## 1 Introduction  
More than 2000 nuclear tests, including military and commercial applications, have been carried out around the world since 1945, which has caused the worldwide spread of nuclear pollution [1]. The abundant long-lived radionuclides have penetrated into the ground soil and groundwater system through diffusion and transport and caused long-term harm to the local environment [2]. For example, the Chernobyl nuclear accident polluted the surrounding soil within a range of 4300 km\({}^{2}\) with various radionuclides, such as Cs, Sr, Eu, Pu, and Am [3, 4]. The Fukushima nuclear accident in Japan was estimated to contaminate buildings and roads within a land range of 1778 km\({}^{2}\), in which the total amount of \({}^{137}\)Cs-contaminated soil was 16-22 million m\({}^{3}\)[5]. Radioactive contaminated soil usually features high concentrations of high-level waste with a range of radionuclides, which makes remediation challenging. Among these radioactive wastes, considerable \({}^{137}\)Cs exists in spent fuel reprocessing liquid waste, the liquid nuclear waste generated during the operation of nuclear power facilities, and nuclear facility decontamination, and it is spontaneously released into the environment and causes soil pollution [5]. Therefore, \({}^{137}\)Cs is the main nuclide in polluted soil, and it is a long-lived fission product that releases considerable heat (t\({}_{1/2}\) = 30.08 years, a \(\beta\)/\(\gamma\) emitter) and has a half-life of approximately 30 years in high-level radioactive liquid waste [6]. High levels of \({}^{137}\)Cs brought near the human body through inhalation or ingestion accumulate in tissue or muscles, which causes nausea, vomiting, diarrhea ratios, and they might lead to byproduct production [8]. Research on the decontamination of radioactive contaminated soil initially began in the 1980s. A series of remediation strategies for the decontamination of soil containing radionuclides were developed, including chemical decontamination, physical decontamination, physical and chemical hybrid treatments, and biological remediation, based on the migration capacities of the radionuclides [9]. Specifically, chemical decontamination includes chemical extraction, electrokinetic decontamination, and heap leaching [10], while physical decontamination technologies include screening, flotation, separation gating, and in situ vitrification [11]. In the 1980s, the Pacific Northwestern National Lab (PNNL) in the United States developed an in situ vitrification technology (in situ vitrification ISV) to remediate soil with nuclear waste [12]. The Argonne National Laboratory (ANL) created a device for in situ vitrification of contaminated soils that simultaneously conducts radioactive waste treatment and research [13]. Moreover, physical and chemical hybrid treatment technologies were studied. [PERSON] et al. (2004) showed that radioactive Pu was removed from contaminated soil via extraction with hydrochloric acid, nitric acid, and citric acid, and the nuclear waste removal rates were as high as 90% [14]. [PERSON] et al. (1983) found that uranium removal was significantly improved with NaHCO\({}_{3}\) as the eluting agent [15]. In addition, bioremediation, including phytoremediation and microbial remediation, has been studied recently due to the low costs and feasibility for use in large polluted fields [16]. Recent bioremediation of radioactive soil was carried out with sunflowers that were planted after the Fukushima accident in Japan [17]. The specific activities of radioactive Cs in the sunflower stems and roots were 52 Bq kg\({}^{-1}\) and 148 Bq kg\({}^{-1}\), respectively, while in the soil, it was 7715 Bq kg\({}^{-1}\) after waste bioremediation [18]. Although numerous soil remediation technologies have been developed, the existing soil decontamination methods have disadvantages that limit their application [18]. For example, physical methods are relatively simple but usually involve considerable labor costs and can cause problems such as secondary pollution.