Next Article in Journal
Tests of Cryogenic Fabry–Perot Cavity with Mirrors on Different Substrates
Next Article in Special Issue
Ecotoxicological Effect of Single and Combined Exposure of Carbamazepine and Cadmium on Female Danio rerio: A Multibiomarker Study
Previous Article in Journal
Preparation of Polyacrylate Hollow Microspheres via Facile Spray Drying
Previous Article in Special Issue
Monitoring the Activated Sludge Activities Affected by Industrial Toxins via an Early-Warning System Based on the Relative Oxygen Uptake Rate (ROUR) Index
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Applied Sciences
Volume 9
Issue 2
10.3390/app9020229
applsci-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Comparison between OCl−-Injection and In Situ Electrochlorination in the Formation of Chlorate and Perchlorate in Seawater

by
Jongchan Yi
1,
Yongtae Ahn
1,
Moongi Hong
2,
Gi-Hyeon Kim
1,
Nisha Shabnam
1,
Byongsueng Jeon
2,
Byoung-In Sang
2 and
Hyunook Kim
1,*
1
Department of Environmental Engineering, University of Seoul, 163 Seoulsiripdaero, Dongdaemun-gu, Seoul 02504, Korea
2
Department of Chemical Engineering, Hanyang University, 222, Wangsimni-ro, Seongdong-gu, Seoul 04763, Korea
*
Author to whom correspondence should be addressed.
Appl. Sci. 2019, 9(2), 229; https://doi.org/10.3390/app9020229
Submission received: 11 December 2018 / Revised: 31 December 2018 / Accepted: 31 December 2018 / Published: 10 January 2019
(This article belongs to the Special Issue Innovative Water and Wastewater Treatment Technologies for Supporting Global Sustainability)
Browse Figures
Versions Notes

Abstract

:
To prevent biofouling from occurring in the cooling systems of coastal power plants, chlorine is often added to the cooling water. In this study, we have evaluated the fate of the total residual oxidants and the formation of inorganic chlorination byproducts including ClO3− and ClO4− during in situ electrochlorination with seawater. Then, the results were compared with those during direct OCl−-injection to seawater. The in situ electrochlorination method based on Ti/RuO2 electrodes produced much less ClO3−, while a similar level of total residual oxidants could be achieved with a reaction time of 5 min. Moreover, no ClO4− was observed, while the direct OCl−-injection system could still result in the production of ClO4−. The less or no production of ClO3− or ClO4− by the electrochlorination of seawater was mainly attributed to two reasons. First, during the electrolysis, the less amount of OCl− is available for ClO3− formation. Secondly, the formation of ClO3− or ClO4− is affected by the electrode material. In other words, if the electrode material is carefully chosen, the production of harmful reaction byproducts can be prevented or minimized. In short, based on the results from our study, electrochlorination technology proves to be a marine environmentally friendly method for controlling biofouling in the pipes of the cooling system in a coastal power plant.

1. Introduction

Inland thermoelectric power plants withdraw natural surface water, underground water, and reclaimed water for their cooling systems [1]. About 10% of global freshwater withdrawal is used by power plants [2]. Therefore, many power plants are built near coastal areas since they can use seawater as a coolant [3]. However, these plants frequently encounter the problem of biofouling or biofilm formation in their inlet pipes and cooling systems. Biofouling is defined as the attachment of micro-/macroorganisms to the inner surface of pipes and the subsequent growth of the organisms. It is caused by a variety of organisms ranging from microorganisms (bacteria, algae) to macroorganisms (mussels, barnacles, etc.), depending on the conditions such as flow regimes of seawater in pipe, the presence of substrate(s), and so on. Biofouling is a huge concern as it blocks seawater flow, which results in the reduced efficiency of heat exchangers, increased loads on pumps, and eventually the failure of power generation [4]. Among all the methods used to control biofouling, chlorination remains the most popular and preferred, because of its proven effectiveness and relatively low cost [5]. Chlorine not only exerts toxic effects on adult organisms but also inhibits the growth of larvae and their attachment to the substratum [6,7]. There are various methods to make chlorine in water, such as (i) dissolution of chlorine gas; (ii) addition of hypochlorite; and (iii) electrolysis of electrolytes containing salt or seawater (i.e., electrochlorination) [8].
Recently, electrochlorination has been applied for biofouling control. Electrochlorination enables the production of sodium hypochlorite, which is produced through the application of electric potential differences between electrodes with NaCl as an electrolyte [9]. Particularly, under direct current (DC) voltage, negatively charged ions such as chloride, hydroxyl, and oxygen ions donate electrons at the anode to form chlorine gas, oxygen gas, hypochlorite ion, hypochlorous acid, and hydrochloric acid. On the other hand, positively charged ions such as hydrogen, sodium, magnesium, calcium, and potassium ions gain electrons at the cathode to form hydrogen gas and hydroxide (reaction 1–7) [10,11,12,13].
Anode
2 Cl− ↔ Cl2 + 2 e− (Eo = 1.36 V)
Bulk solution
Cl2 + H2O → H+ + Cl− + HOCl
HOCl ↔ OCl− + H+ (pKa = 7.5 at 25 °C)
HOCl + H+ + e− ↔ 1/2 Cl2 + H2O (Eo = 1.63 V)
NaCl + H2O → NaOCl + H2
Cathode
O2 + 2 e− + 2 H+ → H2O2 (Eo = 0.68 V)
2 H2O + 2 e− → 2 OH− + H2
Currently, the ex situ electrolytic production of hypochlorite, which is subsequently injected into pipes, is commonly carried out in practice. Compared with ex situ electrochlorination, in situ electrochlorination in seawater has a few advantages. This does not require supply of NaCl since it uses Na+ and Cl− in seawater as electrolytes. In addition, it does not require any space for hypochlorite generation and storage. Therefore, in situ electrochlorination should be more economical than ex situ.
Generally, the residual chlorine concentration of water flowing through the pipe of a cooling system is maintained at 0.2 mg/L or higher to control biofouling [14,15,16]. In practice, chlorine is added in the inlet of the cooling system and the chlorine concentration at the inlet is varied depending on its level at the outlet [17]. In fact, a large amount of seawater is withdrawn for the cooling system in a power generation system (e.g., 95–230 m3/MWh for the once-through cooling system of a nuclear power plant [15,18]). So, an enormous amount of chlorine should be applied in the inlet.
Chlorine exerts a biocidal action on microorganisms in water by oxidizing enzymes responsible for microbial growth. However, chlorine also reacts with other constituents in water to generate unwanted organic and inorganic chlorination byproducts (CBPs); in seawater, for example, trihalomethane, haloacetic acids, chloramines, bromate, chlorite, chlorate, and perchlorate are produced [17]. Due to their persistency in the environment and potential negative impacts on aquatic lives, ClO3− and ClO4− have been of special public interest. In humans, ClO3− causes hematological imbalance by decreasing erythrocyte count and hemoglobin. ClO4− also interferes with iodine uptake to cause thyroid malfunctions [19]. According to a report from WHO, ClO3− may also cause renal tumors [20].
In this study, we have evaluated the fate of the total residual oxidant (TRO) and formation of inorganic CBPs including ClO3− and ClO4− during in situ electrochlorination with seawater using Ti/RuO2 electrodes. Then, the results were compared with those during direct OCl−-injection to seawater.
The specific goals of this study were to: (1) monitor TRO fate when electrochlorination or direct OCl−-injection was applied for seawater; (2) compare the amounts of ClO3− and ClO4− formed during electrochlorination or direct OCl−-injection. We believe that the findings presented in the manuscript will contribute to our understanding of the potential environmental risk associated with ClO3− and ClO4− formed during in situ electrochlorination of seawater, which is used for the cooling system of a power plant.

2. Materials and Methods

2.1. Materials

Seawater samples were collected from the west coast (Yeonggwang, Korea, 35°23′27″ N, 126°24′25″ E) of the Korean peninsula and the east coast (Uljin, Korea, 37°01′53″ N, 129°24′54″ E) (Figure S1). Once the water samples were collected, they were filtered using GF/C (Whatman, Chalfont, UK) and stored at 4 °C. The water quality of the collected seawater samples is summarized in Table 1.
NaOCl (Duksan Chemical, Daejeon, Korea) stock solution of 120,000 mg/L was used for the direct chlorine injection study. For electrochlorination, an anode and a cathode made of Ti and RuO2, respectively, (0.1 m × 0.18 m, Samsung DSA, Seoul, Korea) were used.

2.2. Experimental Procedure

Chlorination experiments were performed in a 500-mL Pyrex batch reactor, and the temperature of the reactor was set to 20.0 ± 0.5 °C using a temperature-controlled bath (C-331, Sibata, Tokyo, Japan) (Figure 1a,b). The OCl− solution of desirable concentration was prepared by diluting the NaOCl stock solution (12%) with deionized (DI) water. Then, the OCl− solution was directly injected to the reactor in the beginning of each experiment.
Electrolysis experiments were performed in a 2-L lab-scale semi-batch reactor. The two electrodes (i.e., Ti and RuO2) were placed vertically, with a distance of 2.5 cm between each other, in the reactor. A DC power supply (SM Techno, Daejeon, Korea) was used to provide electricity for the electrodes; four different current densities were applied (i.e., 2.2, 9.4, 16.6, and 27.7 mA/cm2 (Figure 1c). Prior to executing electrolysis, electrodes were washed with DI water to desorb any materials remaining on their surface. During the experiment, the solution in the reactor was rapidly mixed by a magnetic stirrer, and aliquots were withdrawn from the reactor at predetermined times to measure TRO, and inorganic byproducts (i.e., ClO3− and ClO4−). To measure byproducts, excessive sodium thiosulfate (Na2S2O3) was added as a quenching agent to prevent further oxidation of the byproducts by the oxidant.

2.3. Analysis Methods

For quantitative analysis of TRO, EPA method 330.5 (Spectrophotometric, DPD) was used using spectrophotometer (Qvis 5000, C-mac, Daejeon, Korea) [21]. The quantification range of chlorine was 0.02–4.00 mg/L. TRO was measured at a predetermined time interval after an oxidation was initiated.
Concentration of ClO3− and ClO4− were measured using ion chromatography (883 Basic IC plus, Metrohm, Herisau, Switzerland). The eluent for ClO3− consisted of 3.6 mM sodium carbonate (Na2CO3) and was delivered at a flow rate of 0.8 mL/min. The eluent for ClO4− consisted of a mixture of 10.0 mM Na2CO3 and 45% acetonitrile was delivered at a flow rate of 0.6 mL/min. The separation column was IC 82524A, 4.0 mm × 250 mm (Shodex, Tokyo, Japan). The pH was measured using a pH meter (Mettler-Toledo, Greifensee, Switzerland). Conductivity was measured using a multifunction meter (CX-401 waterproof, Elmetron, Zabrze, Poland). TOC wes measured using a TOC analyzer (TOC−VCPH/CPN, Shimazu Co., Kyoto, Japan).

3. Results and Discussion

3.1. Total Residual Oxidant in Direct OCl−-Injection and Electrolysis

3.1.1. Direct OCl−-Injection

Effects of the initial OCl− concentration on TRO in the direct injection of OCl− to seawater were investigated. The direct OCl−-injection experiments were carried with WS and ES by varying OCl− concentrations (0.5, 0.7, 1, 10, 50, and 150 mg/L as Cl2) and their results are presented in Figure 2. Irrespective of the initial OCl− concentrations, the TRO concentration dropped rapidly in the beginning and was stabilized within 1 min for both ES and WS (Figure 2a,b). Chlorine demand of both WS and ES increased with the increase of the OCl− dose. While the chlorine demand of WS increased by 26-fold, that of ES increased by only 12-fold, as the OCl− dose increased from 0.5 to 150 mg/L. When the OCl− dose of ≥10 mg/L was applied, WS showed a significantly higher chlorine demand compared to that of ES (Figure 2c). These phenomena might be explained by the characteristics of the seawater used in this study, such as organics or nitrogen contents [22]. In other words, once chlorine is added to seawater, reactions between chlorine and chlorine-demanding substances such as Br−, NH4+, NO2−, Fe2+, and residual organics occur rapidly [14,23,24]. Nonetheless, the chlorine demand became obvious when the dose was high. In the case where 150 mg/L OCl− was injected to WS, the chlorine demand reached 13.0 mg/L (Figure 2c). On the other hand, the chlorine demand reached 0.2 mg/L when 0.5 mg/L OCl− was injected. Similar results have been reported by others, e.g., Zeng et al. [25], Venkatnarayanan et al. [26], and Saidan et al. [27].

3.1.2. Effects of Current Density during Electrolysis

Effects of the current density (2.2, 9.4, 16.6, and 27.7 mA/cm2) on TRO during the in situ electro-chlorination of seawater were investigated. For both WS and ES, the TRO concentration increased as the applied current density and time increased (Figure 3). No significant difference in the TRO concentration was observed between WS and ES, probably because the salinities of WS and ES were almost the same. More than 230 mg/L of TRO could be produced via the in situ electrochlorination of seawater within 5 min under the current density of 27.7 mA/cm2: 240 mg/L for WS and 235 mg/L for ES. In other words, at the current density, TRO of 16.8-18 mg Cl2/cm2/min can be produced. If an electrode with a width of 0.5 m is installed along the inner surface of a pipe with a radius of 1 m, the surface area of the electrode will be 3.1 m2 and produce TRO at 520–557 g Cl2/min. Considering the flow pattern developing along the inner surface of the pipe for a cooling system, the amount of TRO generated by seawater electrolysis will be enough to provide a desirable TRO concentration (e.g., >0.5 mg Cl2/L) for the cooling water flowing the pipe (confirmed by a simulation; data not shown).

3.2. Formation of ClO3− and ClO4− in Electrolysis and Direct OCl−-Injection

The kinds and concentrations of CBPs depend on several factors, such as oxidant contact time, organic and inorganic contents, reaction temperature, and solution pH [17,28,29,30,31,32]. If chlorine is added to seawater via direct OCl−-injection or the electrochemical process, chlorite, chlorate, or perchlorate can be generated through the following reactions (Equations (8)–(20) in Table 2) (Figure 4) [11,13,33,34,35,36].

3.2.1. Direct OCl−-Injection

The formation of ClO3− and ClO4− when OCl− was directly added to seawater was evaluated by varying OCl− concentration (0.5, 0.7, 10, 50, and 150 mg/L). Figure 5 shows the pattern of ClO3− formation during the chlorination of WS and ES as a function of contact time. ClO3− was not detected when the OCl− amount added to the seawater samples was low (i.e., 0.5 mg/L). On the other hand, 816 μg/L and 808 μg/L of ClO3− could be observed for WS and ES, respectively when the amount of OCl− added to the seawater was 150 mg/L. This result could be explained by Equations (8)–(17). ClO3− can be formed via either direct or indirect reactions: via either (1) the reaction between OCl−/HOCl and H2O to form ClO3− or (2) the reaction of added OCl−/HOCl with Cl− in seawater to form OCl−, ClO2−, and then to form ClO3−. Regardless of the amount of OCl− added to the water samples, the ClO3− formation occurred within the reaction time of 1 min. Then, the ClO3− concentration slightly decreased by 8–17% due to Equations (18)–(20).
In the case where ClO3− is present at a high level, ClO4− can be formed through the reaction of ClO3− with H2O (Equation (18)). Figure 6 shows the time profiles of ClO4− formation during the chlorination of WS and ES as a function of contact time. ClO4− was not detected from the samples when the OCl− concentration was ≤ 10 mg/L. No significant difference was observed in the formation of ClO4− between WS and ES. When the seawater samples were added with 50 and 150 mg/L OCl−, however, ClO4− of 0.36 and 3.44 μg/L, respectively could be observed. These results indicated that at a low concentration OCl− might not generate ClO4− in seawater.

3.2.2. Electrochlorination

Electrochlorination was performed for both WS and ES with different current densities i.e., 2.2, 9.4, 16.6, and 27.7 mA/cm2) and the formation of ClO3− and ClO4− was studied. The ClO3− concentration increased from 0.60 to 4.75 μg/L for WS and from 0.17 to 4.59 μg/L for ES, as the current density was raised from 2.2 to 27.7 mA/cm2 (Figure 7). The amount of ClO3− formed in ES increased with the increase of the current density. However, in the case of WS, ClO3− increase was noted only at a current density of >16.6 mA/cm2 (Figure 7). Nonetheless, it seems that the amount of ClO3− formed during the electrochlorination of seawater depends on both the applied current density and the surface characteristics of electrodes used in the electrolysis. Jung et al. [37] observed 637 μg/L ClO3− formed during their electrochlorination of seawater from the east coast using Pt/Ti electrodes with 55 mA/cm2 of current density. Our Ti/RuO2-based electrolysis system might produce less ClO3− than the Pt/Ti-based one.
Interestingly, in our electrochlorination study with WS or ES, ClO4− was not detected even at a current density of 27.7 mA/cm2. In fact, other researchers could observe ClO4− only when higher current densities were applied for their electrochlorination. In their electrochlorination study with seawater samples from the east coast of Korea, Oh et al. [38] could generate 27 μg/L of ClO4− with a current density of 110 mA/cm2; in their experiment, they used Pt/Ti electrodes. From the results of our study and others, it can be concluded that the formation of inorganic CBPs such as ClO3− and ClO4− is very dependent on the surface characteristics of electrodes or electrode-surface-specific reactions. When electrode material has a lower potential for oxygen evolution, the electrode easily produces oxygen, which reacts with bromine and chloride to form BrO3− and ClO3− formation [37].
Nonetheless, the amount of ClO3− produced from the electrochlorination of seawater was about 170 times lower than that from the direct OCl−-injection. This phenomenon could be explained by the difference in the amount of OCl− used for the ClO3− formation between the direct OCl−-injection system and the electrochlorination of seawater. If a large amount of OCl− is added to seawater at once, the bromine ions in seawater will rapidly react with OCl−/HOCl to form OBr−/HOBr (reactions 1–5 in the Supplementary Materials). However, some of the OCl− still might be able to participate in reactions that form ClO3−. In the case of electrochlorination, OCl− is gradually produced on the electrode surface. In this case, OCl− generated on the electrode surface might preferentially react with Br− and form OBr−/HOBr. Comparing to the direct OCl−-injection system, thus, a relatively smaller amount of OCl− will be available for the ClO3− formation during seawater electrolysis.
In short, unlike conventional chlorination, electrochlorination produces much less or no inorganic chlorination byproducts, which makes it an environmentally friendly and sustainable technology.

4. Conclusions

In this study, we have evaluated the in situ electrochlorination of seawater, which is used as a coolant for coastal power plants in terms of TRO production and formation of inorganic chlorination byproducts such as ClO3− and ClO4−. Compared to the practice of directly adding OCl− to cooling seawater, the in situ electrochlorination method based on Ti/RuO2 electrodes produced much less ClO3−, while a similar level of TRO could be achieved with a high TRO production rate of 16.8–18 mg Cl2/cm2/min. Moreover, ClO4− was not observed during electrochlorination, while the direct OCl−-injection system could still result in the production of ClO4−. The lower or no production of ClO3− or ClO4− by the electrochlorination of seawater was mainly attributed to two reasons. First, less OCl− is available for ClO3− formation because the OCl− supply is limited by the electrode surface area and reaction time. Secondly, the formation of ClO3− or ClO4− is affected by the electrode material. In other words, if the electrode material is carefully chosen, the production of harmful reaction byproducts can be prevented or minimized.
Based on the results of our study, in situ electrochlorination technology proves to be a marine environmentally friendly and sustainable method for controlling biofouling in the pipes of a cooling system in a coastal power plant. Therefore, this technology should be preferentially considered as an option for antifouling of the cooling system for a thermoelectric power plant.

Supplementary Materials

The following are available online at https://www.mdpi.com/2076-3417/9/2/229/s1.

Author Contributions

H.K. and B.-I.S. conceived and designed the experiments; G.-H.K., Y.A, B.J. and M.H. performed the experiments; J.Y. and Y.A. analyzed the data; J.Y., Y.A., and N.S. prepared the paper; H.K. edited the paper.

Acknowledgments

This work was supported by the Korea Institute of Energy Technology Evaluation and Planning (KETEP) and the Ministry of Trade, Industry & Energy (MOTIE) of the Republic of Korea (No. 20171520101740).

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Pan, S.Y.; Snyder, S.W.; Packman, A.I.; Lin, Y.J.; Chiang, P.C. Cooling water use in thermoelectric power generation and its associated challenges for addressing water-energy nexus. Water-Energy Nexus 2018, 1, 26–41. [Google Scholar] [CrossRef]
  2. International Energy Agency (IEA). World Energy Outlook; OECD/IEA: Paris, France, 2016; p. 13. [Google Scholar]
  3. Pugh, S.J.; Hewitt, G.F.; Müller-Steinhagen, H. Fouling during the use of seawater as coolant—The development of a ‘User Guide’. In Proceedings of the Engineering Conferences International, Heat Exchanger Fouling and Cleaning: Fundamentals and Applications, Santa Fe, NM, USA, 18–22 May 2003. [Google Scholar]
  4. Satpathy, K.K.; Mohanty, A.K.; Sahu, G.; Biswas, S.; Prasad, M.V.R.; Slvanayagam, M. Biofouling and Its Control in Seawater Cooled Power Plant Cooling Water System—A Review. In Nuclear Power; Tsvetkov, P., Ed.; IntechOpen: London, UK, 2010. [Google Scholar]
  5. Nanny, M.A. Handbook of chlorination and alternative disinfectants. Fourth edition by George Clifford White. John Wiley and Sons, Inc.: New York, Chichester, Weinheim, Brisbane, Singapore, and Toronto. 1999. xxi + 1569 pp. $195.00. ISBN 0-471-29297-9. J. Am. Chem. Soc. 1999, 121, 8678–8679. [Google Scholar] [CrossRef]
  6. Masilamoni, G.; Jesudoss, K.S.; Nandakumar, K.; Satapathy, K.K.; Azariah, J.; Nair, K.V.K. Lethal and sub-lethal effects of chlorination on green mussel Perna viridis in the context of biofouling control in a power plant cooling water system. Mar. Environ. Res. 2002, 53, 65–76. [Google Scholar] [CrossRef]
  7. Russell, L.B. Modelling for cost-effectiveness analysis. Stat. Med. 1999, 18, 3235–3244. [Google Scholar] [CrossRef]
  8. White, G.C. Handbook of Chlorination and Alternative Disinfectants; John Wiley and Sons, Inc.: New York, NY, USA, 2009. [Google Scholar]
  9. Asokan, K.; Subramanian, K. Design of a tank electrolyser for in-situ generation of NaClO. In Proceedings of the World Congress on Engineering and Computer Science 2009, San Francisco, CA, USA, 20–22 October 2009. [Google Scholar]
  10. Berl, E. A new cathodic process for the production of H2O2. J. Electrochem. Soc. 1939, 76, 359–369. [Google Scholar] [CrossRef]
  11. Viswanathan, K.; Tilak, B.V. Chemical, electrochemical, and technological aspects of sodium chlorate manufacture. J. Electrochem. Soc. 1984, 131, 1551–1559. [Google Scholar] [CrossRef]
  12. Munichandraiah, N.; Sathyanarayana, S. Kinetics and mechanism of anodic oxidation of chlorate ion to perchlorate ion on lead dioxide electrodes. J. Appl. Electrochem. 1987, 17, 33–48. [Google Scholar] [CrossRef]
  13. Tasaka, A.; Tojo, T. Anodic oxidation mechanism of hypochlorite ion on platinum electrode in alkaline solution. J. Electrochem. Soc. 1985, 132, 1855–1859. [Google Scholar] [CrossRef]
  14. Allonier, A.-S.; Khalanski, M.; Camel, V.; Bermond, A. Characterization of chlorination by-products in cooling effluents of coastal nuclear power stations. Mar. Pollut. Bull. 1999, 31, 1232–1241. [Google Scholar] [CrossRef]
  15. Poornima, E.H.; Rajadurai, M.; Rao, T.S.; Anupkumar, B.; Rajamohan, R.; Narasimhan, S.V.; Rao, V.N.R.; Venugopalan, V.P. Impact of thermal discharge from a tropical coastal power plant on phytoplankton. J. Therm. Biol. 2005, 30, 307–316. [Google Scholar] [CrossRef]
  16. Nebot, E.; Casanueva, J.F.; Casanueva, T.; Fernández-Bastón, M.M.; Sales, D. In situ experimental study for the optimization of chlorine dosage in seawater cooling systems. Appl. Therm. Eng. 2006, 26, 1893–1900. [Google Scholar] [CrossRef]
  17. Kim, D.; Amy, G.L.; Karanfil, T. Disinfection by-product formation during seawater desalination: A review. Water Res. 2015, 81, 343–355. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  18. Kohil, A.; Frenken, K. Cooling Water for Energy Generation and Its Impact on National-Level Water Statistics; Food and Agriculture Organization of the United Nations: Rome, Italy, 2011. [Google Scholar]
  19. Goleman, W.L.; Carr, J.A.; Anderson, T.A. Environmentally relevant concentrations of ammonium perchlorate inhibit thyroid function and alter sex ratios in developing Xenopus laevis. Environ. Toxicol. Chem. 2002, 21, 590–597. [Google Scholar] [CrossRef] [PubMed]
  20. World Health Organization (WHO). Chlorite and Chlorate in Drinking-Water; WHO: Geneva, Switzerland, 2005. [Google Scholar]
  21. United States Environmental Protection Agency (EPA). Chlorine, Total Residual (Spectrophotometric, DPD); EPA-NERL: 330.5; EPA: Cincinnati, OH, USA, 1978.
  22. Beggs, K.M.H.; Summers, R.S. Character and chlorine reactivity of dissolved organic matter from a mountain pine beetle impacted watershed. Environ. Sci. Technol. 2011, 45, 5717–5724. [Google Scholar] [CrossRef] [PubMed]
  23. Boccelli, D.L.; Tryby, M.E.; Uber, J.G.; Summers, R.S. A reactive species model for chlorine decay and THM formation under rechlorination conditions. Water Res. 2003, 37, 2654–2666. [Google Scholar] [CrossRef]
  24. Abarnou, A.; Miossec, L. Chlorinated waters discharged to the marine environment chemistry and environmental impact. An overview. Sci. Total Environ. 1992, 126, 173–197. [Google Scholar] [CrossRef]
  25. Zeng, J.; Jiang, Z.; Chen, Q.; Zheng, P.; Huang, Y. The decay kinetic of residual chlorine in cooling seawater simulation experiments. Acta Oceanol. Sin. 2009, 28, 54–59. [Google Scholar]
  26. Venkatnarayanan, S.; Murthy, P.S.; Kirubagaran, R.; Venugopalan, V.P. Effect of chlorination on barnacle larval stages: Implications for biofouling control and environmental impact. Int. Biodeterior. Biodegrad. 2016, 109, 141–149. [Google Scholar] [CrossRef]
  27. Saidan, M.; Rawajfeh, K.; Nasrallah, S.; Meric, S.; Mashal, A. Evaluation of factors affecting bulk chlorine decay kinetics for Zai water supply system in Jordan: Case Study. Environ. Prot. Eng. 2017, 43, 223–231. [Google Scholar]
  28. Abdel-Wahab, A.; Khodary, A.; Bensalah, N. Formation of trihalomethanes during seawater chlorination. J. Environ. Prot. 2010, 1, 456–465. [Google Scholar] [CrossRef]
  29. Yu, H.-W.; Oh, S.-G.; Kim, I.S.; Pepper, I.; Snyder, S.; Jang, A. Formation and speciation of haloacetic acids in seawater desalination using chlorine dioxide as disinfectant. J. Ind. Eng. Chem. 2015, 26, 193–201. [Google Scholar] [CrossRef]
  30. Brookman, R.M.; Lamsal, R.; Gagnon, G.A. Comparing the formation of bromate and bromoform due to ozonation and UV-TiO2 oxidation in seawater. J. Adv. Oxid. Technol. 2011, 14, 23–30. [Google Scholar] [CrossRef]
  31. Agus, E.; Sedlak, D.L. Formation and fate of chlorination by-products in reverse osmosis desalination systems. Water Res. 2010, 44, 1616–1626. [Google Scholar] [CrossRef] [PubMed]
  32. Yang, X.; Guo, W.; Lee, W. Formation of disinfection byproducts upon chlorine dioxide preoxidation followed by chlorination or chloramination of natural organic matter. Chemosphere 2013, 91, 1477–1485. [Google Scholar] [CrossRef] [PubMed]
  33. Milazzo, G.; Caroli, S.; Braun, R.D. Tables of standard electrode potentials. J. Electrochem. Soc. 1978, 125, 261C. [Google Scholar] [CrossRef]
  34. Czarnetzki, L.R.; Janssen, L.J.J. Formation of hypochlorite, chlorate and oxygen during NaCl electrolysis from alkaline solutions at an RuO2/TiO2 anode. J. Appl. Electrochem. 1992, 22, 315–324. [Google Scholar] [CrossRef]
  35. Jung, Y.J.; Baek, K.W.; Oh, B.S.; Kang, J.-W. An investigation of the formation of chlorate and perchlorate during electrolysis using Pt/Ti electrodes: The effects of pH and reactive oxygen species and the results of kinetic studies. Water Res. 2010, 44, 5345–5355. [Google Scholar] [CrossRef] [PubMed]
  36. Sant’Anna, R.T.P.; Santos, C.M.P.; Silva, G.P.; Ferreira, R.J.R.; Oliveira, A.P.; Côrtes, C.E.S.; Faria, R.B. Kinetics and mechanism of chlorate-chloride reaction. J. Braz. Chem. Soc. 2012, 23, 1543–1550. [Google Scholar] [CrossRef] [Green Version]
  37. Jung, Y.; Hong, E.; Yoon, Y.; Kwon, M.; Kang, J.-W. Formation of bromate and chlorate during ozonation and electrolysis in seawater for ballast water treatment. Ozone Sci. Eng. 2014, 36, 515–525. [Google Scholar] [CrossRef]
  38. Oh, B.S.; Oh, S.G.; Hwang, Y.Y.; Yu, H.W.; Kang, J.-W.; Kim, I.S. Formation of hazardous inorganic by-products during electrolysis of seawater as a disinfection process for desalination. Sci. Total Environ. 2010, 408, 5958–5965. [Google Scholar] [CrossRef]
Applsci 09 00229 g001 550
Figure 1. Schematic diagram for (a) measurement of inorganic CBPs and (b) of residual TRO measure, and (c) electrolysis experimental setup.
Figure 1. Schematic diagram for (a) measurement of inorganic CBPs and (b) of residual TRO measure, and (c) electrolysis experimental setup.
Applsci 09 00229 g001
Applsci 09 00229 g002 550
Figure 2. Effect of initial OCl− concentration on formation of TRO in (a) WS and (b) ES, and (c) comparison of chlorine demands between WS and ES (volume: 0.4 L; temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES).
Figure 2. Effect of initial OCl− concentration on formation of TRO in (a) WS and (b) ES, and (c) comparison of chlorine demands between WS and ES (volume: 0.4 L; temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES).
Applsci 09 00229 g002
Applsci 09 00229 g003 550
Figure 3. Effect of current density on formation of TRO (a) WS, (b) ES (volume: 2 L; temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES; electrode area: 0.018 m2).
Figure 3. Effect of current density on formation of TRO (a) WS, (b) ES (volume: 2 L; temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES; electrode area: 0.018 m2).
Applsci 09 00229 g003
Applsci 09 00229 g004 550
Figure 4. Proposed pathways of ClO3− and ClO4− formation during seawater chlorination.
Figure 4. Proposed pathways of ClO3− and ClO4− formation during seawater chlorination.
Applsci 09 00229 g004
Applsci 09 00229 g005 550
Figure 5. Effect of OCl− dose on ClO3− formation during chlorination of (a) WS and (b) ES (volume: 0.4 L; temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES).
Figure 5. Effect of OCl− dose on ClO3− formation during chlorination of (a) WS and (b) ES (volume: 0.4 L; temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES).
Applsci 09 00229 g005
Applsci 09 00229 g006 550
Figure 6. Effect of OCl− concentration on formation of ClO4− (a) WS, (b) ES (volume: 0.4 L; temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES).
Figure 6. Effect of OCl− concentration on formation of ClO4− (a) WS, (b) ES (volume: 0.4 L; temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES).
Applsci 09 00229 g006
Applsci 09 00229 g007 550
Figure 7. Effect of current density on ClO3− formation during electrochlorination of (a) WS and (b) ES (volume: 2 L, temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES).
Figure 7. Effect of current density on ClO3− formation during electrochlorination of (a) WS and (b) ES (volume: 2 L, temperature: 20 ± 1 °C; salinity: 28.9 PSU for WS and 28.7 PSU for ES; pH: 8.3 for WS and 8.0 for ES).
Applsci 09 00229 g007
Table
Table 1. Sampled seawater quality on west and east coast.
Table 1. Sampled seawater quality on west and east coast.
ParameterWest Seawater (WS)East Seawater (ES)
pH8.38.0
Conductivity(ms/cm)44.3744.67
Salinity (PSU)28.6628.88
TOC (mg/L)2.21.9
TN (mg/L)1.30.5
TP (mg/L)0.10.1
Table
Table 2. Formation of ClO3− and ClO4− during chlorination.
Table 2. Formation of ClO3− and ClO4− during chlorination.
EquationEquivalentEquations No.
 6 OCl− + 3 H2O → 2 ClO3− + 4 Cl− + 6 H+ + 3/2 O2 + 6 e−0.46 V (8) 
 6 HOCl + 3 H2O → 2 ClO3− + 4 Cl− + 12 H+ + 3/2 O2 + 6 e−0.46 V (9) 
 Cl− + 3 H2O → ClO3− + 6 H+ + 6 e−−1.45 V (10) 
 Cl− + 2 OH− → OCl− + H2O + 2 e−−0.94 V (11) 
 Cl− + 4 OH− → ClO2− + H2O + 4 e−−0.76 V (12) 
 OCl− + 2 OH− → ClO2− + H2O + 2 e−−0.59 V (13) 
 ClO2− + 2 OH− → ClO3− + H2O + 2 e−−0.35 V (14) 
 ClO2− + OCl− → Cl− + ClO3−  (15) 
 ClO2− + HOCl → ClO3− + H+ + Cl−  (16) 
 HClO2 + H2O → ClO3− + 3 H+ +2 e−  (17) 
 ClO3− + H2O → ClO4− + 2 H+ + 2e−0.95 V (18) 
 2 ClO3− + 2 Cl− + 4 H+ → Cl2 + 2 ClO2 + 2 H2O  (19) 
 ClO3− + Cl− + 2 H+ → HClO2 + HOCl  (20) 

Share and Cite

MDPI and ACS Style

Yi, J.; Ahn, Y.; Hong, M.; Kim, G.-H.; Shabnam, N.; Jeon, B.; Sang, B.-I.; Kim, H. Comparison between OCl−-Injection and In Situ Electrochlorination in the Formation of Chlorate and Perchlorate in Seawater. Appl. Sci. 2019, 9, 229. https://doi.org/10.3390/app9020229

AMA Style

Yi J, Ahn Y, Hong M, Kim G-H, Shabnam N, Jeon B, Sang B-I, Kim H. Comparison between OCl−-Injection and In Situ Electrochlorination in the Formation of Chlorate and Perchlorate in Seawater. Applied Sciences. 2019; 9(2):229. https://doi.org/10.3390/app9020229

Chicago/Turabian Style

Yi, Jongchan, Yongtae Ahn, Moongi Hong, Gi-Hyeon Kim, Nisha Shabnam, Byongsueng Jeon, Byoung-In Sang, and Hyunook Kim. 2019. "Comparison between OCl−-Injection and In Situ Electrochlorination in the Formation of Chlorate and Perchlorate in Seawater" Applied Sciences 9, no. 2: 229. https://doi.org/10.3390/app9020229

APA Style

Yi, J., Ahn, Y., Hong, M., Kim, G. -H., Shabnam, N., Jeon, B., Sang, B. -I., & Kim, H. (2019). Comparison between OCl−-Injection and In Situ Electrochlorination in the Formation of Chlorate and Perchlorate in Seawater. Applied Sciences, 9(2), 229. https://doi.org/10.3390/app9020229

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop