###### Abstract
[12] tested the ability of various Basidiomycete strains to degrade 1,1,1-trichloro- 2,2-bis(4-chlorophenylenyl)ethane (DDT), representing hardly biodegradable, persistent chlorinated pesticides. They found eight various DDT family metabolites resulting from the biodegradation of DDT by _Marasmiellus_ sp. strains. Similarly, [PERSON] et al. [13] tested the ability of the white-rot fungus _Pleutrotus eryngiu_ to degrade naphthalene and tried to describe the principles of naphthalene metabolism. They identified numerous intermediates, by-products, and other metabolites as well as the depletion of naphthalene and documented the effective naphthalene degradation. However, in this context, the potential toxicity of the intermediates should be considered when assessing the bioremediation effectivity. [PERSON] et al. [14] confirmed the ability of saprotrophic Basidiomycetes _Stroplaria rugosannulata_ and _Planerochaete velitina_ to degrade polychlorinated dibenzo-p-dioxins and dibenzofurans, where the reported decrease in WHO-TEQ value was 62-64% in 3 months. These authors highlighted that the critical factor of the sufficient biodegradation of these pollutants is the strong growth of the fungal mycelia in the polluted soil. The positive effect of mycorrhizal fungi on the effectivity of phytoremediation of the DDT metabolites in soil was also presented by [PERSON] et al. [15]. The persistence of PAHs in the environment is influenced by several factors. These factors include concentration, chemical structure, dispersion, bioavailability, and environmental factors such as soil structure and type, temperature, pH, amount of nutrients, water, and oxygen, which the microorganisms need to degrade the contaminant. These factors influence the duration that PAHs remain in the environment [16]. PAHs with higher molecular weight are more resistant to degradation by microorganisms and more persistent in the environment, while PAHs with lower molecular weight are more volatile. The \"age\" of PAHs in sediment or soil is also important for the ability of microorganisms to degrade a given contaminant [17]. Another factor that can affect the residence time of PAHs in the soil is the association, or formation of associations, of PAHs with other contaminants present,for example, petroleum hydrocarbons and risk elements [18], posing significant challenges to PAH degradation research. Wood-rotting Basidiomycete fungi, specifically white-rot fungi, are organisms known for producing lignin-degrading enzymes. The biodegradation of lignin represents a key step in the carbon cycle in nature. Among the most studied ligninolytic enzymes of white-rot fungi are lignin peroxidase, manganese-dependent peroxidase, and lactose. The ability of white-rot fungi to degrade a wide range of organopolultants has been described in several studies, and ligninolytic enzymes play an important role in this case. _Phareochaete chrysosporium, Tametes versicolor_, and other representatives of these genera are most often named among the fungal species that have been confirmed to be capable of degrading PCBs or PAHs [19]. Due to the especially high production of lactose, _Tametes_ sp. is preferred in mycoremediation research [10]. For instance, [PERSON] et al. [20] observed the removal of between 76.8% and 80.3% of dichlorophenol, diclofenac, and triclosan contained in municipal wastewater. The occurrence of arbuscular mycorrhizal fungi (AMFs) was confirmed in the areas polluted with organic pollutants. Moreover, [PERSON] et al. [21] reviewed numerous findings documenting the beneficial role of AMFs in the tolerance of plants to organic pollutants. Compared to the saprotrophic fungi, the ectomycorrhizal fungi can degrade the POPs. However, their enzymatic degradation mechanism differs from those typical for the white-rot and brown-rot fungi, as reviewed by [PERSON] and [PERSON] [22] and [PERSON] [11]. Moreover, the other organisms present in the associated rhizosphere can contribute to the synergy of pollutant degradation.