Antibiotics were detected in the tailwater of Lanzhou City's wastewater treatment plant in Northwest China's Gansu Province, with the highest concentration value reaching 9.78 \(\upmu\)g\(\cdot\)L\({}^{-1}\). It was deduced that the 14 antibiotics continuously discharged from the wastewater plant to the Lanzhou section of the Yellow River combine to total about 5.66 kg per day, and the risk to the aquatic environment from long-cycle antibiotic exposure cannot be ignored [8]. The bioretention cell-microbial fuel cell (BRC-MFC) has been widely used to remove conventional pollutants from wastewater in recent years [9], and our group has been working on its use for a long time [10; 11; 12; 13; 14]. BRC-MFC has a good degradation effect on antibiotics as it can remove pollutants through multiple pathways such as filler adsorption, plant uptake, root secretion degradation, and microbial decomposition [15; 16; 17]. However, when applying BRC-MFC, plants and microorganisms can also be subjected to reverse stress from antibiotics during the treatment of antibiotic-containing wastewater [18], which, in turn, affects the decontamination performance of the BRC-MFC. For example, TC can inhibit the growth of plants and toxify their roots by inhibiting the protein synthesis of Microcystis aeruginosa and green algae [19], as well as by inhibiting the activity of enzymes in chloroplasts [20; 21]. The residues of OFLX (>20 \(\upmu\)g\(\cdot\)mL\({}^{-1}\)) showed significant negative effects on tomato growth, photosynthesis, fluorescence parameters, antioxidant enzyme activity and transcript-level expression [22]. Antibiotics can also bind to active sites in soil enzyme molecules including sulfhydryl groups and imidazole-containing ligands, forming more stable complexes that inhibit the active centers of enzymes and reduce the activity of soil hydrolytic enzymes, thus affecting the conversion of soil nutrients as well as having indirect effects on plant growth [23]. High concentrations of norfloxacin inhibited the phyla Aspergillus and Actinomycetes [24], with the number of bacteria and fungi in the soil significantly reduced by 10 mg\(\cdot\)kg\({}^{-1}\) TC, marking reductions of 80.67% and 57.20%, while the maximum reduction rates were 86.91% and 74.01%, respectively [25]. Based on the many effects of antibiotics on plants and microorganisms in BRC-MFC systems, further systematic studies on the effects of multiple antibiotics on the decontamination performance of BRC-MFC and the response characteristics of rhizosphere microorganisms are warranted. A microbial fuel cell (MFC) is a device that uses microorganisms to convert chemical energy in organic matter directly into electrical energy. The MFC is divided into an anode layer and a cathode layer, with the anode placed in an anaerobic environment in the submerged layer, the cathode in an aerobic environment in the transition layer and the two electrodes connected by external wires [26]. The electron-producing microorganisms in the submerged layer oxidize organic matter to produce electrons, which are transferred from the anode to the cathode via an external wire, creating a current to accelerate pollutant removal [27]. As a biocatalyst, the microbial community plays an important role in the performance of the MFC. When the MFC degrades antibiotics, the biological composition of the electrode surface is divided into two main components: an electrically active extracellular electricity-producing colony and an antibiotic-degrading colony. The complex interactions between the two are critical to antibiotic degradation and electrical energy production in the MFC [28]. Changes in environmental factors, such as the antibiotic concentration, antibiotic type, pH and temperature, can affect the structure of the microbial community in the MFC, which, in turn, affects the performance of the BRC-MFC in removing contaminants [29].