[Advances in Chemistry] Aquatic Humic Substances Volume 219 (Influence on Fate and Treatment of Pollutants) || The Fate and Removal of Radioactive Iodine in the Aquatic Environment

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<ul><li><p>35 The Fate and Removal of Radioactive Iodine in the Aquatic Environment </p><p>R. Scott Summers1, Friedrich Fuchs, and Heinrich Sontheimer </p><p>Engler-Bunte-Institut, Universitt Karlsruhe, 7500 Karlsruhe, Federal Republic of Germany </p><p>The reaction of iodine with aquatic humic substances (HS) and the subsequent removal of the products by typical drinking-water-treat-ment processes was investigated. Both iodine and iodide react com-pletely with isolated HS in the concentration range below 0.03 mg of I per mg of HS and behave similarly with Rhine River water. The reaction is independent of pH, initial HS concentration, and HS molecular size. However, at higher I-HS ratios iodine reacts slightly more than iodide. Kinetic studies indicate that the reaction is complete within 10 min. No interaction was found between methyl iodide and HS. Flocculation and activated-carbon (AC) adsorption were effective for the removal of the I-HS complex, and the dissolved organic carbon measurement served as a good surrogate parameter. Volatil-ization and AC adsorption were effective for methyl iodide removal. </p><p>/JLFTER A NUCLEAR REACTOR ACCIDENT the release of radionuclides poses a problem for drinking-water-treatment facilities using surface waters as their raw water source. A recent nuclear power plant accident resulted in high levels of radioactivity in the environment throughout Europe, as shown in Table I for the Federal Republic of Germany. The highest activity levels occurred in the southern part of the country where, fortunately, 95% of the potable water originates from ground-water aquifers that were not directly contaminated. However, for communities that use surface waters, an un-</p><p>1Current address: Civil and Environmental Engineering Department, University of Cincinnati, Cincinnati, O H 45221-0071 </p><p>0065-2393/89/0219-0623$06.00/0 1989 American Chemical Society </p><p>Dow</p><p>nloa</p><p>ded </p><p>by U</p><p>CSF</p><p> LIB</p><p> CK</p><p>M R</p><p>SCS </p><p>MG</p><p>MT</p><p> on </p><p>Sept</p><p>embe</p><p>r 4,</p><p> 201</p><p>4 | h</p><p>ttp://</p><p>pubs</p><p>.acs</p><p>.org</p><p> P</p><p>ublic</p><p>atio</p><p>n D</p><p>ate:</p><p> Dec</p><p>embe</p><p>r 15</p><p>, 198</p><p>8 | d</p><p>oi: 1</p><p>0.10</p><p>21/b</p><p>a-19</p><p>88-0</p><p>219.</p><p>ch03</p><p>5</p><p>In Aquatic Humic Substances; Suffet, I., et al.; Advances in Chemistry; American Chemical Society: Washington, DC, 1988. </p></li><li><p>624 AQUATIC HUMIC SUBSTANCES </p><p>Table I. Radioactivity Levels in the Federal Republic of Germany after the Chernobyl Accident </p><p>Maximum Reported Main Ref. Source Activity Component Ref. </p><p>Air (Bq/m3) 150 1-131 1 Ground (Bq/m2) 280,000 1-131 1 Aqueous (Bq/L) </p><p>Rain 35,000 1-132 or 1-131 2 River 370 1-131 2 Reservoir 570 1-131 2 Ground </p></li><li><p>35. SUMMERS ET AL. Radioactive Iodine in the Aquatic Environment 625 </p><p>were also measured in order to find an indicator parameter that could be measured more easily than radioactivity. </p><p>One problem encountered was the determination of the appropriate species of iodine to use in such an investigation. Metal iodide is the chemical form that escapes from the reactor core (7); however, the form of iodine predominating after exposure to the atmosphere is not completely understood. The form is thought to be dependent on the conditions in the containment building; the volatile elemental iodine and methyl iodide are important with respect to atmospheric release. </p><p>Experimental Details The humic substances used in this study were isolated by a strong basic anionic resin (Lewatit MP 500 A, Bayer Chemical Co.) used in the treatment of ground water with a high humic content (7 g of DOC/m3) in Fuhrberg, Federal Republic of Germany. The resins were regenerated with a solution containing 10% NaCl and 2% NaOH (8). The regenerate has a molecular size (MS) range of 200-4000, with an average of 1500 as estimated by gel-permeation chromatography (GPC). The experimental solution properties for the Fuhrberg humic-substances (FHS) are shown in Table II. </p><p>The GPC of the Rhine River sample indicates a MS range of 160-5000, with an average of about 1500. Samples of the Rhine River were taken at Karlsruhe, Federal Republic of Germany, approximately 360 km downstream of Lake Constance. Their properties are also shown in Table II. The radionuclide 1-131 was supplied in a carrier solution of Nal at a ratio of 4.72 104 Bq^g of I, and the solution activity was analyzed by 7-ray spectrometry. The concentrations of I" and I2 were analyzed by the leuco crystal violet method (6) with a detection limit of 5 mg/m3 in the Rhine River and FHS solutions. The DPD (N,N-diethyl-p-phenylenediamine) photometric method was used to measure chlorine (6). The concentration of CH3I was measured with an electron-capture detector-gas chromatograph with a detection limit of less than 0.1 mg/m3. </p><p>The reaction experiments between I~, I2, or CH3I and the FHS or Rhine River water were conducted in 0.1- or 0.25-L closed volumetric flasks. Flocculation was conducted in 1-L glass beakers with the addition of iron sulfate at high mixing intensities (250 rpm) for 5 min, followed by 10 min of flocculation at 50 rpm and 30 min of settling. The cationic polyelectrolyte, poly aery lam ide (PAA), when used, was added 2.5 min after the addition of iron sulfate. Filtration utilized glass-fiber filters or 0.45- membrane filters. Adsorption experiments were conducted with closed 0.25-L bottles on a shaker-table (250 rpm) at a contact time of 2 days with pulverized activated carbon (F300, Chemviron Corp.). In the combined floccula-</p><p>Table II. Properties of Fuhrberg Humic Substances and Rhine River Sample DOC UV-254 Redox Temperature Turbidity </p><p>Sample (g/m3) (m-*) pH (mV) (C) (FTUa) Rhine River 2.62 6.52 7.65 240 19.6 2.9 Fuhrberg humic substances 4.20 16.3 6.5 515 20 "Formazine turbidity units. </p><p>Dow</p><p>nloa</p><p>ded </p><p>by U</p><p>CSF</p><p> LIB</p><p> CK</p><p>M R</p><p>SCS </p><p>MG</p><p>MT</p><p> on </p><p>Sept</p><p>embe</p><p>r 4,</p><p> 201</p><p>4 | h</p><p>ttp://</p><p>pubs</p><p>.acs</p><p>.org</p><p> P</p><p>ublic</p><p>atio</p><p>n D</p><p>ate:</p><p> Dec</p><p>embe</p><p>r 15</p><p>, 198</p><p>8 | d</p><p>oi: 1</p><p>0.10</p><p>21/b</p><p>a-19</p><p>88-0</p><p>219.</p><p>ch03</p><p>5</p><p>In Aquatic Humic Substances; Suffet, I., et al.; Advances in Chemistry; American Chemical Society: Washington, DC, 1988. </p></li><li><p>626 AQUATIC HUMIC SUBSTANCES </p><p>tion-activated-carbon adsorption experiments, the pulverized carbon was added to the beaker at high mixing intensities 10 min prior to the addition of iron sulfate; it was filtered out with the sludge; the result was a 1-h contact time. </p><p>Results and Discussion Reaction with Humic Substances. The reaction kinetics of ele</p><p>mental iodine, I 2 , and iodide, I", with F H S over a 2-week period are shown in Table III. A l l initial solutions of I 2 used throughout this study contained 27% iodide. For both iodine and iodide the reaction with F H S is very fast, with no additional reduction in solution concentration occurring after 10 min. The reaction may even be faster, but this possibility could not be assessed, as 10 min was required for analytical sample preparation. The reaction kinetics of iodine and chlorine with the F H S can be seen in Figure 1. The iodine reaction is much faster than that of chlorine, which displays continued formation of organic-bound chlorine over a 17-h period. </p><p>A l l nonorganic-bound iodine is reduced to iodide in the reaction between 1 2 and F H S , as shown in Table HI . This result can also be seen in Figure 2, where the initial concentrations of iodine were five times higher than in Table HI . In the system of I 2 and F H S , the total amount of iodine in solution decreases from 4.38 to 1.02 g / m 3 after 0.5 h; the I 2 component decreases from 3.20 to 0.23 g /m 3 . After 3.5 h the total amount of iodine does not change, but the I 2 component is completely reduced to iodide. In the system with both I" and C l 2 , all iodide is initially oxidized to I 2 . After reaction with F H S (0.5 h), most of the iodine left in solution has been reduced to iodide. After 3.5 h all solution iodine is in the form of iodide, but no additional organic-bound iodine was formed. </p><p>The relationship between organic-bound iodine and the added or total system iodine is shown in Figure 3 for both elemental iodine and iodide. Below a total iodine concentration, normalized for the D O C concentration of F H S , of 0.05 g of I per g of D O C , both forms of iodine react completely with the F H S . This reaction represents iodine concentrations as high as </p><p>Table . Reaction of Iodine and Iodide with Fuhrberg Humic Substances </p><p>Time Iodine (l2) Iodide (/) </p><p>Time h I 2 / h / - / 0 650 240 890 ndf l 650 650 10 min nd 370 370 nd 280 280 8 h nd 400 400 nd 270 270 1 day nd 380 380 nd 285 285 4 day nd 400 400 nd 290 290 14 day nd 400 400 nd 290 290 NOTE: All values are concentration in milligrams per cubic meter. Solution conditions: 3.2 g of DOC/m3; pH 6.5. end, not detected. </p><p>Dow</p><p>nloa</p><p>ded </p><p>by U</p><p>CSF</p><p> LIB</p><p> CK</p><p>M R</p><p>SCS </p><p>MG</p><p>MT</p><p> on </p><p>Sept</p><p>embe</p><p>r 4,</p><p> 201</p><p>4 | h</p><p>ttp://</p><p>pubs</p><p>.acs</p><p>.org</p><p> P</p><p>ublic</p><p>atio</p><p>n D</p><p>ate:</p><p> Dec</p><p>embe</p><p>r 15</p><p>, 198</p><p>8 | d</p><p>oi: 1</p><p>0.10</p><p>21/b</p><p>a-19</p><p>88-0</p><p>219.</p><p>ch03</p><p>5</p><p>In Aquatic Humic Substances; Suffet, I., et al.; Advances in Chemistry; American Chemical Society: Washington, DC, 1988. </p></li><li><p>35. SUMMERS ET AL. Radioactive Iodine in the Aquatic Environment 627 </p><p>100 </p><p>S 80 X I </p><p>c </p><p>" </p><p>c D m </p><p>60 </p><p>40 </p><p>20 </p><p>Fuhrberg humic substances (FHS) / pH 6.5 </p><p>C l 2 </p><p>7* JPr~~"^ . -o ^ </p><p>(g /m 3 ) </p><p>l l 2 0.89 </p><p>f C l 2 2.42 </p><p>1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 </p><p>DOC 3.20 </p><p>0 15 5 10 </p><p>Time, t (h) </p><p>Figure 1. Halogen and Fuhrberg humic substances reaction kinetics. </p><p>20 </p><p>E en </p><p>c </p><p>D 3 </p><p>c </p></li><li><p>628 AQUATIC HUMIC SUBSTANCES </p><p>0.4 </p><p>\ cn </p><p>0.3 </p><p>I 0.2 </p><p>CD C. </p><p>"D C 3 </p><p>CD </p><p>0.1 </p><p>Fuhrberg humic substances ( H S ( l </p><p>1 0 0 % </p><p>b o u n d </p><p>FHS C 0 (gDOC/m 3) </p><p>3.20 6.40 </p><p>pH 3.5 6.5 6.5 </p><p>0 0.2 0.4 0.6 C.8 </p><p>Total iodine, l /DOC (g /g ) </p><p>Figure 3. Organic-bound iodine as a function of the total iodine in the system with Fuhrberg humic substances. </p><p>160 m g / m 3 for a F H S concentration of 3.2 g of D O C / m 3 . At higher total iodine concentrations the percent of total iodine bound to the F H S decreases, but in the concentration region below 0.8 g of I per g of D O C , a saturation of the F H S by iodine is not found. Elemental iodine is slightly more reactive than iodide, but the reaction is independent of p H and F H S concentration, as shown in Figure 3. However, Skogerboe and Wilson (9) found that low p H values reduce the extent of reaction between a soil fulvic acid and both I 2 and I 3~. </p><p>F H S was separated by ultrafiltration into high (&gt;1000) and low (</p></li><li><p>35. SUMMERS ET AL. Radioactive Iodine in the Aquatic Environment 629 </p><p>electrophilic substitution, charge-transfer, and biochemical oxidation (10-12). However, the specific mechanism involved with humic substances is not clear because of the complex nature of this heterogeneous macro-molecular material. </p><p>The interaction of methyl iodide and F H S is shown in Table V. Although both sample concentrations, with and without F H S , decrease with time, no significant difference exists between the samples at a given time. This similarity indicates little interaction between C H 3 I and F H S . The decrease in solution concentration for both samples is an indication of the volatility of C H 3 I . It also appears from this data that F H S has no effect on the Henrys coefficient, as the liquid-to-gas volume ratio of both samples was the same. </p><p>Removal by DWT Processes. RHINE RIVER AND 1-131. The radionuclide 1-131 as Na l was added to a sample of the Rhine River water to yield an activity level of 1.17 m B q / m 3 (1170 Bq/L) , which is a factor of 3 larger than any river water value reported in the Federal Republic of Germany after Chernobyl (Table I). The sample was mixed for 0.5 h before chlorine was added at a concentration of 1.0 g of C l / m 3 , which raised the redox potential from 240 to 350 mV. Preoxidation is commonly practiced in D W T </p><p>Table IV. Influence of Fuhrberg Humic Substance Molecular Size on Organic-Bound Iodine </p><p>C Bound Iodine, ClI (%) I (mg/m3) FHS High MSb Low MSC </p><p>I 2 274 88 81 85 890 58 62 58 </p><p>i - 200 90 90 85 650 57 46 52 </p><p>NOTE: Solution conditions: 3.2 g of DOC/m3; pH 6.5. "Initial C concentration. ^Molecular size &gt;1000. 'Molecular size </p></li><li><p>630 AQUATIC HUMIC SUBSTANCES </p><p>plants that directly utilize surface waters to control problems associated with biological growth. </p><p>The results of the flocculation experiments with iron sulfate are shown in Figure 4. The results with no addition of iron sulfate indicate the removal by volatilization and sedimentation. The maximum removal effectiveness by flocculation for 1-131 and D O C is about 30%. Effectiveness nearly doubles for UV254 and triples for turbidity. The addition of PAA at 0.1 g / m 3 with an iron sulfate dosage of 15 g / m 3 did not improve the removal effectiveness for any of the measured parameters. Similar removal values for 1-131 and D O C and higher removal values for turbidity indicate that most of the 1-131 has reacted with dissolved organic matter and not particulate organic matter. This finding is also supported by the filtration results shown in Table VI . Both glass-fiber and 0.45- membrane filters are effective in the removal of turbidity, but significantly less so for 1-131, D O C , and U V ^ . With all </p><p>1 0 0 </p><p> &gt; </p><p>-*-&gt; c </p><p>Rhein River </p><p>Turbidity 0 .90 FTU </p><p>U V 2 5 4 6.52 m " 1 </p><p>1 3 1 l 1.17 M B q / m 3 </p><p>DOC 2.62 g / m 3 </p><p>5 10 15 </p><p>Iron sulfate concentration ( g F e 3 + / m 20 25 </p><p>3+ / _ 3 \ 30 </p><p>Figure 4. Removal effectiveness of iron sulfate flocculation of the Rhine River sample. </p><p>Table VI. Removal by Filtration of the Rhine River Sample </p><p>Parameter Glass Fiber Membrane 1-131 7.6 11 DOC 3.0 4.6 UV-254 8.0 11 Turbidity 69 80 NOTE: All values are percents. </p><p>Dow</p><p>nloa</p><p>ded </p><p>by U</p><p>CSF</p><p> LIB</p><p> CK</p><p>M R</p><p>SCS </p><p>MG</p><p>MT</p><p> on </p><p>Sept</p><p>embe</p><p>r 4,</p><p> 201</p><p>4 | h</p><p>ttp://</p><p>pubs</p><p>.acs</p><p>.org</p><p> P</p><p>ublic</p><p>atio</p><p>n D</p><p>ate:</p><p> Dec</p><p>embe</p><p>r 15</p><p>, 198</p><p>8 | d</p><p>oi: 1</p><p>0.10</p><p>21/b</p><p>a-19</p><p>88-0</p><p>219.</p><p>ch03</p><p>5</p><p>In Aquatic Humic Substances; Suffet, I., et al.; Advances in Chemistry; American Chemical Society: Washington, DC, 1988. </p></li><li><p>35. SUMMERS ET AL. Radioactive Iodine in the Aquatic Environment 631 </p><p>parameters, membrane filtration is slightly more effective. The removal as measured by U V ^ most closely matches that of 1-131, while D O C is slightly less removed. </p><p>Adsorption by activated carbon (AC) in the dosage range of 5-1000 g of A C per m 3 is shown in Figure 5 for the Rhine River sample prior to pretreatment. At nearly all dosages, the adsorption as measured by UV254 and D O C is greater than that of 1-131, although for D O C the difference is normally less than 15%. The maximum removal at 1000 g of A C per m 3 is 70%, 83%, and 97% for 1-131, D O C , and U V ^ , respectively. However, when A C is applied after flocculation, as shown in Figure 6, removal by adsorption is increased. This result can be seen by comparing the removal at a dosage of 100 g of A C per m 3 (Table VII). Prior to flocculation this dosage of activated carbon results in a removal of 57%, 71%, and 87% for 1-131, D O C , and U V 2 5 4 , respectively. After flocculation the respective removals by adsorption increased to 79%, 76%, and 91%. The removal of 1-131 after flocculation is paralleled by that of D O C , for both adsorption and the combined results of flocculation followed by adsorption, as shown in Table VII. </p><p>A...</p></li></ul>

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