Biological degradation of catechol in wastewater using the sequencing continuous-inflow reactor (SCR)
© Aghapour et al.; licensee BioMed Central Ltd. 2013
Received: 20 October 2012
Accepted: 21 April 2013
Published: 24 May 2013
Catechol is used in many industries. It can be removed from wastewater by various methods but biological processes are the most superior and commonly used technology. The SCR is a modified form of SBR used to degrade catechol. The objective of this study was to investigate the performance of SCR for biodegradation and mineralization of catechol under various inlet concentrations (630–1500 mg/L) and hydraulic retention times (HRT) (18–9 h). This study used a bench scale SCR setup to test catechol degradation. The acclimation time of biomass for catechol at degradation at 630 mg/L was 41 d. The SCR operating cycle time was 6 h and the consecutive times taken for aerating, settling and decanting were 4, 1.5 and 0.5 h, respectively. This study investigated the effects of inlet catechol concentration (630–1560 mg/L) and HRT (18–9 h). The average catechol removal efficiencies in steady-state conditions of 630, 930, 12954 and 1559 mg/L of catechol were 98.5%, 98.5%, 98.2% and 96.9% in terms catechol and 97.8%, 97.7%, 96.4% and 94.3% for COD, respectively. SCR with acclimated biomasses could effectively remove the catechol and the corresponding COD from wastewater with concentrations of up to 1560, at the loading rate of 5.38 kg COD/m3.d and at a HRT of up to 13 h. The HRT was determined as an important variable affecting catechol removal from wastewater. Reducing the HRT to below 13 h led to reduced removal of catechol and COD.
KeywordsCatechol Sequencing continuous-inflow reactor SCR Biodegradation Mineralization HRT
Catechol, (a derivative of benzene and a phenolic compound) it has many applications in industry for example as a photographic developer, lubricating oil, polymerization inhibitor and in pharmaceuticals [1, 2]. Catechol has a strong aroma; it is also a toxic and persistent water pollutant in the environment . The International Agency for Research on Cancer (IARC) has classified catechol in terms of a carcinogenic risk to humans (Group 2 B) . Phenolic compounds such as catechol have been listed as priority-pollutants by EPA, USA [2, 3]. Catechol is fatally toxic to fish at concentrations of 5–25 mg/L and it inhibits biological growth in microorganisms [4, 5]. It has been detected in wastewater from coal conversion processes, crude wood tar, and drainage water from bituminous shale and in the outflow from coal-tar chemical production. Its concentration varies from a few mg/L to 2000 mg/L in wastewater from coal carbonization and gasification. At low temperature wastewater from coal carbonization, its concentration may be as high as 5300 mg/L [2, 6, 7]. To protect against the hazards of catechol to public health and the environment, catechol bearing aqueous waste must be treated with an efficient, cost effective and environmentally benign technique before being discharged [8, 9].
A review of the related literature indicates that most investigations reporting on catechol removal from wastewater have focused on physical, chemical and biological processes. Physical processes such as adsorption transfer of pollutants from a liquid to a solid phase involve further treatment of the by-products. Chemical processes such as photocatalysis, Fenton, photo-Fenton and Ozonation processes are very efficient but expensive methods available for the mineralization of catechol. However, these chemical processes are often incomplete and create by-products that contribute to serious health risks and environmental hazards [1, 10–12]. Biological processes have several technical advantages for treating biodegradable waste including greater cost-effectiveness, simplicity of implementation and operation and reliability, they are also environmentally benign with a high capacity for degradation . In these terms biological processes are superior to other technologies such as physical and chemical processes used to treat biodegradable contamination.
Some researchers have studied the degradation of catechol in anaerobic bioreactors including up flow fixed film–fixed bed bioreactors  and UASB [2, 6] acclimated to this compound. In the up flow fixed film–fixed bed reactor, at the loading rate of 4.79 kg catechol/m3.d, percentages for maximum degradation and COD removal of catechol were 93.11% and 90.81%, respectively . The biodegradation of catechol through co-metabolism with glucose in an upflow anaerobic sludge blanket (UASB) reactor achieved 95% COD removal efficiency with 500–1000 mg/L catechol concentration in the feed and a glucose concentration of 1500 mg/L as a cosubstrate . Due to the greater inhibitory effect of phenolic compounds on anaerobic microbial metabolism, aerobic biological methods are conventionally preferred to anaerobic biological methods for the treatment of wastewater .
Aerobic microorganisms are able to degrade organic toxic compounds more efficiently because they have higher growth rates than anaerobes and usually covert organic compounds to inorganic compounds (CO2, H2O) . Many groups of aerobic bacteria are capable of using aromatic compounds as sole carbon and energy sources. There have been several reports on the biodegradation of catechol by some microbial strains under aerobic conditions such as Pseudomonas putida , Aspergillus awamori  and Candida parapsilopsis . The bacterial strain Pseudomonas putida in a basal salt medium (BSM) at 29.9°C and pH 7 demonstrated the complete degradation of 500 mg/L of catecholin 94 h . Candida parapsilopsis, in a standard medium, demonstrated the complete degradation of catechol at the concentration of 910 mg/L within 48 h .
However, research has shown that mixed microbial communities are more efficient than pure cultures in terms of their inhibitory effect of organic compounds in wastewater because of the various different organisms present, all of which are necessary for the degradation process . Additionally, the aerobic metabolism is usually the most rapid biodegradation process for biodegradable pollutants [10, 16].
Among those bioreactors invented to treat biological wastewater, SBR has some major advantages such as flexibility, robustness, single basin operation, better control of shock loads, simplicity of operation, relatively low cost and no sludge loss in the reaction period and hence no need to return the activated sludge [3, 17, 18]. SBR is therefore the most commonly applied type of biological process used to treat industrial wastewater [3, 19, 20]. When SBR is used to degrade toxic and inhibitory compounds, batch feeding of the substrate is a main defect for SBR because it affects the biodegradation rate of the substrate [11, 21]. Nonetheless, due to the batch feeding mode, it requires multiple reactors to treat a continuous inflow .
Research by Moussavi et al. (2010) has recently begun to investigate efforts to modify SBR to overcome its defects . Therefore, the mode of feeding the SBR modified from batch setting to continuous, showed a modification procedure to recuperate its performance in degrading toxic and inhibitory compounds through an adjustment of the loading peak and shock, as well as in allowing continuous treatment of wastewater in a single-basin bioreactor [11, 21]. Since the SCR has only recently been introduced and demonstrates highly effective performance in the degradation of phenol and formaldehyde  and a mixture of formaldehyde and ammonia , it is considered worthwhile to examine the capability of this process of degradation of other substances with resistance to organic material including catechol that is frequently found in waste streams.
So, the objective of this study was to investigate the performance of SCR for biodegradation and mineralization under various inlet catechol concentrations (630–1500 mg/L) and hydraulic retention times (HRT) (18–9 h). The performance of SCR was evaluated in terms of degradation and chemical oxygen demand (COD) in the process of removing catechol from contaminated water.
Materials and methods
Feed synthetic wastewater was prepared daily by dissolving catechol (Merck >99%) in tap water and adding aliquots of stock nutrient solution. The stock nutrient solution was prepared by dissolving 5 g K2HPO4, 15 gr KH2PO4, 120 g NH4Cl, 12 g (NH4)2HPO4, 10 g CaCO3 and 10 g NaHCO3 in one liter of tap water. Catechol was used as sole sources of carbon and energy and NH4Cl, K2HPO4, KH2PO4 and (NH4)2HPO4 were used for sources of nitrogen and phosphorous in the biomass in the SCR. The COD: N: P ratio in the feed wastewater was kept constant at 100:5:1 for all tests.
Biomass acclimation and reactor start-up and operation
At the beginning of the reactor start-up, the SCR was inoculated with 1.5 L of an acclimatized phenol degrading biomass  and 1.5 L of an acclimatized furfural degrading biomass , making the suspended solid concentration of 5000 mg/L in the SCR and operational in a continuous current condition. As the seed biomasses were already acclimated to phenol and furfural, the acclimation of biomass to catechol began with 600 mg/L furfural, then the concentration of furfural in the feed wastewater was gradually reduced and catechol was correspondingly increased to an approximate level of 600 mg/L. The starting time was considered to be complete when 95% removal of 630 mg/L catechol was obtained in the SCR.
After successful start up had been achieved, the effect of inlet catechol concentration (630 mg/L) and HRT (18 and 9 h) at each run, the concentration of biomass (measured at the end of decant phase) was 10 ± 1 g/L and kept constant over the course of the experiment by discharging the mixed liquor. The retention time for sludge in the bioreactor was calculated to be 21 d and that was kept constant throughout the tests in the study. The pH level of the feed wastewater was maintained at the value of around 7.2 ± 0.4 (the optimum value for bacterial growth) by adding CaCO3 and NaHCO3. The reactor was operated at room temperature (20 ± 2°C) over the course of tests.
Experimental phases and SCR operation schedule
Catechol inlet (mg/L)
COD inlet (mg/L)
Flow rate (L/d)
kg COD/m 3.d
Effect of catechol concentration
Effect of HRT
The inlet and outlet of the reactor were sampled daily and analyzed for catechol, COD, pH and TSS parameters. In order to measure catechol and COD, samples were filtered to remove particles before analysis using a Whatman filter with a 0.45 μm pore size. Concentrations of catechol were measured using the 5530D method of Standard Methods . The mineralization rate of catechol was determined by COD measurements . Concentrations of total suspended solids (TSS) in the mixed liquor were measured according to standard methods at regular intervals. All parameters were measured according to standard methods . The pH level was measured using an electrode.
Results and discussion
Effect of inlet catechol concentration
However in the steady-state condition (days 115–122 of the operation), the effluent was colorless and the absorption wavelengths at 375 nm were very low (Figure 5). It can therefore be inferred that at the steady-state condition, catechol was degraded via the ortho cleaving pathway, while transiting the concentration of catechol conditions, degradation was probably accomplished via both ortho and meta cleaving pathways. Accordingly, the higher effluent concentrations of COD than of catechol at higher inlet concentrations can be attributed to the formation of organic intermediate compounds, as shown in Figure 4 .
Nonetheless, the SCR attained mineralization of 3.60 kg COD/m3.d at the maximum applied inlet load of 3.82 kg COD/m3.d. This indicates that the capacity of SCR for mineralization of catechol is greater than the level obtained. No work could be found in the available literature on the aerobic biodegradation of catechol in SCR. There are currently only a few studies on the anaerobic biological degradation of catechol by UASB and upflow fixed film–fixed bed reactors. Latkar et al., (2003) reported that the maximum substrate removal of 93.11% and COD removal of 90.81% in upflow fixed film–fixed bed reactors at the catechol concentration of 750 mg/L, the loading rate of 4.79 kg catechol/m3.d and the HRT of 6 h . Research by Subramanyam and Mishra  investigated the biodegradation of catechol through co-metabolism with glucose by UASB reactor and demonstrated a rate of more than 95% COD removal efficiency when the reactor feed contained catechol in concentrations ranging from 500 to 1000 mg/L (OLR=2.86-5.7 kg COD m3/d) with a constant glucose concentration of 1500 mg/L and a constant HRT of 8 h. Their another study  also demonstrated the performance of the UASB reactor for the co-degradation of catechol and resorcinol at a total concentration of 1000 mg/L (800 mg/L of catechol and 200 of mg/L resorcinol) with a fixed organic loading rate of 5.7 kg COD/m3d and with a HRT of 8 h and determined a removal efficiency of 92% as COD.
According to the literature, most investigations in to biodegradation of catechol have reported on tests under anaerobic conditions and/or through co-metabolic degradation processes, whereas biodegradation of catechol in SCR was accomplished by growth-linked biodegradation metabolism under aerobic conditions. In a growth-link biodegradation process, organic compounds such as catechol are used as sole sources of carbon and energy. This growth based process for biodegradation is the most rapid and complete method for the treatment of most organic pollutants such as catechol and the process results in the complete degradation of catechol compared with the co-metabolic degradation process . The co-metabolic degradation process is the basis of bio transformations or bioconversions and the process converts a substance to a chemically modified form . Furthermore, aerobic degradation processes have always been considered preferable to anaerobic degradation in terms of kinetics and capacity . Therefore, the SCR as an aerobic process transformed catechol to inorganic and environmentally acceptable compounds, whereas in an anaerobic condition, like UASB, it may be converted to incomplete and smelly compounds and may require further treatment. So, from a comparison of the results of tests in this study with the results reported in available literature, it can be induced that SCR performed much better in terms of degradation and mineralization of catechol than other processes.
Effect of hydraulic retention time
To investigate the effect of HRT on biodegradation and COD removal of catechol using SCR, the inlet flow rate was increased in steps from 6.28 to 25.12 L/d and then related to the HRTs of 18 to 13 and 9 h. The catechol concentration in the feed wastewater was kept at a constant 1560 mg/l. The time-course results for degradation and COD removal are shown in Figure 6 (zones D, E and F). As demonstrated in Figure 6, upon switching the SCR operation from HRT of 18 h to 13 h, (zone D to zone E corresponding to day 124 of the operation), catechol degradation and COD removal were at first slightly reduced to percentages of 83% and 73% respectively. As demonstrated in Figure 6 these sudden decreases in COD and catechol removal efficiencies at this zone were harsher than they had been in the previous zones. Similar to other switching conditions, a yellow color was observed in the bioreactor and the absorption wavelengths of the bioreactor outlet were increased at 375 nm. However, on continuing operation of the bioreactor there was a rapid improvement to its performance and steady-state performance was attained on day 159. A longer HRT duration to 9 h resulted in progressive reduction of degradation and COD removal of catechol. As can be seen in zone F of Figure 6, the rate of catechol degradation decreased to below 30% after 7 days upon HRT reduction. This suggests that the level of catechol loading on SCR was over the tolerable limit and thereby inhibited metabolism in the microbial degradation process. Accordingly, an HRT duration of 13 h, corresponding to an organic loading of 5.38 kg COD/m3, at which the COD removal 94% was selected as the optimum level for loading on the SCR. As mentioned earlier, Latkar (2003) reported that using upflow fixed film–fixed bed reactors could remove catechol and COD corresponding to 93.11% and 90.81% at the HRT of 6 h, concentrations of 750 mg/L and the loading of 4.79 kg catechol/m3/d. Subramanyam and Mishra  reported more than 95% COD removal efficiency through co-metabolism with glucose by UASB reactor at a HRT of 8 h, catechol concentration inlet range of 500–1000 mg/L, OLR=2.86-5.7 kg COD m3/d and with a constant glucose concentration of 1500 mg/L. Therefore, the findings of this study compared to those of the related literature indicated that SCR had greater biodegradation efficiency than that of UASB  and upflow fixed film–fixed bed reactors .
This work investigated the performance of SCR for degradation and COD removal of catechol from wastewater. The conclusions drawn from this work are summarized as follows:
The performance of SCR was not considerably affected by inlet catechol concentrations up to 1560 mg/L, with a loading rate of 3.82 kg COD/m3.d and at the HRT of 18 h.
The HRT is an important variable affecting catechol removal from wastewater in the SCR, in that reducing the HRT to below 13 h led to reductions in levels of catechol and COD removal.
The SCR with acclimated biomasses could efficiently eliminate over 96% and 94% of catechol and COD up to inlet loads of 5.38 kg COD/m3.d and at a HRT of up to 13 h.
The authors gratefully acknowledge the financial and technical support provided by the Tarbiat Modares University, Tehran, Iran.
- Lofrano G, Rizzo L, Grassi M, Belgiorno V: Advanced oxidation of catechol: A comparison among photocatalysis, Fenton and photo-Fenton processes. Desalination 2009, 249: 878–883. 10.1016/j.desal.2009.02.068View ArticleGoogle Scholar
- Subramanyam R, Mishra IM: Biodegradation of catechol (2-hydroxy phenol) bearing wastewater in an UASB reactor. Chemosphere 2007, 69: 816–824. 10.1016/j.chemosphere.2007.04.064View ArticleGoogle Scholar
- Moussavi G, Barikbin B, Mahmoudi M: The removal of high concentrations of phenol from saline wastewater using aerobic granular SBR. Chem Eng J 2010, 158: 498–504. 10.1016/j.cej.2010.01.038View ArticleGoogle Scholar
- Kumar A, Kumar S, Kumar S: Biodegradation kinetics of phenol and catechol using Pseudomonas putida MTCC 1194. Biochem Eng J 2005, 22: 151–159. 10.1016/j.bej.2004.09.006View ArticleGoogle Scholar
- Rigo M, Alegre RM, Bezerra JRMV, Coelho N, Bastos RG: Catechol Biodegradation kinetics Using Candida parapsilopsis. Braz Archives Biology Technology 2010, 53: 481–486. 10.1590/S1516-89132010000200029View ArticleGoogle Scholar
- Subramanyam R, Mishra IM: Co-degradation of resorcinol and catechol in an UASB reactor. Bioresour Technol 2008, 99: 4147–4157. 10.1016/j.biortech.2007.08.060View ArticleGoogle Scholar
- Subramanyam R, Mishra IM: Treatment of catechol bearing wastewater in an upflow anaerobic sludge blanket (UASB) reactor: Sludge characteristics. Bioresour Technol 2008, 99: 8917–8925. 10.1016/j.biortech.2008.04.067View ArticleGoogle Scholar
- Moussavi G, Mahmoudi M, Barikbin B: Biological removal of phenol from strong wastewaters using a novel MSBR. Water Research 2009, 43: 1295–1302. 10.1016/j.watres.2008.12.026View ArticleGoogle Scholar
- Mehrizad A, Aghaie M, Gharbani P, Dastmalchi S, Monajjemi M, Zare K: Comparison of 4-chloro-2-nitrophenol adsorption on single-walled and multi-walled carbon nanotubes. Iran J Environ Health Sci Eng 2012, 9: 5. 10.1186/1735-2746-9-5View ArticleGoogle Scholar
- Handan U, Ergun Y, Alper N: Phenol biodegradation in a batch jet loop bioreactor (JLB): Kinetics study and pH variation. Bioresour Technol 2010, 101: 2965–2971. 10.1016/j.biortech.2009.12.005View ArticleGoogle Scholar
- Moussavi G, Heidarizad M: The Performance of SBR, SCR and MSCR for Simultaneous biodegradation of high concentration of formaldehyde and ammonia. Sep purificaion Thechnology 2011, 77: 187–195. 10.1016/j.seppur.2010.11.028View ArticleGoogle Scholar
- Sarfaraz S, Thomas S, Tewari UK, Iyengar L: Anoxic treatment of phenolic wastewater in sequencing batch reactor. Water Res 2004, 38: 965–971. 10.1016/j.watres.2003.10.039View ArticleGoogle Scholar
- Latkar M, Swaminathan K, Chakrabarti T: Kinetics of anaerobic biodegradation of resorcinol catechol and hydroquinone in upflow fixed film–fixed bed reactors. Bioresour Technol 2003, 88: 69–74. 10.1016/S0960-8524(02)00261-4View ArticleGoogle Scholar
- Stanchev V, Stoilova I, Krastanov A: Biodegradation dynamics of high catechol concentrations by Aspergillus awamori. J Hazard Mater 2008, 154: 396–402. 10.1016/j.jhazmat.2007.10.038View ArticleGoogle Scholar
- Fritsche W, Hofrichter M: Aerobic Degradation of Recalcitrant Organic Compounds by Microorganisms. In Environmental Biotechnology Concepts and Applications. Edited by: Jördening HJ, Winter J. Weinheim: WILEY-VCH Verlag GmbH & Co. KGaA; 2005.Google Scholar
- Das N, Chandran P: Microbial Degradation of Petroleum Hydrocarbon Contaminants: An Overview. Biotechnol Res International 2011, 2011: 13.Google Scholar
- Mohseni-Bandpi A, Bazari H: Biological Treatment of Dairy Wastewater by Sequencing Batch Reactor. Iran J Environ Health Sci Eng 2004, 1: 65–69.Google Scholar
- Movahedyan H, Assadi A, Amin M: Effects of 4-chlorophenol loading on acclimation of biomasswith optimized fixed time sequencing batch reactor. Iran J Environ Health Sci Eng 2008, 5: 225–234.Google Scholar
- Ganjidoust H, Ayati B: Use of Sequencing Batch Reactors (SBRs) in Treatment of Wood Fiber Wastewater. Iran J Environ Health Sci Eng 2004, 1: 91–96.Google Scholar
- Mahvi AH: Sequencing batch reactor: a promising technology in wastewater treatment. Iran J Environ Health Sci Eng 2008, 5: 79–90.Google Scholar
- Moussavi G, Heidarizad M: Biodegradation of mixture of phenol and formaldehyde in wastewater using a single-basin MSCR process. J Biotechnol 2010, 150: 240–245.View ArticleGoogle Scholar
- Leili M, Moussavi G: Removal of Furfural from Wastewater Using Combined Catalytic Ozonation Process (COP) and Cyclic Biological Reactor (CBR). Tarbiat Modares University: Environmental Health Engineering; 2012.Google Scholar
- APHA: Standard methods for the examination of water and wastewater. 20th edition. Washington DC: American Public Health Association; 1998.Google Scholar
- Moussavi G, Mohseni M: The treatment of waste air containing phenol vapors in biotrickling filter. Chemosphere 2008, 72: 1649–1654. 10.1016/j.chemosphere.2008.05.040View ArticleGoogle Scholar
- Moreno-Andrade I, Buitrón G: Variation of the microbial activity during the acclimation phase of a SBR system degrading 4-chlorophenol. Water Sci Technol 2004, 50: 251–258.Google Scholar
- Allsop P, Chisti Y, Young M, Sullivan G: Dynamics of phenol degradation by Pseudomonas putida. Biotechnol Bioeng 1993, 41: 572–580. 10.1002/bit.260410510View ArticleGoogle Scholar
- Basha KM, Rajendran A, Thangavelu V: Recent advances in the Biodegradation of Phenol: A review. Asian J Exp Biol Sci 2010, 1: 219–234.Google Scholar
- Albaugh C: Degradation of monoaromatic compounds by an aerobic halotolerant alkaliphitic bacterium. Washington State University: Department of Chemical Engineering; 2005.Google Scholar
- Nair CI, Jayachandran Shashidhar KS: Biodegradation of phenol. Afr J Biotechnol 2008, 7: 4951–4958.Google Scholar
- Miguez C: Isolation and physiological characterization of two chlorobenzoic acid degrading bacteria from polychlorinated biphenyl contaminated soils. McGiII University: Department of Microbiology; 1993.Google Scholar
- ZAKI S: Detection of meta- and ortho-cleavage dioxygenases in bacterial phenol-degraders. J Appl Sci Environ Mgt 2006, 10: 75–81.Google Scholar
- Khleifat KM: Biodegradation of phenol by Ewingella americana: Effect of carbon starvation and some growth conditions. Process Biochem 2006, 41: 2010–2016. 10.1016/j.procbio.2006.04.015View ArticleGoogle Scholar
- Mahiudddin M, Fakhruddin ANM, Abdullah Al M: Degradation of Phenol via Meta Cleavage Pathway by Pseudomonas fluorescens PU1. ISRN Microbiology 2012, 2012: 6.View ArticleGoogle Scholar
- Ali S, Fernandez-Lafuente R, Cowan* DA: Meta-pathway degradation of phenolics by thermophilic Bacilli. Enzyme Microb Technol 1998, 23: 462–468. 10.1016/S0141-0229(98)00072-6View ArticleGoogle Scholar
- Loh K-C, Chua S-S: Ortho pathway of benzoate degradation in Pseudomonas putida:induction of meta pathway at high substrate concentrations. Enzyme Microb Technol 2002, 30: 620–626. 10.1016/S0141-0229(02)00016-9View ArticleGoogle Scholar
- Song J, Sung J, Kim YM, Zylstra GJ, Kim E: Roles of the meta- and the ortho-Cleavage Pathways for the Efficient Utilization of Aromatic Hydrocarbons by Sphingomonas yanoikuyae B1. J Microbiol 2000, 38: 245–249.Google Scholar
- Schink B: Principles of Anaerobic Degradation of Organic Compounds. In Environmental Biotechnology Concepts and Applications. Edited by: Jördening HJ, Winter J. Weinheim: WILEY-VCH Verlag GmbH & Co. KGaA; 2005.Google Scholar
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