## 1 Introduction  
The development of the economy and society has intensified lead (Pb) pollution in soils due to various human activities [1; 2]. Pb, a persistent environmental pollutant, accumulates and biomagnifies through the food chain, posing serious risks to human health [3]. Pb pollution not only induces Pb resistance but also antibiotic resistance in soil bacteria, turning Pb-contaminated soils into significant reservoirs for antibiotic resistance genes (ARGs) [4]. ARGs are a growing public health threat, as they enable bacteria to resist antibiotic treatments, leading to more difficult infections, higher healthcare costs, and increased mortality [4; 5; 6]. ARGs spread through horizontal gene transfer, accelerating their dissemination in both clinical and environmental settings. Addressing the factors driving ARG proliferation is crucial to preserving the effectiveness of antibiotics and safeguarding public health. Studies have shown that the average Pb concentration in surface agricultural soils in mining areas is 58.4 mg/kg [5], with a positive correlation between Pb concentrations and certain ARGs in soils [6]. Therefore, Pb-contaminated soil inherently poses risks for ARGs dissemination, underscoring the need to study the patterns and factors influencing this process. Currently, several methods are available for remediating Pb-contaminated soils. One effective method involves adsorption using montmorillonite, where Pb ions is primarily adsorbed through chemical and electrostatic bonding [7]. Another effective method is the remediation using monocalcium phosphate (Ca(H\({}_{2}\)PO\({}_{4}\))\({}_{2}\)), which alters soil pH to displace or adsorb Pb, forming stable precipitates that reduce Pb mobility and toxicity [8]. Clay minerals, as key components of soil colloids, have been successfully used to solidify and stabilize soil with minimal disruption to its structure. Active magnesium oxide (MgO) has shown greater effectiveness compared to other stabilizers in enhancing soil strength and reducing Pb\({}^{2+}\) leaching toxicity [9]. Combining different remediation agents often mitigates Pb toxicity through various reactions, making it critical for the development of green composite remediation agents for Pb-contaminated soils. For instance, the combination of Ca(H\({}_{2}\)PO\({}_{4}\))\({}_{2}\) and montmorillonite improves soil biocompatibility, enhances bioactivity, and lowers toxicity and remediation costs [10]. Similarly, combining MgO with natural materials improve heavy metal adsorption and solidification. The synergy between Ca(H\({}_{2}\)PO\({}_{4}\))\({}_{2}\), MgO, and montmorillonite enhances heavy metal remediation, boosting both adsorption and stabilization. Bioelectrochemical system (BES) is a technology that integrates biological and electrochemical processes to convert chemical energy into electrical energy or drive redox reactions. It offers an eco-friendly and cost-effective technology for soil remediation, with the added benefit of reducing ARGs without causing secondary pollution [11; 12]. These methods not only remediate Pb contamination but also alter the soil's physicochemical properties, such as Pb speciation, Pb\({}^{2+}\) concentration, and pH. [PERSON] et al. [13] reported that Pb significantly increased the total relative abundance of \(\beta\)-lactamase (except 100 mg/kg) and vancomycin resistance genes in soils. pH was demonstrated to influence the selection of multidrug efflux pump genes, thus shaped the soil resistance [14]. Hence, understanding how various remediation processes affect ARGs dissemination in Pb-contaminated soils is crucial. Our previous research demonstrated that combining composite amendments with BES enhanced Pb stabilization, with Pb concentration and pH significantly influencing Pb speciation and remediation efficiency [15]. However, there is limited research on ARGs transmission during the remediation process of various soil heavy metal pollutions.