A method, system and application for treating antibiotic-containing wastewater

Abstract

This invention discloses a method, system, and application for treating antibiotic-containing wastewater. The treatment method includes the following steps: inoculating sludge into a wastewater treatment reactor, then introducing wastewater for treatment; adding N-acylhomoserine lactone during the 149th-212th day of wastewater treatment; the N-acylhomoserine lactone includes C6-HSL and C12-HSL; the concentration of the N-acylhomoserine lactone in the system is 1-2.8 μM. This invention's method for treating antibiotic-containing wastewater, by adding N-acylhomoserine lactone during the wastewater treatment stage, effectively improves the antibiotic degradation rate, methane production, and QS-related gene abundance during the wastewater treatment stage, and can be effectively used to treat antibiotic-containing wastewater.

Description

Technical Field

[0001] This invention belongs to the field of wastewater treatment, specifically relating to a method, system, and application for treating antibiotic-containing wastewater. Background Technology

[0002] The global spread of antibiotic resistance (AMR) has become one of the most serious public health challenges of the 21st century. The environment is a significant medium for the spread of antibiotics and antibiotic resistance genes (ARGs), especially in the discharge of pharmaceutical wastewater, hospital wastewater, and livestock and poultry wastewater, where antibiotics often enter water and soil systems in high concentrations, either continuously or intermittently. This type of pollution not only directly threatens the ecological functions of aquatic bodies but may also accelerate the spread of resistant strains and genes through the drug-resistant selection effect of environmental microbial communities, thus posing a serious risk to human health. Therefore, developing efficient and sustainable water treatment technologies to achieve efficient removal of antibiotics and effective suppression of resistance transmission has become a core issue that urgently needs to be addressed in the fields of environmental science and environmental engineering.

[0003] Sulfamethoxazole (SMX), a typical recalcitrant antibiotic, is difficult to remove effectively in traditional sludge treatment processes such as anaerobic digestion. Microbial electrolysis cell coupled anaerobic digestion (MEC-AD) systems, by applying a small external voltage to an anaerobic system, enrich electroactive microorganisms (EAMs) and promote extracellular electron transfer (EET), significantly improving the degradation efficiency of organic pollutants and methanogenesis. However, when treating wastewater with high concentrations of SMX, the MEC-AD system still faces challenges such as decreased SMX removal efficiency and reduced methane production. Summary of the Invention

[0004] The present invention aims to solve at least one of the technical problems existing in the prior art. To this end, the present invention proposes a method for treating antibiotic-containing wastewater.

[0005] The present invention also proposes a system for treating wastewater containing antibiotics.

[0006] The present invention also proposes applications of the above-mentioned processing methods and systems.

[0007] According to a first aspect of the present invention, a method for treating antibiotic-containing wastewater is provided, comprising the following steps: inoculating sludge into a wastewater treatment reactor, then introducing wastewater for wastewater treatment; adding N-acylhomoserine lactone during the 149th-212th day of wastewater treatment; wherein the N-acylhomoserine lactone comprises C6-HSL and C12-HSL; and wherein the concentration of the N-acylhomoserine lactone in the system is 1-2.8 μM.

[0008] In some embodiments of the present invention, the inoculation amount of the sludge is 85-100 g / L.

[0009] In some embodiments of the present invention, the inoculum amount of sludge is 88-95 g / L. Specifically, it can be 88, 89, 90, 91, 92, 93, 94, or 95 g / L.

[0010] In some embodiments of the present invention, the inoculum amount of sludge inoculated into each compartment of the wastewater treatment reactor is 15-22 g / L. Specifically, it can be 15, 16, 17, 18, 19, 20, 21, or 22 g / L.

[0011] In some embodiments of the present invention, after the sludge is inoculated into the wastewater treatment reactor, the hydraulic retention time of the wastewater is set to 22-28 hours. Specifically, it can be 22, 23, 24, 25, 26, 27, or 28 hours.

[0012] In some embodiments of the present invention, the wastewater treatment reactor is made of glass.

[0013] In some embodiments of the present invention, the volume of the wastewater treatment reactor is 2-4L. Specifically, it can be 2, 2.8, 3, or 4L.

[0014] In some embodiments of the invention, the wastewater treatment reactor includes five compartments, wherein the first three compartments have external electrodes.

[0015] In some embodiments of the present invention, the external electrode is connected to a voltage of 0.5-1.5V via a titanium wire (1mm). Specifically, the voltage can be 0.5, 0.6, 0.7, 0.8, 0.9, 1, 1.1, 1.2, 1.3, 1.4, or 1.5V.

[0016] In some embodiments of the present invention, the volume of the compartment is 0.4-0.7L. Specifically, it can be 0.4, 0.5, 0.56, 0.6, or 0.7L.

[0017] In some embodiments of the present invention, the electrode material of the wastewater treatment reactor is carbon felt.

[0018] In some embodiments of the present invention, the carbon felt is soaked in a mixed solution of concentrated sulfuric acid and concentrated nitric acid with a volume ratio of (2-4):1 for 11-13 hours before use to remove surface impurities and enhance its hydrophilicity.

[0019] In some embodiments of the present invention, a double-valve gas bag is connected above the compartment to collect the generated gas.

[0020] In some embodiments of the present invention, the external voltage of the wastewater treatment reactor is 0.5-1.5V. Specifically, it can be 0.5, 0.6, 0.7, 0.8, 0.9, 1, 1.1, 1.2, 1.3, 1.4, or 1.5V.

[0021] In some embodiments of the present invention, the wastewater treatment reactor includes an ABR (anaerobic baffled reactor).

[0022] In some embodiments of the present invention, the wastewater includes wastewater containing antibiotics.

[0023] In some embodiments of the present invention, the antibiotics include sulfonamide antibiotics.

[0024] In some embodiments of the present invention, the sulfonamide antibiotics include at least one of sulfamethoxazole, sulfadiazine, sulfadimidine, sulfamethoxypyrimidine, and sulfathiazole.

[0025] In some embodiments of the present invention, the concentration of antibiotics in the wastewater is 0~50 mg / L.

[0026] In some embodiments of the present invention, the COD of the wastewater is 350-2000 mg / L.

[0027] In some embodiments of the present invention, the pH of the wastewater is 7.3 ± 0.2.

[0028] In some embodiments of the present invention, the wastewater treatment includes four stages: the first stage is the start-up period and sludge acclimatization period of the wastewater treatment reactor; the second stage is the SMX shock period; the third stage is the MEC coupling stage; and the fourth stage is the wastewater treatment enhancement stage by adding N-acylhomoserine lactone during the 149th to 212th day of wastewater treatment.

[0029] In some embodiments of the present invention, the first stage lasts for days 1 to 44 of wastewater treatment.

[0030] In some embodiments of the present invention, the second stage takes place from day 45 to day 92 of wastewater treatment.

[0031] In some embodiments of the present invention, the third stage is therefore scheduled for days 93 to 148 of wastewater treatment.

[0032] In some embodiments of the present invention, the wastewater treated in the second to fourth stages is wastewater containing antibiotics.

[0033] In some embodiments of the present invention, the electrodes are energized in the third stage to perform MEC coupling.

[0034] In some embodiments of the present invention, the treatment method further includes the step of adding a carbon source, a nitrogen source, a phosphorus source, a trace element solution, and vitamins to the wastewater treatment reactor.

[0035] In some embodiments of the present invention, the carbon source, nitrogen source and phosphorus source are added in a ratio of C:N:P = (190-210):(4-6):(0.5-2).

[0036] In some embodiments of the present invention, the trace element solution includes H3BO3, CuCl·2H2O, MnSO4·H2O, CoCl2·6H2O, concentrated HCl, NiCl2, ZnCl2, and (NH4)Mo7O. 24 A solution of at least one of ·4H2O, AlCl3·6H2O and FeCl2·4H2O.

[0037] In some embodiments of the present invention, the trace element solution comprises H3BO3 at a concentration of 0.03-0.06 g / L, CuCl·2H2O at a concentration of 0.02-0.04 g / L, MnSO4·H2O at a concentration of 0.03-0.06 g / L, CoCl2·6H2O at a concentration of 0.1-0.3 g / L, concentrated HCl at a concentration of 0.5-2 mL / L, NiCl2 at a concentration of 0.1-0.3 g / L, ZnCl2 at a concentration of 0.03-0.06 g / L, and (NH4)Mo7O at a concentration of 0.03-0.06 g / L. 24 A solution of at least one of the following: AlCl3·6H2O with a concentration of 0.03-0.06 g / L and FeCl2·4H2O with a concentration of 1-3 g / L.

[0038] In some embodiments of the present invention, the solvent of the solution includes water.

[0039] In some embodiments of the present invention, the vitamins include vitamin B1, vitamin B2, vitamin B3, vitamin B5, vitamin B6, vitamin B9, vitamin B12, vitamin H, para-aminobenzoic acid, and lipoic acid.

[0040] In some embodiments of the present invention, the molar ratio of the added C6-HSL and the added C12-HSL is (1-2):(1-2).

[0041] In some embodiments of the present invention, the concentration of the N-acylhomoserine lactone in the system is 1, 1.5, 2.5, 2.8 μM or any two of these values ​​as any intermediate value of the endpoint values.

[0042] According to a second aspect of the present invention, a system for treating antibiotic-containing wastewater is provided, the system comprising, in sequence, a feed tank, a feed pump, an anaerobic baffle reactor, a hydrothermal circulation pump, an effluent tank, and a power source.

[0043] In some embodiments of the present invention, the system further includes a dual-valve air bag.

[0044] According to a third aspect of the present invention, the application of the above-described treatment method and system in wastewater treatment is proposed.

[0045] In some embodiments of the present invention, the wastewater includes wastewater containing antibiotics.

[0046] In some embodiments of the present invention, the antibiotics include sulfonamide antibiotics.

[0047] In some embodiments of the present invention, the sulfonamide antibiotics include at least one of sulfamethoxazole, sulfadiazine, sulfadimidine, sulfamethoxypyrimidine, and sulfathiazole.

[0048] In some embodiments of the present invention, the wastewater treatment includes removing at least one of antibiotics and COD from the wastewater.

[0049] According to some embodiments of the present invention, at least the following beneficial effects are achieved: The method for treating antibiotic-containing wastewater according to the present invention is based on a MEC-ABR coupled system. By adding N-acylhomoserine lactone during the wastewater treatment stage, the degradation rate of antibiotics, methane production, and QS-related gene abundance during the wastewater treatment stage are effectively improved, while simultaneously enhancing the system's... Bacillota Alternative Chloroflexota Becoming the dominant bacterium gives the system a stronger acid-producing capacity and a faster substrate transformation rate, while also providing a breeding ground for acetic acid-producing methanogenic archaea. Methanothrix and Methanosarcina It provides a favorable metabolic environment and can be effectively used to treat wastewater containing antibiotics. Attached Figure Description

[0050] The present invention will be further described below with reference to the accompanying drawings and embodiments, wherein: Figure 1This is a schematic diagram of the device in Embodiment 1 of the present invention, wherein ① is a feed tank; ② is a feed pump; ③ is an anaerobic baffle reactor; ④ is a hydrothermal circulation pump; ⑤ is an outlet tank; and ⑥ is a power source. Figure 2 The graph shows the concentration change of sulfamethoxazole in Example 1 of the present invention, where C1, C2, C3, C4, and C5 are compartments. Figure 3 The diagram shows the relative abundance detection results of ARGs in each compartment in Embodiment 1 of the present invention. C1, C2, C3, C4, and C5 are compartments, and A and B represent AHLs before (A) and after (B) addition, respectively. Figure 4 The graph shows the methane production detection results of each compartment at each stage in Example 1 of the present invention, where C1, C2, C3, C4, and C5 are compartments. Figure 5 The graph shows the detection results of COD, pH and ORP changes at each stage in Example 1 of the present invention, where C1, C2, C3, C4 and C5 are compartments; Figure 6 The diagram shows the EPS composition of suspended sludge in each compartment in Embodiment 1 of the present invention, where C1, C2, C3, C4, and C5 are compartments, and A and B represent AHLs before and after their addition, respectively. Figure 7 This is a PCA analysis diagram from Embodiment 1 of the present invention; Figure 8 The image shows the results of sludge level abundance detection in Embodiment 1 of the present invention, where C1, C2, C3, and C4 are compartments, and A and B represent AHLs before and after addition, respectively. Figure 9 The graph shows the results of the level abundance detection of sludge in Example 1 of the present invention, where C1, C2, C3, and C4 are compartments, and A and B represent AHLs before and after their addition, respectively. Figure 10 The graph shows the results of the level abundance detection of sludge in Example 1 of the present invention, where C1, C2, C3, and C4 are compartments, and A and B represent AHLs before and after their addition, respectively. Figure 11 This is a graph showing the abundance detection results of anodic microorganisms at the phylum level in Example 1 of the present invention; Figure 12 This is a graph showing the abundance detection results of anodic microbial genus levels in Example 1 of the present invention; Figure 13 This is a heatmap of KEGG level 2 abundance in Embodiment 1 of the present invention, where C1, C2, C3, and C4 are compartments, and A and B represent AHLs before and after their addition, respectively. Figure 14This is a heatmap of QS-related gene abundance in Example 1 of the present invention, where C1, C2, C3, and C4 are compartments, and A and B represent AHLs before and after their addition, respectively. Figure 15 This is a heatmap of enzyme abundance related to the methanogenesis process in Example 1 of the present invention, where C1, C2, C3, and C4 are compartments, and A and B represent AHLs before and after their addition, respectively. Figure 16 This is a graph showing the detection results of Pearson correlation analysis between the QS-related gene and the key enzyme gene for methane production in Example 1 of the present invention. Detailed Implementation

[0051] The following will describe the concept and technical effects of the present invention clearly and completely with reference to embodiments, so as to fully understand the purpose, features and effects of the present invention. Obviously, the described embodiments are only some embodiments of the present invention, not all embodiments. Other embodiments obtained by those skilled in the art based on the embodiments of the present invention without creative effort are all within the scope of protection of the present invention.

[0052] Unless otherwise specified in the examples, the procedures should be performed under standard conditions or conditions recommended by the manufacturer. Reagents or instruments whose manufacturers are not specified are all commercially available products.

[0053] When a numerical range is disclosed herein, the range is considered continuous and includes the minimum and maximum values ​​of the range, as well as every value between the minimum and maximum values. Furthermore, when the range refers to integers, it includes every integer between the minimum and maximum values ​​of the range. Additionally, when multiple ranges are provided to describe a feature or characteristic, the ranges may be combined. In other words, unless otherwise specified, all ranges disclosed herein should be understood to include any and all subranges to which they are incorporated.

[0054] "And / or" is used to indicate that one or both of the described situations may occur, for example, A and / or B includes (A and B) and (A or B).

[0055] Experimental setup: The continuous flow experiment used an anaerobic baffled reactor (ABR) as the basic device, and its structure and process are as follows: Figure 1As shown. The anaerobic baffle reactor is made of plexiglass, with an overall effective volume of 2.80 L and an effective volume of 0.56 L for each individual compartment (C1, C2, C3, C4, C5). Carbon felt was used as the electrode material, and before use, the raw carbon felt was soaked in a 3:1 (volume ratio) mixed solution of concentrated sulfuric acid and concentrated nitric acid for 12 h to remove surface impurities and enhance its hydrophilicity. Anode and cathode electrodes were added to the first three compartments, connected to an external 0.8V voltage via 1mm titanium wire. A 2L double-valve gas bag was connected above each compartment to collect the generated gas. Wastewater was stored in a 10 L feed tank, with the influent controlled by a peristaltic pump and a hydraulic retention time set to 24 h.

[0056] Example 1 This embodiment provides a method for treating antibiotic-containing wastewater, the method comprising the following steps: After the ABR was inoculated with initial sludge (the sludge inoculation amount for all 5 compartments was VSS=18.63g / L), the hydraulic retention time was set to 24h, and carbon felt electrodes were added to the first three compartments and connected to an external voltage of 0.8V.

[0057] Phase I (days 1-44) is the start-up and sludge acclimatization period of the ABR; Phase II (days 45-92) is the SMX shock phase; Phase III (days 93-148) is the MEC (microbial electrolyzer) coupling phase, with electrodes added and the voltage gradually increased to 0.8V; Phase IV (days 149-212) is the AHLs enhancement phase, where mixed chain length AHLs (final concentration of 2.5μM C6-HSL and 2.5μM C12-HSL) are added to the system, specifically by adding the mixed chain length AHLs to the influent and introducing them into the system via a peristaltic pump; the system operating parameters for Phases I-IV are shown in Table 1, with C6H... 12 O6 and CH3COONa are used as mixed carbon sources, and NH4Cl and KH2PO4 are used as nitrogen and phosphorus sources, respectively, and are added in a ratio of C:N:P = 200:5:1. In addition, appropriate amounts of trace element solution and vitamin solution are added to the water to meet the needs of microbial growth. 10 mL of trace element solution and 10 mL of vitamin solution are added per liter of influent. The specific formulas are shown in Tables 2 and 3.

[0058] Table 1 System Operating Parameters

[0059] Table 2. Composition of Trace Element Solution

[0060] Table 3 Vitamin Liquid Ingredients

[0061] Detection methods for each indicator: (1) pH pH was measured using a Sartorius PB-10 pH meter.

[0062] (2) Oxidation-reduction potential (ORP) The ORP meter, model PHS-3E, was used for measurement.

[0063] (3) COD COD was measured using a rapid COD analyzer (Lianhua Technology).

[0064] (4) SMX and its degradation products SMX was determined using a high-performance liquid chromatograph (1260 Infinity II, Agilent Technologies, USA). Methanol and 1 / 1000 acetic acid aqueous solution were used as the mobile phase. The column was C18, the detection wavelength was set to 294 nm, and the monitoring time was 5.5 min. The sample was first centrifuged at 8000 rpm for 10 min, and then filtered through a 0.22 µm aqueous filter membrane.

[0065] After the experiment, water samples were taken and the intermediate degradation products of SMX were detected using high performance liquid chromatography-mass spectrometry (Thermo Ultmate 3000 UHPLC-QExactive MS).

[0066] (5) Methane production Biogas yield was determined using the syringe extraction method (sequential batch assay) and the water displacement gas collection method (continuous flow assay). Methane purity was determined using a gas chromatograph (8890, Agilent Technologies, USA). Manual injection mode was used. The capillary column was an HP-5 model, and the FID detector, column oven, and injection port temperatures were 110℃, 80℃, and 200℃, respectively. The detection time was 3 min.

[0067] (6) Extraction and determination of EPS The extraction of EPS from sludge followed these steps: 3 mL of sludge sample was placed in a 5 mL centrifuge tube and centrifuged at 4000 rpm for 8 min. The supernatant was S-PBS. Then, 3 mL of 0.05% NaCl solution at 70°C was added for resuspending. The mixture was then shaken at 150 rpm for 10 min and centrifuged at 4000 rpm. The supernatant was LB-PBS. Next, 3 mL of 0.05% NaCl solution was added, and the mixture was heated in a 60°C water bath for 40 min, cooled in water for 2 min, and then centrifuged at 4000 rpm for 20 min. The supernatant was TB-EPS.

[0068] The extracted EPS was filtered through a 0.45µm PES membrane. Protein content was determined using a BCA method microprotein concentration assay kit (Sangon Biotech, Shanghai), with bovine serum albumin as the standard. Polysaccharide content was determined using a modified phenol-sulfuric acid method, with glucose (dried at 105℃ to constant weight) as the standard. The luminescent substances in the appropriately diluted EPS solution were determined using a fluorescence spectrophotometer.

[0069] (7) EAB analysis method To observe the adhesion of EAMs on the MEC-AD anode, the electrode was treated as follows: First, the sample surface was gently rinsed with 1×PBS (pH 7.2) to remove loosely attached microorganisms and wastewater residue; this process was repeated three times. Then, the sample was fixed by immersing it in a 2.5% glutaraldehyde solution and placed in a 4°C freezer for 8 hours. After fixation, the sample was rinsed three times with 1×PBS (pH 7.2) for 10 minutes each time to thoroughly remove any glutaraldehyde residue. Next, dehydration was performed using a gradient of ethanol concentrations, followed by immersion in anhydrous ethanol 2-3 times to completely displace the water. The sample was then dried using a vacuum freeze dryer to completely remove moisture. The treated sample was then sputter-coated with gold and scanned using a scanning electron microscope.

[0070] To further analyze the electrochemical performance, cyclic voltammetry (CV) was performed on the anode in the system using an electrochemical workstation (Chenhua, China). The carbon felt anode was used as the working electrode, an Ag / AgCl electrode filled with saturated potassium chloride solution (197 mV vs. SHE) was used as the reference electrode, and the carbon felt cathode was used as the counter electrode. The scan rate was set to 10 mV / s, and the scan range was set to... The voltage was set at 0.8–0.2 V, and three scans were performed. A 50 mM PBS solution (pH 7.4) was used as the electrolyte, and high-purity nitrogen gas was purged for 60 min beforehand to remove dissolved oxygen. During the scans, high-purity nitrogen gas was continuously purged into the headspace of the electrochemical cell to prevent dissolved oxygen from interfering with the results.

[0071] (8) Metagenomic sequencing Sample collection and DNA extraction were performed according to section 2.2.4. Raw sequencing data were first processed using FASTP software for quality control. The main procedures included: removing adapters at the 3' and 5' ends of the sequences, and discarding sequences shorter than 50 bp, with an average quality score below 20, or containing ambiguous N bases, ultimately obtaining high-quality paired-end and single-end sequences suitable for subsequent analysis. Based on this, BWA software was used to align clean reads with the host genome to remove sequences that might be contaminated by the host.

[0072] Based on the quality-controlled sequences, Megahit software was used for assembly, and contigs longer than 300 bp were selected as the basis for subsequent analysis. MetaGene was used to predict open reading frames from the assembled results, and genes with nucleic acid lengths greater than 100 bp were translated into amino acid sequences to complete gene prediction for each sample. Subsequently, CD-HIT software was used to cluster the predicted genes, setting similarity of 95% and coverage of 90% as thresholds. The longest sequence in each cluster was selected to construct a non-redundant gene set. Gene abundance calculation was performed by aligning high-quality sequences from each sample to this gene set (with a similarity threshold of 95%) using SOAPaligner.

[0073] Bioinformatics analysis comprises two parts: species annotation and functional annotation. Species annotation uses BLASTP to align the non-redundant gene set with the NR database (e-value ≤ 10). -5 Based on the classification information in the database, the species affiliation of each sequence was determined, and the relative abundance of different species was calculated. For functional annotation, BLASTP was used to align the gene set sequences to the EggNOG database (version 4.5) and the KEGG gene database (e-value ≤ 10). -5 The former is used to obtain COG functional classification and abundance information, while the latter provides basic data support for subsequent metabolic pathway analysis.

[0074] Experimental results: 1. The effect of mixed chain lengths (AHLs) on SMX and ARGs SMX concentration changes as follows Figure 2 As shown in the figure, after 212 days of system operation, at the end of Phase II, the SMX removal rates of each compartment (C1, C2, C3, C4, and C5) were only 22.28%, 27.76%, 28.54%, 31.32%, and 30.78%, respectively. At the end of Phase III, the SMX removal rates of the compartments were only 49.42%, 53.94%, 53.8%, 57.42%, and 56.48%, respectively. At the end of the experiment, the SMX removal rates of each compartment increased to 71.96%, 74.4%, 74.08%, 75.72%, and 78.56%, respectively.

[0075] Related studies have shown that adding the AHL-like signaling molecule 3OC8-HSL to a dual-chamber microbial fuel cell system significantly improves the degradation efficiency of chloramphenicol, while also significantly increasing the system power density. This is presumably related to AHLs promoting EAM enrichment, enhancing EAB activity, and strengthening EET. Other studies have indicated that AHLs can promote EPS secretion, thereby enhancing the microorganisms' tolerance to antibiotic toxicity. Simultaneously, the SMX removal rate gradually increases along the reactor flow direction, indicating that each compartment plays a synergistic role in the stepwise degradation of pollutants. Therefore, the significant improvement in SMX removal rate in this study is likely closely related to AHLs promoting EAM enrichment and improving EET efficiency.

[0076] from Figure 3 As can be seen, the addition of exogenous AHLs promoted the enrichment of ARGs to some extent. Spatially, the relative abundance of ARGs in compartment C1 was significantly higher than in subsequent compartments. This phenomenon may be related to the enrichment of potential ARG host bacteria in the front compartment. Community structure analysis results showed that after the addition of AHLs, the abundance of ARGs in compartment C1... Bacteroidota and Bacillota A distinct enrichment was observed that differed from that in subsequent compartments, and these microorganisms are typically considered to possess sulfonamide resistance genes (such as...). sul1 and sul2 These bacteria are important potential hosts for ARGs. Therefore, the enrichment of these bacteria in the C1 compartment may have contributed to the increased abundance of ARGs.

[0077] 2. Impact of mixed chain length AHLs on system performance Statistical analysis was performed on the average methane yield of each compartment in each stage of the reactor. The statistical analysis chart is shown below. Figure 4 As shown in the figure, methane production exhibits obvious phased changes at different operating stages, and shows a gradually decreasing spatial distribution characteristic along the reactor flow direction.

[0078] During the start-up phase (Phase I), the system was in the initial stage of stable operation, with average methane yields in compartments C1 through C5 of 112, 105, 94, 73, and 65 mL / g CODremoved, respectively. Upon entering the SMX impact phase (Phase II), the methane yields in each compartment decreased to varying degrees due to SMX addition. Specifically, C1 decreased from 112 mL / g CODremoved to 73 mL / g CODremoved, indicating that the addition of SMX significantly inhibited methanogenesis. During the MEC coupling phase (Phase III), the methane yields in each compartment rebounded significantly. C1 and C2 increased to 158 and 142 mL / g CODremoved, respectively, representing increases of approximately 116% and 145% compared to Phase II, indicating that the introduction of external voltage effectively mitigated the inhibition of methanogenesis by SMX.

[0079] With the introduction of AHLs (Stage IV), methane production in each compartment reached its highest level throughout the entire operation. Methane production from C1 to C5 was 121.20, 147.20, 117.50, 73.10, and 56.50 mL / g CODremoved, respectively, indicating improved reactor methane production performance under the regulation of AHLs. These figures represent increases of 28.48, 38.03, 31.5, 28.43, and 47.43% compared to the previous stage.

[0080] At the end of Phase IV, the COD removal efficiencies of each compartment reached 74.74%, 76.99%, 78.88%, 80.12%, and 80.4%, respectively. Figure 5 Compared with the end of Phase 3, the improvement in COD removal efficiency of each compartment showed a decreasing trend from the front end to the back end: C1 increased by 31.95%, C2 by 25.10%, C3 by 19.35%, C4 by 15.38%, and C5 by 13.40%.

[0081] In Stage II, under continuous SMX stress, the metabolic activity of microorganisms in the ABR-MEC system was significantly inhibited, leading to a decrease in COD degradation efficiency and a significant reduction in methane production. As SMX concentration increased, the system pH continuously decreased, reaching a minimum below 5. This is because methanogenic archaea are more sensitive to adverse conditions such as antibiotics, and their metabolic activity is significantly inhibited. Organic matter, after being decomposed by hydrolytic acidifying bacteria, produces volatile fatty acids that cannot be promptly converted into methane by methanogenic archaea, leading to the continuous accumulation of organic acids in the system and thus system acidification. The optimal pH range for methanogenic archaea is typically between 6.5 and 8.5; the continuous decrease in pH, in turn, further inhibits the activity of methanogenic archaea, creating a vicious cycle and ultimately causing metabolic imbalance in the system. The higher methanogenesis in compartment C4 compared to compartment C3 in Stage II may also be based on the fact that as metabolism occurs in each compartment, the SMX concentration decreases, and the lower SMX concentration in compartment C4 reduces the inhibitory effect on methanogenic archaea; the higher pH also favors methanogenesis.

[0082] 3. The impact of mixed chain lengths (AHLs) on the composition and structure of EPS EPS (extracellular polymeric substances) are highly hydrated three-dimensional polymer networks secreted by microorganisms and encapsulated on the cell surface, mainly composed of PS (polysaccharide), PN (phosphoric acid), humic acid, and lipids. EPS acts as the first line of defense, mitigating the direct damage of high-concentration antibiotics to microorganisms through adsorption and spatial barrier. Therefore, the secretion level of EPS is often considered an important indicator reflecting the metabolic activity and environmental adaptability of microorganisms.

[0083] Figure 6 The composition of PN and PS in the three layers of granular sludge EPS (S-EPS, LB-EPS and TB-EPS) in each compartment of the ABR-MEC reactor after the addition of mixed chain length AHLs is shown.

[0084] Firstly, the changes in the total concentrations of PN and PS in EPS were analyzed. Compared with before the addition of AHLs (A), the total amount of EPS in each compartment was significantly increased after enhancement (B). The total amount of EPS in compartments C1, C2, C3, C4, and C5 increased by 40.24, 38.64, 36.98, 36.25, and 36.2%, respectively. This result indicates that the addition of mixed-chain-length AHLs effectively activated the QS regulatory process of microorganisms in the system, thereby inducing microorganisms to secrete more EPS to adapt to the antibiotic stress environment. Further analysis of EPS composition revealed that the PN component responded more significantly to AHLs than the PS component. This differential change led to an overall increase in the PN / PS ratio in each compartment, with the most significant change in compartment C1, increasing from 1.64 to 1.89, while compartments C2–C5 increased to 1.71, 2.09, 2.25, and 2.73, respectively. An increased PN / PS ratio is generally considered an important indicator of enhanced hydrophobicity of sludge surfaces and stable particle structure, representing a further increase in the sludge's resistance to external shocks. Previous studies have shown that higher PN content can reduce the Zeta potential of the sludge surface and enhance intercellular hydrophobic interactions, thereby further promoting microbial cell aggregation and particle structure stability.

[0085] Besides changes in the total amount and composition of EPS, the addition of AHLs also altered the distribution characteristics of EPS in different stratified structures. In all five compartments, the proportion of S-EPS in the total EPS showed a decreasing trend, with the most significant change in compartment C1, decreasing from 31.39% before enhancement to 18.34%. Simultaneously, the proportions of LB-EPS and TB-EPS increased significantly. The decrease in S-EPS content reflects the optimization of the microbial metabolic microenvironment by AHLs and also represents further structural stability. On the one hand, AHLs reduced cell autolysis caused by environmental stress by regulating community behavior, thereby reducing the amount of intracellular substances released to the outside. On the other hand, soluble PN and PS originally present in S-EPS tended to bind more tightly under the induction of AHLs and gradually migrated into the internal structural layers of granular sludge (LB-EPS and TB-EPS), achieving a transformation from free to structured EPS. This is consistent with the significant increase in LB-EPS and TB-EPS, indicating that AHLs with mixed chain lengths can make the sludge structure more stable. Compared to LB-EPS, TB-EPS showed the most significant changes, primarily due to a substantial increase in the PN component. Specifically, the PN content in each compartment of TB-EPS increased from 96.13, 69.23, 54.85, 40.75, and 38.72 mg / L to 160.22, 115.40, 91.43, 76.26, and 74.53 mg / L. As the EPS most tightly bound to the cell body, the specific enrichment of the PN component in TB-EPS is a core manifestation of the enhanced efficacy of AHLs. Related studies have shown that some PN and related amino acid components (such as tryptophan-like substances) in EPS possess certain redox activities and can participate in EET. Therefore, the increase in TB-PN content may, to some extent, indicate the enrichment of tryptophan-like fluorescent substances, thereby providing more potential active sites for electron transfer between microorganisms. This process helps optimize the electron transfer microenvironment of microorganisms and, to some extent, promotes EET and charge transfer processes at different interfaces.

[0086] Furthermore, as the influent and AHLs flowed sequentially through each compartment of the ABR-MEC reactor, the EPS content and its variations exhibited a distinct spatial distribution. Generally, the upstream compartments, bearing higher loads and antibiotic pressures, generally had higher EPS secretion, with EPS content decreasing progressively from C1 to C5. Simultaneously, the upstream compartments were also the first to be regulated by AHLs, especially the C1 compartment, where the QS response of EPS was most significant. As the hydraulic retention time increased, the decreasing signal intensity and substrate levels along the flow path led to a more robust EPS response in the downstream compartments. This spatial gradient distribution along the reactor axis reflects the differentiated adaptation strategies of microorganisms in different functional zones to environmental conditions, and further illustrates that AHLs, by regulating microbial community behavior, collectively promoted sludge structural stability and enhanced electron transport capacity in different compartments.

[0087] 4. Effects of mixed chain lengths (AHLs) on the structure of sludge microbial communities The first four compartments bear the main organic matter degradation load and are the key areas for reactor performance changes. Therefore, this study focused on collecting and analyzing samples from the first four compartments to reveal the impact of adding mixed chain lengths (AHLs) on the microbial community and function.

[0088] The PCA analysis results based on Bray-Curtis distance are as follows: Figure 7 As shown in the figure, the microbial community structure before and after the addition of AHLs is clearly separated along the PC1 axis (explanation 41.10%). The samples in the "before" group are distributed along the positive PC1 axis, while those in the "after" group are concentrated along the negative PC1 axis. The confidence ellipses of the two groups overlap little, indicating that the addition of AHLs significantly altered the overall community composition. Furthermore, the sample points in the "after" group are more concentrated along the PC2 axis, suggesting that AHLs may have enhanced the structural stability of the microbial community.

[0089] like Figure 8As shown, before the addition of mixed chain length AHLs, the dominant species at the phylum level were Methanobacteriota (23.37–36%), Chloroflexota (13.65–17.36%), Bacteroidota (5.02–6.75%), Thermodesulfobacteriota (4.97–6.13%), and Pseudomonadota (2.64–6.62%). After the addition of mixed AHLs, the dominant species at the phylum level became Methanobacteriota (25.64–35.68%), Chloroflexota (9.04–17.8%), Bacteroidota (5.63–15.27%), Thermodesulfobacteriota (5.89–9.5%), and Bacillota (3.95–10.51%). It is noteworthy that the abundance of Chloroflexota, which previously accounted for a certain proportion, showed a decreasing trend, while the relative abundance of Bacillota significantly increased, becoming the dominant bacterial group. Both are hydrolytic bacteria that break down and ferment complex organic matter to produce acetic acid, but Bacillota has a stronger acid-producing capacity and a faster substrate transformation rate. Bacillota is a motile, spore-forming Gram-positive bacterium that can enhance its environmental adaptability through QS (quantitative stress response). It is speculated that the exogenous addition of AHLs mobilized the QS of Bacillota, promoting its enrichment, which could enhance the hydrolysis and acidification efficiency of the C1 compartment.

[0090] Further analysis of bacterial and archaea community changes at the genus level, such as... Figure 9-10 As shown, the addition of AHLs significantly reshaped the genus-level composition of the bacterial community. After the addition of AHLs, the typical fermenting bacteria genera... Mesotoga , Longilinea and Candidatus_Fermentibacter The relative abundance of all of these bacteria decreased significantly. These bacteria typically participate in the fermentation and degradation of complex organic matter, producing intermediate metabolites such as acetic acid and H2. The decrease in their abundance may indicate that, under the regulation of exogenous AHLs, the synergistic metabolic capacity of microorganisms in the system is enhanced, thereby promoting the rapid conversion and utilization of fermentation products.

[0091] Before the addition of AHLs, the methanogenic archaea were respectively... Methanothrix (56.15~68.2%) Methanobacterium (12.62~18.2%) Methanolinea (4.46~5.93%) and unclassifiedMethanofastidiosia (1.39~4.21%) Dominant species (such as Figure 9-10 (As shown). Acetic acid-producing methanogenic archaea after AHLs addition. MethanothrixThe abundance increased significantly to 63.17–74.42%, indicating hydrogenotrophic methanogens. Methanobacterium and Methanolinea The abundance decreased to 5.11–12.48% and 0.53–2.3%. Further analysis revealed that the changes in compartment C1 differed slightly from those in other compartments; compartment C1 contained mixed-trophic methanogenic archaea. Methanosarcina The abundance increased dramatically, surging from 1.12% before addition to 10.67%. This trend is very similar to the significant increase in Bacillota at the C1 level (from 2.27% to 10.52%), suggesting that the enrichment of Bacillota led to enhanced acetic acid metabolism in the reactor, indicating an acetic acid-producing methanogenic archaea. Methanothrix and Methanosarcina It provides a favorable metabolic environment, and its full utilization of substrates also affects hydrogen production, thus inhibiting hydrogen-nutritive methanogenic archaea.

[0092] 5. The impact of mixed chain lengths (AHLs) on anode community structure like Figure 11 As shown, at the phylum level, *Thermodesulfobacteriota* (17.21–43.58%), *Chloroflexota* (11.75–16.78%), *Pseudomonadota* (3.3–14.81%), *Bacteroidota* (5.55–12%), and *Bacillota* (5.02–10.13%) were the dominant bacterial species on the anolyte biofilm. *Thermodesulfobacteriota* possesses strong electron transport capabilities, transferring electrons to the anode via electron transfer through electro-electro-transfer (EET). Previous studies have shown that some members of this group contain c-type pili, which can mediate direct interspecific electron transfer, giving them a stronger ecological competitive advantage in the EAB. At the phylum level, the methanogenic archaea community on the anolyte biofilm exhibited high homogeneity, with *Methanobacteriota* (64.06–96.52%) holding an absolute dominant position.

[0093] In the anodic biofilm, Geobacter , Trichlorobacter , Syntrophus and Smithella The genera *Isperi* showed a high relative abundance ( Figure 12 ). Geobacter As typical electroactive bacteria, QSAHLs can directly transfer metabolic electrons to the anode via EET, playing a crucial role in the electrode electron transfer process. According to existing research, QSAHLs can significantly enhance the synthesis of EPS, promote the aggregation of electroactive bacteria, and enhance e-pili / c-Cyts expression, thereby improving the overall electroactive content of the anode. Geobacter Electroactivity and biomembrane stability. Spatial distribution, GeobacterThe relative abundance in the C2 anode (26.48%) was significantly higher than that in the C1 anode (1.62%), while it decreased to 0.34% in the subsequent C3 anode. Geobacter It exhibits some sensitivity to antibiotics, and the lower SMX residue and suitable substrate concentration in compartment C2 may be more conducive to its growth. In stable anolyte biofilms formed from various inoculum sources such as activated sludge, MEC effluent, soil, and coastal sediments, Trichlorobacter All of them have been confirmed to be core EAMs, playing an important role in the EET process of anodic biofilms.

[0094] Within the anodic biofilm, significant differences emerged between compartments at the archaea level. Figure 12 In the anodic biofilm E1 of compartment C1, Methanosarcina The abundance was as high as 76.38%, while compartments C2 and C3 were relatively low. Methanothrix The dominant bacterial species (33.48~41.44%). Methanosarcina As a mixed-trophic methanogen, it exhibits strong metabolic diversity and high tolerance to environmental disturbances, thus making it more likely to dominate under conditions of high organic loading and SMX shock in the front compartment. Furthermore, the hydrogen-trophic... Methanobacterium A stable distribution (7.75–16.15%) was observed on all anodes. On the anode surface, EAMs drive the oxidative decomposition of organic matter via EET, a process accompanied by the generation of CO2 and the metabolic byproduct H2. Hydrotrophic methanogenic archaea... Methanobacterium It can efficiently utilize the H2 produced by anodic respiration for methanogenic metabolism. Methanobacterium The enrichment of H2 avoids the thermodynamic feedback inhibition of anodic respiration of electroactive bacteria caused by local H2 accumulation, and in turn promotes the growth of anodic electroactive bacteria and EET efficiency.

[0095] 6. Effects of mixed chain length AHLs on metabolic pathways and QS genes To reveal the changes in metabolic pathways of microorganisms in each compartment after the addition of mixed-length AHLs, KEGG functional annotation was performed on metagenomic sequencing data, and a normalized difference heatmap based on the relative abundance of KEGG secondary pathways was constructed (e.g., Figure 13 (As shown in the figure). Overall, the functional structures of the samples showed high consistency, mainly enriched in metabolic-related pathways such as global and overview maps, carbohydrate metabolism, amino acid metabolism, metabolism of cofactors and vitamins, and energy metabolism, indicating that the microbial community in the system mainly participates in core metabolic processes such as organic matter degradation, energy conversion, and cell growth.

[0096] After the addition of AHLs, functional pathways changed, with a significant increase in signal transduction. Signal transduction is responsible for microorganisms to sense environmental signals and respond promptly. This enrichment suggests that the addition of exogenous AHLs makes the microbial sensory system more sensitive, and enhances intercellular communication and regulatory networks as well as intracellular regulatory behaviors. The Cellular Community–Prokaryotes pathway, which includes QS (quantitative silencing), was only enriched in compartment C1. This is presumably because this pathway encompasses not only QS but also collaborative microbial behaviors such as biofilm formation, which typically depend on high substrate concentrations and strong microbial metabolic activity. With the enhancement of exogenous AHLs, the performance of compartment C1 was significantly improved. As the reactor progressed, the substrate concentration in subsequent compartments gradually decreased, and microbial metabolic activity relatively weakened.

[0097] like Figure 14 As shown in the figure, the abundance of QS-related genes in each compartment significantly increased after the addition of AHLs, with compartments C1-C4 showing increases of 9.51, 8.209, 4.02, and 4.69%, respectively, compared to before the addition of AHLs. Various QS-related genes showed changes to varying degrees, with the most significant changes observed in the anterior compartments (C1 and C2). The abundance of ACSL, luxC, and cviR significantly increased in compartment C1. ACSL participates in AHL precursor synthesis and is a key enzyme regulating fatty acid substrate chain length and AHL synthesis. luxC As a component of the fatty acid reductase complex, it is responsible for generating the precursor aldehyde of the AHL molecule. The enrichment of both indicates that the addition of exogenous AHLs can promote the synthesis of AHLs in the system. Meanwhile... cviR These are typical AHL receptor genes, responsible for mediating AHL sensing and regulating downstream gene expression. The co-enrichment of these three genes indicates that the addition of exogenous AHLs further promotes the synthesis and sensing of AHLs in the C1 compartment microbial community, significantly enhancing its internal QS signaling activity. AHL degrading enzymes ahlD The relative abundance of AHLs varied little across the samples, indicating that the addition of exogenous AHLs at the experimental concentrations did not induce AHL degradation-related responses in the system. The AI-1 signaling pathway also showed significant enrichment after the addition of AHLs, exhibiting […]. spo0A , agrC , agrA , agrB Genes with significantly increased abundance in the C1 compartment were observed. Furthermore, genes of the DSF type showed a significant negative correlation with AHLs. rpfF , rpfG and r pfCGene expression consistently decreased across all compartments after addition. This is because DSF-type genes are involved in quorum quenching (QS suppression system). This indicates that the addition of AHLs not only activates QS-related genes but also reduces the expression of genes that inhibit QS to some extent.

[0098] 7. Effects of mixed chain length AHLs on key enzymes of methane production Further analysis of the gene abundance of key enzymes in methane production was conducted to investigate the impact of exogenous AHLs on the methanogenic metabolic pathway from the perspective of gene response. The results are as follows: Figure 15 As shown, the addition of AHLs significantly increased the abundance of various methane generation-related enzyme genes in the C1 compartment. Thioredoxin reductase-related enzymes (EC: 1.8.7.3-6), involved in electron transport, exhibited high gene abundance in C1. Simultaneously, key enzyme genes such as F420-dependent hydrogenase (EC: 1.12.98.1) and CO dehydrogenase (EC: 1.2.7.4), involved in hydrogen metabolism, also showed relatively high levels. Furthermore, key enzyme genes such as formylmethanefuran dehydrogenase (EC: 1.2.7.12), involved in the oxidation of formylmethanefuran, and acetyl-CoA synthase (EC: 2.3.1.8), involved in acetyl-CoA synthesis, also showed high abundance in the C1 compartment. These enzymes play crucial roles in the oxidation of electron donors and the conversion of intermediate metabolites in the methane generation pathway; their enrichment indicates an enhanced methane metabolic potential in the upstream compartment. As the reactor progressed, the abundance of the aforementioned methane metabolism-related enzyme genes in compartments C2 to C4 generally decreased compared to before their addition. This phenomenon may be related to the decrease in substrate concentration and microbial metabolic activity within the ABR reactor along the process.

[0099] To further explore the potential link between QS and methane metabolism, Pearson correlation analysis was performed on QS-related genes and key enzyme genes involved in methane production. The results are as follows: Figure 16 As shown in the figure, most QS-related genes (AHL and AI-1 classes) exhibit a positive correlation with key methanogenic enzymes. Specifically, F420-dependent hydrogenase (EC: 1.12.98.1), involved in hydrogen metabolism, formylmethanefuran dehydrogenase (EC: 1.2.7.12), and F420-dependent methylenetetrahydromethanepterin dehydrogenase (EC: 1.5.98.1) are all significantly correlated. Furthermore, CO dehydrogenase (EC: 41.2.7.4) and acetyl-CoA synthase hybrid (EC: 2.3.1.169), associated with the Wood–Ljungdahl pathway, are also positively correlated with key methanogenic enzymes. cviR Significantly correlated. This suggests that AHL-mediated QS may promote the expression of hydrogenotrophic and acetate-cleaved methanogenic metabolic pathways by enhancing microbial co-metabolism and electron donor supply.

[0100] Mixed-length aminohydrogenases (AHLs) activated the expression of QS-related genes at the gene level and significantly upregulated the transcriptional levels of methanogenic enzyme genes. The abundance of QS-related genes in each compartment significantly increased after the addition of AHLs, with compartments C1-C4 showing increases of 9.51, 8.209, 4.02, and 4.69% respectively compared to before AHL addition. The abundance of ACSL, luxC, and cviR was significantly increased in compartment C1. Simultaneously, thioredoxin reductase-related enzymes (EC: 1.8.7.3-6), involved in electron transport, showed high gene abundance in C1; F420-dependent hydrogenase (EC: 1.12.98.1) and CO dehydrogenase (EC: 1.2.7.4), involved in hydrogen metabolism, also showed high abundance. These findings suggest that AHL-mediated QS may promote the expression of both hydrogenotrophic and acetate-cleaved methanogenic pathways by enhancing microbial co-metabolism and electron donor supply.

[0101] In summary, this invention constructs a MEC-ABR coupled system based on an anaerobic baffled reactor (ABR) to systematically study the degradation patterns of SMX in each compartment under AHLs-regulated conditions. During reactor operation, the impact of mixed-chain-length AHLs on system performance is evaluated by continuously monitoring operating indicators such as SMX removal rate and methane yield. Simultaneously, the structural characteristics and electrochemical performance of electrode biofilms are systematically analyzed using characterization techniques such as scanning electron microscopy, electrochemical workstation, high-performance liquid chromatography-mass spectrometry, and three-dimensional fluorescence spectroscopy. Furthermore, by combining microbial community structure analysis and metagenomic sequencing, the regulatory role of mixed-chain-length AHLs on the system's microbial metabolic processes and EET mechanism is deeply elucidated from the perspectives of community structure succession, changes in functional genes, and key metabolic pathways.

[0102] This study revealed the regulatory role of mixed-chain-length AHLs on the long-term SMX impact in the ABR-MEC system. Compared with before addition, the addition of composite AHLs increased the SMX degradation rate of each compartment by 45.61%, 37.93%, 37.7%, 31.87%, and 39.09%, respectively, and the methane production increased by 31.95%, 25.10%, 19.35%, 15.38%, and 13.40%, respectively. Bacillota Alternative Chloroflexota Becoming the dominant bacterium gives the system a stronger acid-producing capacity and a faster substrate transformation rate, while also providing a breeding ground for acetic acid-producing methanogenic archaea. Methanothrix and Methanosarcina It provides a favorable metabolic environment.

[0103] The regulatory mechanism of mixed-chain length hydroxyl groups (AHLs) on methanogenesis was elucidated. The abundance of QS-related genes in each compartment significantly increased after the addition of AHLs, by 9.51, 8.209, 4.02, and 4.69% respectively compared to the four compartments before AHL addition. Correlation analysis revealed a positive correlation between QS-related genes and key methanogenic enzymes. Specifically, F420-dependent hydrogenase (EC: 1.12.98.1), involved in hydrogen metabolism, formylmethanefuran dehydrogenase (EC: 1.2.7.12), and F420-dependent methylenetetrahydromethanepterin dehydrogenase (EC: 1.5.98.1), were all significantly correlated. Furthermore, CO dehydrogenase (EC: 41.2.7.4) and the acetyl-CoA synthase mixture (EC: 2.3.1.169), both associated with the Wood–Ljungdahl pathway, were also significantly correlated with cviR. This suggests that AHL-mediated QS may promote the expression of hydrogenotrophic and acetateotrophic methanogenic pathways by enhancing microbial co-metabolism and electron donor supply.

[0104] The embodiments of the present invention have been described in detail above with reference to the accompanying drawings. However, the present invention is not limited to the above embodiments, and various changes can be made within the scope of knowledge possessed by those skilled in the art without departing from the spirit of the present invention. Furthermore, the embodiments of the present invention and the features thereof can be combined with each other unless otherwise specified.

Claims

1. A method for treating antibiotic-containing wastewater, characterized in that, The treatment method includes the following steps: after inoculating sludge into a wastewater treatment reactor, wastewater is introduced for wastewater treatment; N-acylhomoserine lactone is added during the 149th-212th day of wastewater treatment; the N-acylhomoserine lactone includes C6-HSL and C12-HSL; the concentration of the N-acylhomoserine lactone in the system is 1-2.8 μM.

2. The processing method according to claim 1, characterized in that, The inoculation amount of the sludge is 85-100 g / L.

3. The processing method according to claim 1, characterized in that, After the sludge is inoculated into the wastewater treatment reactor, the hydraulic retention time of the wastewater is set to 22-28 hours.

4. The processing method according to claim 1, characterized in that, The wastewater treatment reactor comprises five compartments, of which the first three compartments have external electrodes.

5. The processing method according to claim 1, characterized in that, The external voltage of the wastewater treatment reactor is 0.5-1.5V.

6. The processing method according to claim 1, characterized in that, The wastewater includes wastewater containing antibiotics; Preferably, the antibiotics include sulfonamide antibiotics; More preferably, the sulfonamide antibiotics include at least one of sulfamethoxazole, sulfadiazine, sulfadimidine, sulfamethoxypyrimidine, and sulfathiazole; Preferably, the concentration of antibiotics in the wastewater is 0~50 mg / L.

7. The processing method according to claim 1, characterized in that, The treatment method further includes the steps of adding carbon source, nitrogen source, phosphorus source, trace element solution and vitamins to the wastewater treatment reactor; Preferably, the carbon source, nitrogen source and phosphorus source are added in a ratio of C:N:P = (190-210):(4-6):(0.5-2).

8. The processing method according to claim 1, characterized in that, The molar ratio of C6-HSL to C12-HSL is (1-2):(1-2).

9. A system for treating antibiotic-containing wastewater, characterized in that, The system includes a feed tank, a feed pump, an anaerobic baffle reactor, a hydrothermal circulation pump, an outlet tank, and a power supply, which are connected in sequence.

10. The application of the treatment method according to any one of claims 1-8 or the system according to claim 9 in wastewater treatment; Preferably, the wastewater includes wastewater containing antibiotics; Preferably, the wastewater treatment includes removing at least one of antibiotics and COD from the wastewater.

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