Applied Water Science

, Volume 7, Issue 3, pp 1231–1237 | Cite as

Treatment of high salt oxidized modified starch waste water using micro-electrolysis, two-phase anaerobic aerobic and electrolysis for reuse

  • Xuenong Yi
  • Yulin WangEmail author
Open Access
Original Article


A combined process of micro-electrolysis, two-phase anaerobic, aerobic and electrolysis was investigated for the treatment of oxidized modified starch wastewater (OMSW). Optimum ranges for important operating variables were experimentally determined and the treated water was tested for reuse in the production process of corn starch. The optimum hydraulic retention time (HRT) of micro-electrolysis, methanation reactor, aerobic process and electrolysis process were 5, 24, 12 and 3 h, respectively. The addition of iron-carbon fillers to the acidification reactor was 200 mg/L while the best current density of electrolysis was 300 A/m2. The biodegradability was improved from 0.12 to 0.34 by micro-electrolysis. The whole treatment was found to be effective with removal of 96 % of the chemical oxygen demand (COD), 0.71 L/day of methane energy recovery. In addition, active chlorine production (15,720 mg/L) was obtained by electrolysis. The advantage of this hybrid process is that, through appropriate control of reaction conditions, effect from high concentration of salt on the treatment was avoided. Moreover, the process also produced the material needed in the production of oxidized starch while remaining emission-free and solved the problem of high process cost.


High salt Oxidized starch wastewater Combined process Reuse Emission-free 


Industrial demand for modified starch triggers the rise in number and expanding in scale of starch factories. The modified starch processes generate wastewater containing organic and inorganic matters that affect wastewater treatment, especially in chemical modification such as oxidation. A large amount of NaCl was produced during the oxidized modified starch production processes in the wastewater (Chavalparit and Limpaseni 1995). This is because of the addition of chemical substances to the process and the adjustment of pH with HCl. The presence of high salt concentration has been traditionally considered as inhibitory for biological wastewater treatment (Fusuwankaya et al. 2009; Kokabian et al. 2013) and caused paralysis of the original wastewater treatment system.

In recent days, studies on treatment of starch wastewater treatments mainly include flocculation and sedimentation, anaerobic biological treatment and aerobic biological process (Abeling and Seyfried 1993; Deng et al. 2003; Rajasimman and Karthikeyan 2007; Li et al. 2011). But there have been few cases on modified starch wastewater treatment, and those under investigation have considered neither the removal nor the reuse of salt generated. In one approach, an anaerobic hybrid reactor was used to treat the wastewater and its feasibility under high salt condition was proved but with no further discussion on salt removing (Fusuwankaya et al. 2009). In another approach, combined process of sedimentation, microfiltration and reverse osmosis was developed, but it only discussed the impact of high salt, and the cost was high, and utilization of resources was limited (Cancino-Madariaga and Aguirre 2001).

Considering the poor biodegradability, high salt concentration and complexity of oxidized modified starch wastewater, a combination process of micro electrolysis, two-phase anaerobic, aerobic and electrolysis was designed and a micro-electrolysis anaerobic two-phase reactor was developed. Effective control of the reaction conditions was necessary to avoid the inhibition of high salt to the processes. Hazardous materials and pollutants with poor biodegradability can be eliminated by the preset micro electrolysis (Huang et al. 2013) and the ratio of BOD/COD can be greatly improved so that microorganism activity is not restrained by hazardous materials in the wastewater (Li et al. 2010; Tao and Kang 2014). Other organic pollutants, ammonia nitrogen, and biodegradable pollutants can be removed by anaerobic and aerobic biological treatment (Abou-Elela et al. 2010; Shi et al. 2014). The remaining organics can be removed by electrolysis (Kim et al. 2013), and then active chlorine produced in the process can be reused in oxidized starch production process (Lin et al. 1998; Zaviska et al. 2012), as well as the treated water. This combination saves production process costs and maximizes resource utilization.

Materials and methods

The source and quality of wastewater

Table 1 is the original composition of oxidized starch wastewater obtained from a corn starch factory.
Table 1

Characteristics of OMSW process



COD (mg/L)


BOD (mg/L)


\( {\text{NH}}^{ + }_{4}-{\text{N}} \) (mg/L)


Salinity–NaCl (%)




Figure 1 shows the flow chart of the combined process.
Fig. 1

Technological flow chart of the combination process


A cylindrical-shaped reactor operated in a fed-batch mode as the micro-electrolysis anaerobic two-phase reactor is shown in Fig. 2. It had a working volume of 1.5 L and was divided into two laps. The volume ratio of inner to outer lap was 1:2. The inner lap was further divided into two along diameter. The left serves as a micro electrolysis reactor where iron-carbon fillers were placed, and the right is an acidification reactor with five compartments, where iron-carbon fillers, as the biocarriers to enrich the biofacies, were also placed. The outer lap, as a methane reactor, has 12 compartments. Inside both the methane reactor and the acidification reactor were installed an inclined tube. The iron-carbon fillers had a surface area of 120 m2/g, a porosity of 65 %, Fe content of 75 %, C content of 20 % and the catalytic element of 5 %. Halophilic bacteria including acid-forming bacteria and methanogen were needed to be acclimated for anaerobic.
Fig. 2

Micro-electrolysis-anaerobic two-phase reactor. 1 inlet; 2 iron-carbon fillers; 3 acidification reactor; 4 methane reactor; 5 inclined tube; 6 outlet; 7 methane outlet; 8 sample connection for micro electrolysis effluent

Micro electrolysis, two-phase anaerobic and aerobic procedures

Bacteria extracted in starch wastewater outfall was used for the biochemical procedure after halotolerancy improvement in the wastewater with gradually increasing salt concentration. The fluid was removed from the reactor in the middle and into the micro electrolysis reactor from the bottom. The volume ratio of solution to fillers was 1:1. Because of the high salinity, the raw wastewater worked as an electrolyte and promoted micro electrolysis (Tao and Kang 2014). After a certain time of mixing and reaction, the pH value was regulated to 8 with NaOH. After sedimentation, the hydroxide precipitation was separated from the reaction system, and the supernatant overflowed into the up-flow and down-flow of the first interlayer in acidification reactor alternately at a HRT of 1–6 h. The methane reactor was between the two interlayers. And the second interlayer had a similar running mode with the first one at a HRT of 12–48 h. The inclined tube was in the up-flow area.

Electrolytic experiments

To avoid deposition on the electrode during the electrolysis, poly aluminium chloride (PAC) was added into the aerobically treated water for the purpose of removing microorganisms and suspended solids. The electrolysis experiments used titanium electrode coated with RuO2 (Ti-RuO2) as anode and cathode with an effective surface area of 24 cm2 and the interval between electrode plates was 2 cm. The test was conducted under room temperature in an installation which had a total working volume of 300 mL. H2 f process was directly discharged and Cl2 was transferred into the electrolytes by air tube in favor of sodium hypochlorite generation.

Analytical methods

After the steady-state conditions were reached, the physic-chemical analysis investigated covers the following parameters. COD was determined using the potassium dichromate method based on the Standard of the People’s Republic of China for Environmental Protection (Zhang et al. 2006). Five-day biological oxygen demand (BOD5) was measured by the respirometric method (WTW Oxitop®IS6, Germany). The methane production and pH values were daily determined. The biogas production was first passed through a bottle filled with 3 % NaOH solution to adsorb the CO2, H2S and other trace amounts gas, and then the methane production was measured volumetrically using a wet gas flow meter (Sun et al. 2012). During the electrolysis process, the current density and temperature were monitored in real time. Chloride of the effluent was measured using argentometric method (APHA and AWWA 1998) and active chlorine was measured by iodometry (Lide 2012).

Results and discussion

Optimum HRT of micro electrolysis

The pH did not need to be adjusted, because the wastewater feed pH was 3.9 which was conducive to the micro electrolysis (Li et al. 2010). When those fillers were in contact with wastewater, numerous microscopic galvanic cells formed between the iron and carbon (Qin et al. 2012). The reactions can be represented as:

Iron anode (oxidation):
$$ {\text{Fe }} \to {\text{Fe}}^{2 + } + 2{\text{e}} $$
$$ {\text{Fe}}^{2 + } \to {\text{Fe}}^{3 + } + {\text{e}} $$
Carbon cathode (reduction) in the presence of oxygen:
$$ 2{\text{H}}^{ + } + 2{\text{e }} \to 2 \left[ {\text{H}} \right] \to {\text{H}}_{2 } $$
$$ {\text{O}}_{2} + 2{\text{H}}_{2} {\text{O}} + 4{\text{e }} \to 2 {\text{OH}}^{ - } $$
Fe2+ and [H] generated during micro-electrolysis have high chemical activity (Lai et al. 2012) and are believed to break down the carbon chains of organic contaminants. As shown in Fig. 3, the reaction times were 1, 2, 3, 4, 5 and 6 h, removing COD of 13.2, 24.7, 33.4, 42.7, 46.4 and 49.1 %, respectively. From the 4th hour, COD removal showed down as the increase in pH value retards the reaction rate of micro electrolysis. As HRT is too long, since the biopolymers in the reactor contained large amount of anion groups such as OH, CO3 2− and other negatives groups, the iron ions could easily precipitate in term of Fe(OH)X. They can cover the surface of iron-carbon fillers, and inhibit the process of micro electrolysis. To ensure good results on COD removing under neutral environment during the subsequent biological treatment and minimize the loss of fillers, the optimal reaction time was determined as 5 h.
Fig. 3

Changes of pH and removal efficiency of COD by micro-electrolysis

Improvement of wastewater biodegradability by micro electrolysis

The ratio of BOD/COD was measured as a representation of biodegradability. The detection values of micro-electrolysis effluent were shown in Fig. 4. The water samples of inner reactor were replaced every 5 h for batch tests. The value of COD for seven batch tests dropped from 8050 mg/L to 4428.6, 4506.3, 4410.2, 4379.8, 4398.4, 4296.5 and 4403.8 mg/L, respectively. The BOD/COD ratio of wastewater changed from 0.12 to 0.34, indicating that those poorly biodegradable pollutants became easily biodegradable and toxic substances became less toxic after micro electrolysis treatment. This also provided a foundation for the follow-up bioprocess.
Fig. 4

The ratio of BOD/COD of micro-electrolysis effluent for seven batch tests

Influence of dosage of iron-carbon fillers in the acidification reactor

COD changes of the anaerobic effluent under different dosage at 0, 100, 200 and 300 mg/L were shown in Fig. 5. The COD removal efficiency were 28.2, 34.9, 43.5 and 42 %. When dosage of iron-carbon fillers was 100 mg/L, compared with no added fillers, the removal efficiency increased by about 1/4, indicating that the presence of iron-carbon fillers strengthens the anaerobic treatment. Iron could improve the degradability of anaerobic sludge, because iron could lower the solution oxidation–reduction potential beneficial to anaerobic organism and could be oxidized to Fe2+ and Fe3+ which were the necessary elements for anaerobic microorganism (Zhang et al. 2007), and some anaerobic organism could also accelerated the corrosion of iron (Duan et al. 2008). That was a possible reason for the improved COD removal at 100 mg/L dosage. And when the dosage was 200 mg/L, the removal efficiency of COD reached the highest value.
Fig. 5

COD removal efficiency of the anaerobic effluent at various dosage of iron-carbon fillers

Optimization of HRT in the methane reactor

In this study, a reactor was used as the micro-electrolysis-anaerobic two-phase reactor with the inner lap designed as micro electrolysis and acidification reactor and the outer as a two-phase anaerobic reactor. Two parts of acidogenic phase and methanogenic phase separated in the reactor, which could ensure the acid-forming bacteria and methanogenic bacteria functioning in their corresponding circumstances. The sludge sedimentation in the inclined tube did not only effectively reduce the loss of sludge, but also formed a layer of suspended sludge at the base so that sludge concentration improved. The water operated continually. The HRT at acidification reactor was similar with the micro-electrolysis reactor. At the optimal conditions of previous process, the effect of HRT (HRT in the methane reactor) on the removal efficiencies of COD was investigated. As shown in the Fig. 6, the COD removal efficiency were 40, 60.1, 60.2, 60.5 % respectively, at the HRT of 12, 24, 36 and 48 h, accordingly. Organic pollutants cannot be adequately degraded at a short HRT, but too long HRT caused self-degradation of microorganisms. It’s clear that HRT at 24 h is recommended for the reactor.
Fig. 6

COD removal efficiency at different HRT of the methane reactor

The methane gas yield during anaerobic process

To investigate the effect of Fe2+ and Fe3+ on the anaerobic performance, a micro-electrolysis anaerobic two-phase reactor (R1) and its control reactor (R2) were operated in parallel. There were no iron fillers in R2. Collection of methane gas from the micro-electrolysis anaerobic two-phase reactor started when the reactor had started up for 10 days. As shown in the Fig. 7, at a influent COD concentration of 1500 mg/L from 1st day to 7th day, the methane production in the two reactors were 0.71 ± 0.19 L/d (R1) and 0.32 ± 0.11 L/d (R2). According to the calculation based on the theoretical methane production of 0.35 mL/mg COD removed at standard state (Toprak 1995), the methane production efficiency (methane COD/removed COD) were 79.8 and 36.0 % in the R1 and R2. This result indicated that the addition of Fex+ in R1 increased methane production by two times compared with R2, which was in agreement with the report of Coates et al. (2005) who demonstrated that stimulated microbial Fe3+ reduction can enhance methane production. For the idea of zero emissions and the maximization of utility in resource, the methane gas can be collected for recycling and generating economic effects.
Fig. 7

Methane gas yield in the two reactors (R1, R2)

Optimization of HRT in the aerobic reactor

Anaerobic affluently moved into the aerobic reactor, the COD variation of aerobic effluent is shown in Fig. 8. The effluent COD removal significantly reduced in the aerobic process within 12 h and reached to 40.9 % at 12 h. After 12 h, the decreasing trend of COD was not obvious. So the optimal HRT of 12 h was determined.
Fig. 8

Removal efficiency of COD at different HRT of the aerobic reactor

Influence of current density during electrolysis

The reaction was running under the current density of 200, 300 and 400 A/m2 for the aerobic treated effluent. The explanation of why the initial pH of feed less than 7 was that PAC was added into the effluent of aerobic to remove microorganisms.

After the electrolysis process performed for 3 h, the COD removal efficiency significantly were 36, 73 and 78 %, as shown in Fig. 9. It was probably because Cl ions in the water turned into active chlorine in the electric field, resulting in direct degradation of organic pollutants. The removal rate proved that with the increase of current density, electrolysis process effect was improved naturally. During the test, the water samples would be heated as the reaction progress and the temperature rose quickly at current density of 400 A/m2. To make efficient use of energy, the optimum current density was designed as 300 A/m2, and all subsequent trials selected this density.
Fig. 9

Removal efficiency of COD at different current density

Salt content in wastewater was high so that sodium hypochlorite and [O], which had strong oxidizing with organic matters (Zhou et al. 2014), were produced by electrolysis of salt. Then the organic matters were degraded by electrolysis process. The mechanism displays as follows.

Electrode reaction:
$$ 2{\text{Cl}}^{ - } \to {\text{Cl}}_{2} + 2{\text{e}} $$
$$ 2{\text{H}}^{ + } + 2{\text{e}} \to {\text{H}}_{2} $$
$$ 2{\text{NaOH}} + {\text{Cl}}_{2} \to {\text{NaCl}} + {\text{NaClO}} + {\text{H}}_{2} $$
$$ {\text{ClO}}^{ - } \to {\text{Cl}}^{ - } + [{\text{O}}] $$
$$ {\text{ClO}}^{ - } + 2{\text{H}}^{ + } + 2{\text{e}} \to {\text{Cl}}^{ - } + {\text{H}}_{2} {\text{O}} $$
The concentration of chlorine ions and available chlorine were shown in Fig. 10. In fact, during electrolysis, pH value of the electrolyzed-solution increases due to the production of hydroxide ions at the cathode electrode. The concentration of chloride ion decreased from 22,855.5 to 4787.6 mg/L and active chlorine rose to 15,719 mg/L. Theoretical yield based on the reaction formula of active chlorine showed that, the remaining available chlorine concentration accounted for 60 % of the theoretical yield. Considering the incomplete conversion factors and 30–40 % active chlorine in the electrolysis process involved in the degradation of organic matters, both production of sodium hypochlorite and degradation of organic matters reacted in the electrolytic process. Residual chlorine in water samples could be collected after treatment and reused.
Fig. 10

The concentration of chlorine ions and available chlorine

Reuse of treated water

This study treated oxidized modified starch wastewater with high salt by micro electrolysis, two-phase anaerobic, aerobic and electrolysis. The treated effluent quality was shown in Table 2.
Table 2

Effluent quality



COD (mg/L)


Cl (mg/L)


Active chlorine (mg/L)




The treated water by this treatment was used in the production process of corn starch. The quality tests for the production were shown in Table 3.
Table 3

The quality testing of oxidized starch




Starch content









Ash content


















Because of the lack of sodium hypochlorite in the treated water, the productive process needs appropriate amount to add. But the added amount was far less than the amount in the previous production. As apparently seen from Table 3, it successfully applied the treated water to the production, and the oxidized starch product quality testing standards can be achieved.


Water quality was greatly improved and effectively reused in the production process of modified starch after the compound process of micro-electrolysis, two-phase anaerobic, aerobic and electrolysis. Thus, we can conclude that the combined process was an effective method to improve water quality of oxidized modified starch wastewater with high salt concentration. The removal rate of COD was 97.3 % in the whole process.

Micro electrolysis is a feasible method for the treatment and remediation of wastewater with high salt. After pretreatment, the removal efficiency of COD reached 46 %, and the ratio of BOD/COD in the effluent increased from 0.12 to 0.34, which provided a good foundation for the follow-up bioprocess. The arrangement of iron-carbon fillers reinforced the effect of anaerobic treatment at a best dosage of 200 mg/L.

The optimum hydraulic retention time of micro-electrolysis and acidification reactor, methane reactor and aerobic process were 5, 24 and 12 h, respectively. The most effective current density of electrolysis was 300 A/m2 with reaction time of 3 h. The removal rates of COD in anaerobic process, aerobic treatment and electrolysis process were 45, 62, 40, 70 %, respectively.

The additional Fex+ enhance methane production and 0.71 L/day methane gas was collected from anaerobic biological process. Moreover, 15,800 mg/L active chlorine was produced by electrolytic process. These resources can be recycled to produce economic benefits.


  1. Abeling U, Seyfried CF (1993) Anaerobic-aerobic treatment of potato-starch wastewater. Water Sci Technol 28(2):165–176Google Scholar
  2. Abou-Elela SI, Kamel MM, Fawzy ME (2010) Biological treatment of saline wastewater using a salt-tolerant microorganism. Desalination 250(1):1–5CrossRefGoogle Scholar
  3. APHA, AWWA (1998) Standard methods for the examination of water and waste water, 20th edn. WPCF, New YorkGoogle Scholar
  4. Cancino-Madariaga B, Aguirre J (2001) Combination treatment of corn starch wastewater by sedimentation, microfiltration and reverse osmosis. Desalination 279(1):285–290Google Scholar
  5. Chavalparit O, Limpaseni W (1995) Pollutant load from modified starch factories in Thailand. The Engineering Institute of Thailand Under HM The King’s Patronage (EIT), Annual Conference 77–89Google Scholar
  6. Coates JD, Cole KA, Michaelidou U et al (2005) Biological control of hog waste odor through stimulated microbial Fe(III) reduction. Appl Environ Microbiol 71(8):4728–4735CrossRefGoogle Scholar
  7. Deng S, Bai R, Hu X et al (2003) Characteristics of a bioflocculant produced by Bacillus mucilaginosus and its use in starch wastewater treatment. Appl Microbiol Biotechnol 60(5):588–593CrossRefGoogle Scholar
  8. Duan J, Wu S, Zhang X et al (2008) Corrosion of carbon steel influenced by anaerobic biofilm in natural seawater. Electrochem Acta 54(1):22–28CrossRefGoogle Scholar
  9. Fusuwankaya K, Chaiprasert P, Suraraksa B (2009) Treatment of modified starch wastewater with high sodium chloride (NaCl) concentration using an anaerobic hybrid reactor. Desalin Water Treat 4(1–3):224–228CrossRefGoogle Scholar
  10. Huang L, Sun G, Yang T et al (2013) A preliminary study of anaerobic treatment coupled with micro-electrolysis for anthraquinone dye wastewater. Desalination 309:91–96CrossRefGoogle Scholar
  11. Kim DG, Kim WY, Yun CY et al (2013) Agro-industrial wastewater treatment by electrolysis technology. Int J Electrochem Sci 8(7):9835–9850Google Scholar
  12. Kokabian B, Bonakdarpour B, Fazel S (2013) The effect of salt on the performance and characteristics of a combined anaerobic–aerobic biological process for the treatment of synthetic wastewaters containing Reactive Black 5. Chem Eng J 221:363–372CrossRefGoogle Scholar
  13. Lai B, Zhou Y, Yang P (2012) Passivation of sponge iron and GAC in Fe0/GAC mixed-potential corrosion reactor. Ind Eng Chem Res 51(22):7777–7785CrossRefGoogle Scholar
  14. Li G, Guo S, Li F (2010) Treatment of oilfield produced water by anaerobic process coupled with micro-electrolysis. J Environ Sci 22(12):1875–1882CrossRefGoogle Scholar
  15. Li G, Ma X, Tu J (2011) Treatment of starch wastewater using UASB reactor with hydraulic circulation and biomass screen. Water Resource and Environmental Protection (ISWREP), 2011 International Symposium IEEE 2:834–837Google Scholar
  16. Lide DR (ed) (2012) CRC handbook of chemistry and physics. CRC Press, Boca RatonGoogle Scholar
  17. Lin SH, Shyu CT, Sun MC (1998) Saline wastewater treatment by electrochemical method. Water Res 32(4):1059–1066CrossRefGoogle Scholar
  18. Qin L, Zhang G, Meng Q et al (2012) Enhanced MBR by internal micro-electrolysis for degradation of anthraquinone dye wastewater. Chem Eng J 210:575–584CrossRefGoogle Scholar
  19. Rajasimman M, Karthikeyan C (2007) Aerobic digestion of starch wastewater in a fluidized bed bioreactor with low density biomass support. J Hazard Mater 143(1):82–86CrossRefGoogle Scholar
  20. Shi X, Lefebvre O, Ng KK et al (2014) Sequential anaerobic–aerobic treatment of pharmaceutical wastewater with high salinity. Bioresour Technol 153:79–86CrossRefGoogle Scholar
  21. Sun L, Wan S, Yu Z et al (2012) Anaerobic biological treatment of high strength cassava starch wastewater in a new type up-flow multistage anaerobic reactor. Bioresour Technol 104:280–288CrossRefGoogle Scholar
  22. Tao M, Kang TT (2014) Experimental study on high salt acid pretreatment of refinery wastewater. Adv Mater Res 859:369–372CrossRefGoogle Scholar
  23. Toprak H (1995) Temperature and organic loading dependency of methane and carbon dioxide emission rates of a full-scale anaerobic waste stabilization pond. Water Res 29(4):1111–1119CrossRefGoogle Scholar
  24. Zaviska F, Drogui P, Pablo G (2012) Statistical optimization of active chlorine production from a synthetic saline effluent by electrolysis. Desalination 296:16–23CrossRefGoogle Scholar
  25. Zhang H, Zhang D, Zhou J (2006) Removal of COD from landfill leachate by electro-Fenton method. J Hazard Mater 135(1):106–111CrossRefGoogle Scholar
  26. Zhang W, Chen L, Chen H, Xia SQ (2007) The effect of Fe0/Fe2+/Fe3+ on nitrobenzene degradation in the anaerobic sludge. Hazard Mater 143:57–64CrossRefGoogle Scholar
  27. Zhou Z, Hu DL, Zhang CQ et al (2014) Study on treatment of ammonium nitrogen in desulfurization and denitrification wastewater with sodium hypochlorite. Adv Mater Res 864:438–441CrossRefGoogle Scholar

Copyright information

© The Author(s) 2016

Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (, which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made.

Authors and Affiliations

  1. 1.School of Environment and ArchitectureUniversity of Shanghai for Science and TechnologyShanghaiChina
  2. 2.Environment Protection DepartmentShanghai Anyo Energy Efficiency Co., LtdShanghaiChina

Personalised recommendations