Yian Wangab,
Xuehong Zhangab and
Hua Lin*ab
aCollege of Environmental Science and Engineering, Guilin University of Technology, 319 Yanshan Street, Guilin 541000, China. E-mail: linhua5894@163.com
bGuangxi Collaborative Innovation Center for Water Pollution Control and Water Safety in Karst Areas, Guilin University of Technology, 319 Yanshan Street, Guilin 541000, China
First published on 17th May 2022
Heavy metals and phenolic compounds existing in polluted wastewater are a threat to the environment and human safety. A downflow Leersia hexandra Swartz constructed wetland-microbial fuel cell (DLCW–MFC) was designed to treat polluted wastewater containing Cr(VI) and p-chlorophenol (4-CP). To determine the effect of 4-CP concentration and hydraulic retention time (HRT) on the performance of the DLCW–MFC system, the wastewater purification, electricity generation, electrochemical performance, and L. hexandra growth status were studied. Addition of 17.9 mg L−1 4-CP improved the power density (72.04 mW m−2) and the charge transfer capacity (exchange current, 4.72 × 10−3 A) of DLCW–MFC. The removal rates of Cr(VI) and 4-CP at a 4-CP concentration of 17.9 mg L−1 were 98.8% and 38.1%, respectively. The Cr content in L. hexandra was 17.66 mg/10 plants. However, a 4-CP concentration of 35.7 mg L−1 inhibited the removal of Cr(VI) and the growth of L. hexandra, and decreased the electricity generation (2.5 mW m−2) as well as exchange current (1.21 × 10−3 A) of DLCW–MFC. An increase in power density and removal of Cr(VI) and 4-CP, along with an enhanced transport coefficient of L. hexandra, was observed with HRT. At an optimal HRT of 6.5 d, the power density, coulomb efficiency, and exchange current of DLCW–MFC were 72.25 mW m−2, 2.38%, and 4.99 × 10−3 A, respectively. The removal rates of Cr(VI) and 4-CP were 99.0% and 78.6%, respectively. The Cr content and transport coefficient of L. hexandra were 4.56 mg/10 plants and 0.451, respectively. Thus, DLCW–MFC is a promising technology that can be used to detoxify polluted wastewater containing composite mixtures and synchronously generate electricity.
Constructed wetland (CW) is effective in removing phenols or Cr(VI).5,6 The hyperaccumulator Leersia hexandra has been used to remove Cr.7 Liu et al. found that the lack of electrons reduces the efficiency of Cr(VI) reduction to Cr(III), which decreases the Cr(VI) direct removal rate by L. hexandra and thus diminishes the chromium removal efficiency of L. hexandra CW.8 The emergence of microbial fuel cell (MFC) technology is expected to facilitate Cr(VI) reduction. MFC is effective in removing 4-CP, phenol or Cr(VI), and phenol is the main dechlorination product of 4-CP.9–11 Therefore, the combination of CW and MFC (CW–MFC) has been used to treat single pollutants.12,13 Fang et al. utilized CW–MFC to treat azo dyes at a power density of 11.8 mW m−2, and the azo dye decolorization efficiency was 91.05%.14 Studies also used other technologies such as biofilm electrode reactor-MFC and photocatalytic-MFC to treat refractory organics and synchronize electricity generation.15,16 These methods are usually used to treat single refractory organic compounds or heavy metals and are limited in their application for detoxification of aqueous environments containing composite mixtures of heavy metals and phenolic compounds.
Miran et al. reported that the 10–100 mg L−1 4-CP removal rate was approximately 40% and yielded electricity under different 4-CP concentrations and lactate as carbon sources in the MFC anode chamber.17 Phenol can be used as the only fuel for MFC electricity generation; however, the power output was only 6 mW m−2. The co-matrix type including glucose and phenol, azo dye and glucose as carbon sources can be used to improve electricity generation.15,18 Co-substrates such as glucose and sodium acetate are essential because electricigens cannot directly degrade refractory substances to generate electricity. The presence of a co-substrate facilitates electricity generation and ensures stability of the coupled system.
A high concentration of phenolic pollutants inhibits plant growth via endogenous regulation of auxin transport and enzymatic performance. It inhibits microbial activity and survival by denaturing proteins and destroying cell membranes.19,20 The growth and photosynthetic capacity of plants can affect functions such as release of oxygen, heavy metal enrichment and transfer, which affect the ability of CW–MFC to generate electricity and remove pollutants.21,22 Experiments were carried out at specific 4-CP concentrations controlling the total COD for effective removal of Cr(VI) and 4-CP and electricity generation. To ensure the stability of the system, it is necessary to reduce the levels of sodium acetate during electricity generation using CW–MFC and prevent the waste of resources when 4-CP is used as a co-substrate. Therefore, the concentration of 4-CP is one of the critical factors determining Cr(VI) and 4-CP treatment. Hydraulic retention time (HRT) affects the performance of CW and MFC. HRT affects the bacterial community at the CW–MFC anode biofilm and the contact time between microorganisms and wastewater.23 Based on previous studies, it is useful to investigate whether downflow L. hexandra-based constructed wetland-microbial fuel cell (DLCW–MFC) can be used to effectively treat polluted water containing Cr(VI) and 4-CP composites.
In present study, simultaneous Cr(VI) and 4-CP removal by DLCW–MFC was proposed using a combination of bioelectrochemical reduction, matrix adsorption, L. hexandra enrichment and microbial methods. The effect of each critical parameter including 4-CP concentration and HRT on the treatment of polluted wastewater containing Cr(VI) and 4-CP composites was analyzed to ensure electricity generation. Toward this end, we analyzed the performance of DLCW–MFC in terms of electricity generation, electrochemical changes, water quality, plant physiology and biochemical response, as well as Cr enrichment.
Fig. 1 DLCW–MFC structure diagram (S1, S2 and S3 were sample taps, and the suffix E represents effluent tap). |
A cylinder measuring 21 cm in diameter and 42 cm in height was used to construct DLCW–MFC (Fig. 1), with an effective height of 28 cm. Gravels measuring 0.3 to 0.6 cm in diameter were used as the support layer weighing 14.15 ± 0.15 kg in total. The packing height was 26 cm, which improved the distribution of wastewater and played a supporting role.25 The total effective liquid volume of the system was 2.6 ± 0.05 L. As a spacer layer with 10 mm thickness and 21 cm diameter, the glass fiber wool prevents oxygen diffusion from cathode to anode.26 Cylindrical stainless steel mesh screens (10 mesh, thickness 0.5 mm, no gravel inside the screen) measuring 3 cm in diameter and 8 cm in height were inserted into the cathode area on the left and right sides. Twenty pre-cultured L. hexandra plants were planted into the cylindrical stainless steel mesh screens.27 A closed circuit was formed by a copper wire (1 mm diameter) connected to an anode and a cathode, with a resistance of 2000 Ω.28 The liquid level was maintained at the lower surface of the cathode to form an air cathode.
Stage 1 | Stage 2 | Stage 3 | Stage 4 | Stage 5 | Stage 6 | |
---|---|---|---|---|---|---|
4-CP concentration (mg L−1) | 0 | 17.9 | 35.7 | 35.7 | 35.7 | 35.7 |
Sodium acetate concentration (mg L−1) | 384.5 | 346.1 | 307.6 | 307.6 | 307.6 | 307.6 |
HRT (d) | 1.5 | 1.5 | 1.5 | 2.5 | 4.5 | 6.5 |
The 4-CP content was determined via high performance liquid chromatography (HPLC) (LC-2030C-3DPLUS, SHIMADZU, Japan). A symmetric C-18 column (5 μm, 4.6 × 250 mm column) was used at a temperature of 30 °C. A methanol/water mixture (70:30, v/v) was used as the mobile phase. The mobile phase flow rate was 1 mL min−1 during the analysis, and the sample injection volume was 20 μL. The detection was performed at 280 nm.17 The standard sample of 2 g L−1 4-CP was filtered with 0.45 μm PVDF and PTFE filtration membranes (Tianjin Jinteng Experimental Equipment Co., LTD., China) to analyze the role of filter membrane. An appropriate filter membrane was selected to determine the 4-CP content in the effluent (S1E sample tap) of DLCW–MFC.
Electricigens can be used as biocatalysts to oxidize carbon sources and promote electricity generation. The presence of multiple grooves on the raw graphite felt surface facilitates bacterial growth and the formation of an effective electrical biofilm on the electrode surface (Fig. 3). Electrochemical performance and electricity generation were analyzed to explore the effect of different 4-CP concentrations on the bioelectric output of DLCW–MFC. CV and LSV curves (Fig. S3a and b†) indicate that low concentrations of 4-CP enhanced the current response and charge transfer capacity of the system anode, because 4-CP is an electron receptor.9 Influx of water at the cathode reduced the effect of cathode polarization. However, a high concentration of 4-CP inhibited the electron transfer capacity and current response, because the water pollutants cannot be effectively removed within the short HRT, resulting in serious toxicity. TAF curves (Fig. S3c†) show that the exchange current (i0) at stage 2 was 4.72 × 10−3 A, which was higher than at stage 1 (4.63 × 10−3 A) and stage 3 (1.21 × 10−3 A), indicating higher kinetic activity of the anode at low concentrations of 4-CP. The results of EIS (Fig. S3d†) show that the solution resistance (Rs) plus charge transfer resistance (Rp) at stage 2 was 71.3 Ω, which was lower than at stage 1 (77.8 Ω) and stage 3 (75.1 Ω). The Warburg impedance diffusion resistance (W) at stages 1, 2 and 3 was 0.48 × 10−3 Ω, 0.55 × 10−3 Ω and 0.58 × 10−3 Ω, respectively. The 4-CP may form larger ionic radii and greater steric hindrance during movement, compared with sodium acetate.41,42 The viscosity of 4-CP is higher than that of sodium acetate, which decreases the local motion and hinders ion diffusion.43 These results show that the diffusion of ions generated in the system at the electrode interface is attenuated and the charge transfer was inhibited by the increased 4-CP concentration.
As shown in Fig. 4a, the electricity generation by DLCW–MFC at stages 1 and 2 (>500 mV) was better than at stage 3. Anode electricigens can degrade organic compounds such as phenol and sodium acetate to obtain electrons,18 reaching the cathode via an external circuit to generate voltage. Under similar high current density, the anode potential at stage 2 was lower, while the cathode potential was higher (Fig. 4b), which is attributed to the oxidizing effects of Cr(VI) and 4-CP and effective utilization of electrons at the cathode, thus slowing down the cathode polarization effect. The decrease in cathode polarization improves the output power density, and the maximum output power density at stage 2 was 72.0 mW m−2 (Fig. 4c), higher than at stage 1 (64.2 mW m−2) and stage 3 (2.5 mW m−2). Miran et al. reported that an excessively high concentration of 4-CP inhibits the electricity generation of MFC.17 The system anode had a higher potential at stage 3, indicating accumulation of excessive positive charge in the anode, and the electricigens were exposed to specific toxic effects. Therefore, the difference in power density between stages 1 and 2 was mainly induced by the cathode performance, and the anode potential played a major role in power output at stage 3. At stage 3, the H2O2 content at the cathode (Fig. S4†) decreased to 4.59 mg L−1, mainly due to declining power generation capacity.44 4-CP is oxidized and degraded by H2O2 and undergoes dechlorination by accepting electrons,17,45 while Cr(VI) can be reduced by the electrons and H2O2,1,46 further indicating that the inhibition of electricity generation reduced the detoxification efficiency of the polluted water. The CE at stage 3 (Fig. 4d) was 0.14%, which was lower than at stage 1 (0.67%) and stage 2 (0.65%), indicating that the rate of utilization of organic matter by electricigens at stage 3 was low. By contrast, CE was only 0.1–0.3% in previous CW–MFC studies.30 Khan et al. reported that the presence of phenol at the cathode of double-chamber MFC enhanced electron flux and enhanced the power output; however, the output power density decreased with the increased phenol levels, thereby slowing down the overall system performance.10 This phenomenon was similar to stages 2 and 3 in this study.
Fig. 4 (a) Output voltage, (b) cathode and anode potential, (c) power density curves and (d) CE at different concentrations of 4-CP. |
To effectively recover the heavy metals from the polluted water, the L. hexandra plants were included in the cathode area of DLCW–MFC to enrich Cr.32 As shown in Fig. S5,† the total phenol content of L. hexandra leaves at stages 1, 2 and 3 was 2.77, 3.20 and 2.22 mg g−1, respectively. Generally, the antioxidant activity of plants is positively correlated with the total phenol content in vivo.47 Total phenols can inhibit the conversion of hydrogen peroxide to reactive oxygen species and promote defense mechanisms to resist toxicity.48 Compared with stages 1 and 3 (Fig. S6†), stage 2 showed improvement in plant height, root length, and dry weight of each tissue of L. hexandra, indicating that low phenolic concentrations promoted plant growth. This result was similar to the growth reported by Ibáñez et al.39 With the increase of 4-CP concentration, the toxic effect generated a large number of reactive oxygen species (ROS), which triggered oxidative damage of plants and damaged protein and chlorophyll structure and function.49 The levels of chlorophyll a, chlorophyll b and carotenoids at stage 3 decreased by 39.8%, 57.4% and 14.3%, respectively, compared with those at stage 2. Toxic effects reduce the levels of chlorophyll a, chlorophyll b and carotenoids,50 thereby inhibiting plant photosynthesis and growth.
The Cr concentrations in roots, stems and leaves of L. hexandra at stage 2 were 11401, 2915 and 434 mg kg−1, respectively (Fig. 5a), higher than at stage 1 at 10214, 2717 and 454 mg kg−1, respectively and at stage 3 at 11343, 2960 and 408 mg kg−1, respectively. These results were higher than those reported previously including an underground Cr concentration of 785 mg kg−1 and an aboveground level of 297 mg kg−1.7 This result was mainly attributed to the positive Cr(III) absorption of L. hexandra.32 Cr(VI) can be converted to Cr(III) via H2O2, electron capture and microbial mechanisms, which accumulate large amounts of Cr in L. hexandra. The Cr content of L. hexandra at stages 1, 2 and 3 was 13.95, 17.66 and 11.61 mg/10 plants, respectively (Fig. 5b). Accordingly, the contribution to Cr(VI) removal of L. hexandra decreased in the following order: stage 2 (3.40%) > stage 1 (2.68%) > stage 3 (2.23%). This is attributed to variation in plant growth status, which resulted in different detoxification outcomes and varying levels of electricity generation.22 This study further contributes to the practical applications of CW–MFC to treat different types of polluted industrial wastewater. Considering the decline in output voltage to 90–110 mV at stage 3 and the stability, the rate of 4-CP removal at stage 3 was comparable to that at stage 2, which indicates that the presence of electricigens in the system and their tolerance to the influx of synthetic solution containing 35.7 mg L−1 4-CP. Therefore, 35.7 mg L−1 4-CP was selected for subsequent experiments.
Fig. 5 (a) Cr concentrations in roots, stems and leaves and TF and (b) Cr content in aboveground and underground parts of L. hexandra at different concentrations of 4-CP. |
The effect of different HRT levels on biological electricity generation of DLCW–MFC was explored by analyzing the electrochemical performance and electricity generation. Based on CV and LSV curves (Fig. S8a and b†), the current response and charge transfer capability of the anode increased with the increase in HRT, mainly due to the prevention of excessive influx of toxic substances into the anode. TAF curves (Fig. S8c†) show that i0 at stages 4, 5 and 6 was 4.34 × 10−3 A, 4.99 × 10−3 A and 4.99 × 10−3 A, respectively, indicating that prolonged HRT improved the anode kinetic activity. Studies have shown that the increased HRT can reduce the toxic effects on microorganisms and improve electricity generation by the system.52 EIS (Fig. S8d†) results indicate that the Rs plus Rp at stage 6 was 71.3 Ω, which was lower than at stages 3–5. The value of W at stages 4, 5 and 6 was 0.39 × 10−3 Ω, 0.39 × 10−3 Ω and 0.41 × 10−3 Ω, respectively, which were lower than at stage 3 (0.58 × 10−3 Ω), mainly due to the effective removal of 4-CP. These results indicate that prolonged HRT increases the diffusion of ions generated in the system to the electrode interface and improve the charge transferability.
Fig. 7a shows that the output voltage was recovered and exceeded 500 mV at stage 4. Under the same high current density, prolonged HRT can reduce the anode potential (Fig. 7b) to increase the potential difference between anode and cathode, and improve the output power density. When the HRT was increased from 2.5 to 4.5 d, the maximum power density increased to 10.0% (Fig. 7c). However, when the HRT increased from 4.5 to 6.5 days, the maximum power density only increased by 1.8% to 72.25 mW m−2. Studies have shown that increased HRT can increase the utilization of the available organic matter by microbes,23 thus promoting their growth and reproduction and improving the abundance of electricigens. The increased activity of electricigens generates electrons and improves electron transport capacity, thereby reducing internal resistance and enhancing power density.53 At stage 4, the H2O2 content at the cathode (Fig. S9†) increased to 5.54 mg L−1, mainly due to improved electricity generation. Yong et al. reported that only 4.6 mg L−1 of H2O2 was released at the cathode of MFC.54 The H2O2 content at cathode at stages 5 and 6 was 3.00 mg L−1 and 2.71 mg L−1, respectively, mainly due to the increased HRT, which was conducive to the removal of 4-CP and Cr(VI) by H2O2. Thus, a large amount of H2O2 is consumed under conditions of limited dissolved oxygen. The CE (Fig. 7d) at stages 4, 5 and 6 was 1.06%, 1.71% and 2.38%, respectively, further indicating that increased HRT can promote effective utilization of organic matter by electricigens. The CE of this study was substantially larger than in previous studies (0.1–0.3%).30 Excessive increase in HRT affects plant growth and electron donor supply due to the consumption of available carbon sources. Therefore, an HRT of 6.5 d was expected to improve the treatment performance and electricity generation by DLCW–MFC exposed to Cr(VI) and 4-CP composite polluted wastewater.
Fig. 7 (a) Output voltage, (b) cathode and anode potential, (c) power density curves and (d) CE at different HRT. |
The total phenol content at stages 4, 5 and 6 was 8.04, 8.59 and 8.87 mg g−1, respectively (Fig. S10†), indicating that increased HRT improved the total phenol content alleviate stress. Plant height, root length, tissue dry weight and chlorophyll and carotenoid contents were increased at stages 4, 5 and 6, compared with stage 3 (Fig. S11†). Thus, prolonged HRT facilitated the removal of Cr(VI) and 4-CP to alleviate the toxic effects on plants. Studies reported that increased HRT contributes to plant growth and improves their ability to eliminate pollutants, due to slow biodegradation.55,56 With the increase of HRT, the Cr concentrations in the roots, stems and leaves were decreased (Fig. 8a). When HRT increased to 6.5 d, the Cr concentrations in the roots, stems and leaves were 3279, 1290 and 171 mg kg−1, respectively. The TF of L. hexandra at stages 4, 5 and 6 was 0.382, 0.418 and 0.451, respectively, higher than at stage 3 (0.298), and higher than those reported previously (0.1–0.3).7 The results show a decrease in Cr concentration of each tissue of L. hexandra, while the transport capacity improved with increased HRT. The accumulated Cr content of L. hexandra at stages 4, 5 and 6 was 8.14, 5.02 and 4.56 mg/10 plant, respectively (Fig. 8b). The contribution to Cr(VI) removal of L. hexandra was in the following order: stage 4 (2.61%) < stage 5 (2.90%) < stage 6 (3.80%). This is because different HRTs under the limited experimental period led to variation in the total volume of influent synthetic solution. This study further enhances the role of plants in the recovery of heavy metals, wastewater treatment and available carbon source utilization in DLCW–MFC. Considering that the system had the highest output power density and exhibited excellent treatment performance in eliminating Cr(VI) and 4-CP at stage 6, the growth state of L. hexandra at stage 6 decreased slightly compared with stage 5. Therefore, an HRT of 6.5 d was considered as the most appropriate for optimal performance.
Fig. 8 (a) Cr concentrations in roots, stems and leaves and TF and (b) Cr content in aboveground and underground parts of L. hexandra at different HRT. |
HRT (d) | Substrate | Influent COD (mg L−1) | Refractory organics or heavy metals | Voltage (mV) | Power density (mW m−2) | Removal rate | Ref. |
---|---|---|---|---|---|---|---|
2.5 | Sodium acetate | 300 | 35.7 mg L−1 4-CP and 40 mg L−1 Cr(VI) | 516 | 64.6 | 4-CP: 42.1% | Present study |
Cr(VI): 98.5% | |||||||
6.5 | 543 | 72.25 | 4-CP: 78.6% | ||||
Cr(VI): 99.0% | |||||||
4 | Glucose | 500 | 60 mg L−1 Cr(VI) | 545.6 | 29.8 | Cr(VI): 89.6% | 52 |
0.625 | Sodium acetate | 880 | — | 27–42 | 2.016 | — | 58 |
3 | — | — | 10 mg L−1 Zn(II) | 257 | 3.87 | Zn(II): 98.56% | 59 |
3 | Glucose | 60 | 5 mg L−1 Pb(II) | 343 | 7.432 | Pb(II): 84.86% | 57 |
7.6 | Glucose | 262 | — | — | 2–3 | — | 60 |
3 | Glucose | — | 300 mg L−1 azo dye ABRX3 | 342 | 11.8 | ABRX3: 91.05% | 14 |
3 | Glucose | 426.8 | 4 mg L−1 sulfadiazine | 472 | 15.41 | Sulfadiazine: 99.9% | 61 |
0.67 | Glucose | 426.8 | 10 mg L−1 bisphenol A | 420 | 18.43 | Bisphenol A: 91.3% | 62 |
However, there are two noteworthy limitations: (1) This study did not explore other important factors such as pH or electrode spacing; (2) the role of root exudate of L. hexandra in DLCW–MFC remains to be clarified due to secretions that help bacterial growth.
Footnote |
† Electronic supplementary information (ESI) available. See https://doi.org/10.1039/d2ra01828d |
This journal is © The Royal Society of Chemistry 2022 |