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Bibi Saima Zeb, Qaisar Mahmood, Saima Jadoon, Arshid Pervez, Muhammad Irshad, Muhammad Bilal, Zulfiqar Ahmad Bhatti, "Corrigendum to “Combined Industrial Wastewater Treatment in Anaerobic Bioreactor Post-Treated in Constructed Wetland”", BioMed Research International, vol. 2020, Article ID 6102379, 9 pages, 2020.

Corrigendum to “Combined Industrial Wastewater Treatment in Anaerobic Bioreactor Post-Treated in Constructed Wetland”

Received29 Apr 2020
Accepted21 May 2020
Published29 Sep 2020

In the article titled “Combined Industrial Wastewater Treatment in Anaerobic Bioreactor Post-treated in Constructed Wetland” [1], there were typographical errors and errors in the figures. These have been corrected in the revised version shown below: (1)The abstract was revised for typographical errors(2)Language corrections were made in the text(3)The objectives of the study were clearly mentioned(4)All acronyms were spelled out when used for the first time(5)Corrections were made to the captions of Figures 1 to 10, to aid clear understanding of the plots(6)Table 2 was deleted as its values were repeated in Table 3 and hence section 3.1 was also deleted(7)A separate Discussion section was added(8)An additional article was cited as reference 42 [2] and the previous references 42-49 became references 43-50

The corrected article is as follows.


Constructed Wetland (CW), containing monoculture of Arundo donax L., was investigated for the post-treatment of effluent from Anaerobic Bioreactor (ABR) treating combined industrial wastewater. Different dilutions of combined industrial wastewater (20, 40, 60, and 80% v/v) and original wastewater were fed into the ABR as pretreatment. ABR effluent was post-treated by the laboratory scale CW. The removal efficiencies of Chemical Oxygen Demand (COD), Biochemical Oxygen Demand (BOD), Total Suspended Solids (TSS), nitrates and ammonia were 80%, 78-82%, 91.7%, 88-92% and 100%, respectively, for original industrial wastewater treated in ABR. ABR was found efficient in the removal of the metals Ni, Pb and Cd with removal efficiencies in the order of Cd (2.7%) > Ni (79%) > Pb (85%). Post-treatment of the ABR-treated effluent was carried out in lab scale CW planted with A. donax L. CW was effective in removal of COD and various heavy metals present in ABR effluents. Post-treatment in CW resulted in reducing the metal concentrations of Ni, Pb and Cd to 1.95 mg/L, 0 mg/L and 0.004 mg/L, respectively, which were within the limits of permissible water quality standards for industrial effluents. The treatment strategy was effective and sustainable to treat combined industrial wastewater.

1. Introduction

Pakistan’s current population of 180 million is expected to grow to about 221 million by the year end 2025 [1]. In Pakistan and other developing countries, water pollution is a major threat to the livelihood of people [2]. Heavy metal contamination of aquatic and terrestrial ecosystems is a major environmental problem. Each pollution problem calls for specific optimal and cost-effective solutions; if one technology proves less effective or ineffective, another takes its place. It is indispensable to treat industrial wastewaters for their subsequent use for irrigation, drinking and other purposes. In addition, due to an increased scarcity of clean water, there is a need for appropriate management of available water resources [3]. Factors like profound demographic changes, economic changes and the global energy crisis are compelling the implementation of low-cost natural treatment systems for domestic and industrial wastewaters [1].

In recent years, wastewater treatment strategies have shifted to one of the most promising methods, i.e. biological anaerobic treatment with the adoption of high rate anaerobic systems like up-flow anaerobic sludge blanket (UASB) reactor and other related treatment systems. The outstanding characteristics of high-rate Anaerobic Bioreactors (ABR) include anaerobic microorganisms capable of aggregation, low operational and maintenance costs, energy recovery in the form of biogas, low energy consumption and low production of digested sludge [4-7]. In developing countries like India, Brazil and Colombia, where financial resources are generally scarce due to high energy costs, the process is familiar as one of the most feasible methods for wastewater treatment. Despite several modifications, the quality of ABR-treated effluent hardly ever meets the discharge standards [6, 8]. Lettinga and co-researchers applied ABR process for municipal wastewater treatment since the early 1980s [9-13] and reported that about 70% chemical oxygen demand (COD) removal can be achieved under warm climates [6, 14, 15]. Since its inception, wider hype has been gained by this process [16, 17]. ABR-treated effluents can be employed for irrigation of various crops. However, such type of effluent may be high in COD, biological oxygen demand (BOD) and coliforms [18]. Thus, additional post-treatment strategy is mandatory for ABR-treated effluents if further use is desired [19-21].

CW wastewater treatment systems are engineered structures specifically designed for treating wastewater by optimizing the physical, chemical and biological processes that occur in natural wetland ecosystems [1, 18, 22-24]. CW is known as green technology, which uses plants for the removal of contaminants from a specified area, and the process is known as phytoremediation [25]. CW is a low cost or economical on-site wastewater treatment technology which is not only effective but also aesthetically pleasing. Since 1980, the utilization of the CW for the treatment of variety of wastewater has quickly become widespread. The amount of nutrients removed by plants and stored in their tissues is highly relative, which depends on the plant type, biomass and nutrient concentration in tissues [26].

The plant species, media like sand and gravel of specific ratio and size and containers are the foundation materials for CW. There are two major types of CW: subsurface flowing water (SSF) CW and free water surface (FWS) flowing CW. A variety of macrophytes are used in CW and the most common are floating macrophytes (i.e. Lemna spp or Eichhornia crassipes), submerged macrophytes (i.e. Elodea canadiensis) and rooted emergent macrophytes (i.e. Phragmites australis and Typha anguistifolia). The plants roots create a conducive environment for microbial growth and in winter the plant litter acts as an insulator. CW is an attached-growth biological reactor, which tender higher pollutant removal efficiency through physical, chemical and biological mechanisms. The common removal mechanisms associated with wetlands include sedimentation, coagulation, adsorption, filtration, biological uptake and microbial transformation [3, 24, 27].

CW technology is well-known at present, but it is not well documented for treating specific industrial effluents [28-30] and it can be used for polishing effluents of anaerobic bioreactors. A variety of post-treatment configurations based on various combinations with ABR have been studied; ABR followed by final polishing units (FPU) or polishing pond (PP) is a common process used in India, Colombia and Brazil due to its simplicity in operation [6, 31-33]. The implementation of low-cost, simple mitigation measures is required for the timely control and sustainable management of pollution problems in developing countries. The objective of this study was to evaluate the performance of ABR for the treatment of combined industrial wastewater followed by post-treatment in CW planted with A. donax.

2. Materials and Methods

2.1. Collection of Wastewater and Treatment

The industrial wastewater was collected from a combined drain at Hattar Industrial Estate (HIE), Hattar, Pakistan as grab samples. A number of industries are operating in HIE, like steel rerolling, paper recycling, ghee, food, beverages and cement. The physicochemical parameters like pH, turbidity and electric conductivity (EC) were determined onsite using portable pH, EC and turbidity analyzer, while the rest were analyzed in the laboratory within 24 h. As a treatment strategy and to avoid toxic effects of the pollutants, various dilutions (with distilled water) of wastewater included 20, 40, 60 and 80% (v/v) to feed into ABR, after which original wastewater was also treated in ABR and then CW.

2.2. ABR Experimental Set- up

This research work was carried out in the Bioremediation Laboratory of COMSATS Institute of Information Technology, Abbottabad, Pakistan. In this study, ABR was used as primary treatment step. A lab scale ABR was operated in up-flow mode with biomass retention as shown in Figure 1. The reactor is made of Perspex with a working volume of 5 L. The influent was pumped into ABR using a peristaltic pump from the influent vessel to the reactor (Figure 1). The flow rate was adjusted according to results of a startup study. A recycling pump was used to mix the influent (substrate) and sludge (biocatalyst) and to decrease possible substrate inhibition. The ratio of recycle flow to the influent flow was set at about 2.5-3. Bioreactor start up was carried out by feeding synthetic wastewater and nutrient solution at various Organic Loading Rate (OLR) and COD by using organic compounds at a fixed Hydraulic Retention Time (HRT) but increasing OLR, and at a fixed OLR but decreasing HRT. The ABR reactor in the Department of Environmental Sciences, COMSATS, Abbottabad was used for various types of the wastewater treatments in the past. Different wastewaters like domestic, industrial, municipal wastewater were treated through this ABR.

Inoculum was collected from the anaerobic methanogenic reactor in COMSATS Institute of Information and Technology Abbottabad, operating in the same laboratory. Its total solids (TS) and volatile solids (VS) were 115.6 g/L and 33.61 g/L, respectively, with VS/TS ratio of 0.25. The ABR reactor was fed with synthetic wastewater in order to enrich the sludge and for acclimatization of bacteria to the new substrates.

The reactor was fed on a daily basis with freshly prepared synthetic influent containing NaHCO3 (as a source of inorganic carbon for the growth of bacteria), MgCl2, KH2PO4, (1 g/L each), (NH4)2SO4 (0.24 g/L) and trace element solution (1 ml/L). The trace element solution contained Na2–EDTA (5 g/L), NaOH (11 g/L), CaCl2.2H2O (11 g/L), FeCl2·4H2O (3.58 g/L), MnCl2.2H2O (2.5 g/l), ZnCl2 (1.06 g/L), CoCl2.6H2O (0.5 g/L), (NH+4)6Mo7O24.4H2O (0.5 g/L) and CuCl2.2H2O (0.14 g/L). Sucrose is used as source of COD, the starting COD feeding to the ABR reactor was 200 mg/L and, then increased up to 3000 mg/L. The influent was flushed with argon gas for five minutes to create anoxic conditions. The ABR reactor was operated at 20°C, operating at a different HRT (hydraulic retention time) and Organic Loading Rates in order to analyze the process performance.

2.3. Experimental Set-up

The lab scale experimental CW consisted of two independent rectangular basins (length: 120 cm, width: 90 cm, depth: 40 cm). The basins were filled with gravel, sand and soil from bottom to top with one layer of each as shown in Figure 2. Each basin had a 10% slope and was equipped with a nozzle outlet to discharge the treated effluent. The CW was planted with A. donax (6 shoots/m2) taken from the botanical garden of the institute.

An unplanted bed served as a control. Treated effluents were collected directly from the lab scale experimental plant. The operational conditions of the experimental set up of CW are shown in Table 1. All plants, sand and gravel were properly washed before planting into CW system.

Dimensions of CW
Length1.2 m
Width0.9 m
Total height0.6 m
Total container volume0.432 m3
Water depth0.3 m
Substrate depth0.25 m
Plant nameArundo donax L (Giant reed)
No. of rhizome/m23

Operational conditions
OLR538 kg/ha/d
HRT3 days
Hydraulic load rate (HLR)862 m3/ha/d

Pollutant removal rates (%) were calculated according to the following equation:


Where: R is the removal rate, Ci is the concentration (mg/L) of the considered parameter in the untreated WW (influent), Cf is the concentration (mg/L) of the considered parameter in the treatment bed effluent.

2.4. Analytical Procedures

Raw and treated samples were analyzed for their BOD, COD, EC, pH, turbidity etc., according to the standard methods [34]. For COD determination closed reflux, colorimetric method included digestion at 150°C for 2 h in COD vials followed by spectrophotometer reading at 530 nm [34]. The pH was measured using a digital pH meter (HANNA, HI 991003 Sensor) while total dissolved solids (TDS) and conductivity were determined by HANNA, HI9835 Microprocessor. Heavy metals were analyzed through atomic absorption spectrophotometer. At least three readings were taken for each parameter each time and then the mean value was calculated.

2.5. Statistical Analysis

Collected data were analyzed by descriptive statistics and arithmetic averages of percent removal were calculated using Microsoft Excel XP version 2010 and Origin Lab 8.

3. Results and Discussion

3.1. Pretreatment of Combined Industrial Wastewater in ABR

The ABR was fed with combined industrial wastewater for treatment at retention time of 12 h. The treated effluent characteristics and percent removal efficiency are showed in Table 2.

ParametersInfluent/raw wastewaterABR effluent% removal
20%40%60%80%Original WW20%40%60%80%Original WW20%40%60%80%Original WW

Conductivity (μs)627646645676702654616645687702

The results describe the performance of the ABR for the treatment of combined industrial wastewater, as the concentrations of COD before pretreatment were 70, 189, 284, 379 and 474 mg/L, respectively, for 20, 40, 60 and 80% dilutions, and original wastewater. After pre-treatment with ABR, the COD was reduced to 42, 54, 121, 159, 297 mg/L with 40.0, 40.8, 57.3, 58.0, 37.3% removal efficiency, respectively. The results in Figure 3 show the maximum COD removal efficiency for the 80% dilution of the wastewater through ABR. The ABR also reduced the BOD concentrations of the dilutions in 78 to 82%, as shown in Figure 3. The BOD concentration reduced from 23.3, 25.4, 50.9, 77.0 and 84.8 mg/L to 18.5, 4.16, 5.1, 10.2 and 18.5, respectively. It was observed from the results that ABR showed excellent removal efficiency for BOD.

Total solids were tremendously removed by 84% with the corresponding concentration of 1960 mg/L for original wastewater. The concentration of NO3-N was reduced from 24, 59, 83, 98, 145 to 1.8, 6.1, 9.23, 8.9, and 16 mg/L for 20, 40, 60, 80% dilutions and original wastewater. ABR showed 88 to 92% removal efficiency for the NO3-Nitrogen as shown in Figure 4.

Similarly, the removal efficiency of NH4-N was 87.6, 90.8, 90, 85.9 and 87.8% for the four different dilutions 20, 40, 60, 80% and original wastewater, respectively, as shown in Figure 4. The concentrations of NH4- N of 17, 23, 45, 57 and 82 mg/L were reduced to 2.1, 2.1, 4.5, 8 and 10 mg/L. On the other hand, Pb, Ni and Cd removal by reactor was 2.7%, 79% and 85.4% for real industrial wastewater. Heavy metal removal was found in the order Cd > Ni > Pb as shown in Figure 5.

3.2. Post Treatment of ABR Effluent with CW

The pre-treated effluent was then further treated by CW for 30 days for each dilution. The results for FWS CW effluent are shown in Figures 610 with pollutant removal efficiency.

The results of treatment in CW showed efficient removal efficiency for COD, BOD, TS, nitrates, ammonia and metals like Pb, Ni and Cd. The residual concentrations of COD and BOD were 64.3, 66.7, 67, 76.4, 82.4 and 78.4, 76, 80.3, 80.3 and 78.4 mg/L, respectively, for the corresponding dilutions of 20, 40, 60, 80% and original WW as shown in Figures 6 and 7. The CW showed the highest COD removal efficiency of 82.4% for original WW, but at the same dilution the BOD was reduced to 78.4%. Nitrates and ammonia removal efficiency was found to be 95, 82, 86, 72, 75% for the respective concentrations of 1.8, 6.1, 9.23, 8.9 and 16 mg/L of the corresponding four different dilutions and original pre-treated effluent. Ammonia removal was not satisfactory compared to other parameters and the highest removal efficiency was 70.1% by CW.

3.3. Discussion

Previous workers observed that the treatment of complex industrial wastewater reduced the efficiency of the ABR [35], as also observed in the present study. However, ABR showed promising results regarding treatment of BOD in the present work. During anaerobic digestion of organic matter, biochemical reactions take place which are affected by heavy metal presence [35]. It is clear from the results that soluble heavy metals rapidly decreased at the initial concentrations. It depends on which chemical form the heavy metal exists in. The most common and important form of heavy metals are precipitation (as sulfides, carbonates and hydroxides), sorption on to solid form (inhibitory effect of heavy metals on anaerobic sludge) [36]. Ni could be bound in all forms. So it was clear that high initial concentrations were tolerated by the ABR sludge and thus showed the satisfactory removal of heavy metals.

However, the residual concentration of organic (BOD and COD) and heavy metals in the anaerobic reactor effluent usually exceeds the maximum permissible level prescribed by the effluent discharge standards of most developing countries [20, 37-38]. From this standpoint, post-treatment of anaerobic effluent is necessary to reduce these contaminants to the required level [39].

CW normally improves the dissolved oxygen (DO) in wetland. The introduction of excess organic matter may result in depletion of oxygen from an aquatic system. Prolonged exposure to low dissolved oxygen levels (<5.0– 6.0 mg/L) may not directly kill an organism, but will increase its susceptibility to other environmental stresses. Exposure to <30% saturation (<2.0 mg/L oxygen) for one to four days kills most of the biota in a system. If oxygen-requiring organisms perish, the remaining organisms will be air-breathing insects and anaerobic (not requiring oxygen) bacteria [40]. If all oxygen is depleted, aerobic (oxygen-consuming) decomposition ceases. So, treating pollutants in wetlands may help to increase DO, which is consumed by the other aerobes. In this experiment during the post-treatment by CW the DO increased to 8.8 mg/L.

Industrial wastewater was previously treated in two-stage constructed wetland [41] planted with Typha latifolia and Phragmites australis. For tannery wastewater, CW may be an interesting treatment option. Two-stage series of horizontal subsurface flow CW with Phragmites australis (UP series) and Typha latifolia (UT series) provided high removal of organics from tannery wastewater, up to 88% of BOD(5) (from an inlet of 420 to 1000 mg/L) and 92% of COD (from an inlet of 808 to 24vx49 mg/L) and of other contaminants, such as nitrogen, operating at hydraulic retention times of 2, 5 and 7 days. Overall mass removals of up to 1294 kg COD/ha/d and 529 kg BOD(5)/ha/d were achieved for a loading ranging from 242 to 1925 kg COD/ha/d and from 126 to 900 kg BOD(5)/ha/d. Plants were resilient to the conditions imposed, however P. australis exceeded T. latifolia in terms of propagation [41].

In the present study, A. donax was used in the CW for post-treatment, which showed an efficient performance for the further removal of pollutants from the ABR pre-treated effluent. The results confirmed that effluent showed traces of heavy metals Ni and Cd with the corresponding ABR treated wastewater at almost all the levels of dilutions of 20, 40, 60, 80% and original wastewater. CW showed the maximum removal efficiency for Ni and Cd as depicted in Figures 9 and 10, respectively. CW post-treatment of Pb was not satisfactory in reduction of its concentration. Using the San Joaquin Marsh constructed wetlands, the removal efficiencies for four heavy metal elements Cd, Cu, Pb and Zn were evaluated. It was found that the effluent metal concentrations were not substantially lower than the influent. The removal efficiencies of 23.9%, 10.6%, and 17.6% were found for Cd, Cu, and Zn, respectively. No significant reduction was observed for concentrations of Pb [43].

The removal of metals and metalloids from contaminated waters was investigated in constructed wetlands. Metal removal rates in wetlands depend on the type of element (Hg > Mn > Fe ¼ Cd > Pb ¼ Cr > Zn ¼ Cu > Al > Ni > As), their ionic forms, substrate conditions, season, and plant species. Standardized procedures and data are lacking for efficiently comparing properties of plants and substrates. The study depicted the relative treatment efficiency index (RTEI) to quantify treatment impacts on metal removal in constructed wetlands [44].

Various mechanisms, including sedimentation, filtration, chemical precipitation, adsorption, microbial interactions and uptake by vegetation have been attributed with the removal of metals within CW. Specifically, the major processes that are responsible for metal removal in CW are binding to sediments and soils, precipitation as insoluble salts and uptake by plants and bacteria [45]. In CW, substrate interactions remove most metals from contaminated water [46]. The anoxic condition of wetland soil helps create an environment for immobilization of heavy metals in the highly reduced sulfite or metallic form [47]. Wetland plants adsorb and accumulate metals in tissues, which can play important role in CW pollutant treatment efficiency [48]. Phytoremediation, using vegetation to remove, detoxify, or stabilize heavy metal pollutants, is an accepted tool for cleaning polluted soils and waters [49]. Research has also shown that metal storage in sediment is influenced by vegetation. Concentrations of metals were significantly higher in the vegetated sediments than in the non-vegetated sediments [50].

4. Conclusion

This paper presented the evaluation results on removal efficiencies for COD, BOD, nitrates, TS, and heavy metals (Cd, Ni, Pb) in ABR and post-treated by a lab scale Arundo donax based CW. It was clearly observed that post-treatment accomplished efficient removal of the COD, BOD, TS, Ni, and Cd. The efficiency of both the treatment systems was not very satisfactory for Pb removal. Because of the positive effects of vegetation on metal removal efficiency, CWs containing A. donax is recommended for HIE combined wastewater treatment.


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Conflicts of Interest

The authors have neither any conflict of interest nor financial gain from the present manuscript.


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Copyright © 2020 Bibi Saima Zeb et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

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