I AF(OM Table 4-2 Cimarron River Water Quality Data, Cimarron Site, Crescent, Oklahoma SPECIFIC TOTAL TOTAL DISCHARGE pH POTASSIUM SILICA CALCIUM CHLORIDE2 MAGNESIUM SODIUM SULFATE2 DISSOLVED SAMPLE LOCATION CONDUCTANCE ALKALINITY SOLIDS2 (cfs)

    (mg/L)

    (mg/L)

    (umhos)

    (mg/L)

    (mg/L)

    (mg/L)

    (mg/L)

    (mg/L)

    (mg/L)

    (mg/L)

    .. ~*,

    ~

    -~, ~

    ~

    Waynoka Gage (2-86) 149 8.2 9.6 10 27,000 290 9,100 100 5,400 940 173 16,600 (Adams et al, 1994)

    Ranges (1979-1990) 9-17,700 7.5-8.4 10 44,200-51,000 120-450 5,000-26-160 2,000-240-1400 5,900-35,900 (USGS NWIS Waterdata) 21,000 12,000 Dover Gage (2-86) 304 8.1 7.6 5.1 12,100 240 5,700 89 3,400 780 193 10,600 (Adams et al, 1994)

    Ranges (1979-1989) 7.5-8.4 6-12 3,270-29,000 76-310 830-9,500 17-100 550-5,800 200-780 1,840-17,300 (USGS NWIS Waterdata)

    ., -~

    -* r--,

    ~ --*

    ~

    ~

    "-~ --

    ~-,* -- -v,

    ....... d

    ~-.

    Guthrie Gage 1 (2-86) 466 8.4 6.4 6.1 12,000 200 3,600 79 1,900 650 210 7,090 (Adams et al, 1994)

    Note (1 ): Guthrie Gage is located approximately 1 0 miles east of the Cimarron site.

    Note (2): All values for chlorides, sulfates, and TDS reported represent exceedances of the US EPA Secondary Drinking Water Maximum Concentration Limits (MCLs) i.e., 250 mg/L for chlorides/sulfates; 500 mg/L for TDS Report No. 04020-044 (Revision 01) 4-19 October 18, 2006

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