## 2 Materials and Methods  
Activated carbon and unamended mineral materials, e.g., zeolite, limestone sand, diatomic and halloysite, were used in the analyses (Figure 1). The mineral materials were not subject to pre-treatment to ensure use of the most economically favorable material, as these relatively cheap materials are widely used for water treatment processes [40; 41; 42; 43], and also in the phytostabilisation of soils contaminated by heavy metals [44; 45]. The only exception is activated carbon, which was selected as a reference material due to its wide application in the treatment of contaminants in the soil-water environment using permeable reactive barrier technology [46; 47; 48; 49]. Surface morphology and oxide composition of the applied materials were determined using scanning electron microscopy (FEG Quanta 250, USA) and X-ray spectroscopy with energy dispersion X-ray microscopy--EDS by EDAX (USA). The specific surface area (S\({}_{\mathrm{BET}}\)) of the reactive materials was calculated using the Brunauer-Emmett-Teller (BET) method based on the nitrogen adsorption-desorption isotherm at 77 K using ASAP 2020M by Micromeritics (Norcross, GA, USA). Electrical conductivity (EC) and pH of the reactive materials were measured in an aqueous suspension of 1:2.5 (\(w/v\)) and 1:5 (\(w/v\)) using a conductivity and pH multimeter pH/LF 12 (Schott, Munich, Germany). The cation exchangeable capacity (CEC) of Na\({}^{+}\), K\({}^{+}\), Mg\({}^{2+}\), and Ca\({}^{2+}\) was determined at pH 7 with ammonium acetate [50] and their concentrations measured by an Atomic Absorption Spectrophotometer iCE-3000 (Thermo Scientific, Waltham, MA, USA). Analysis of the effect of temperature on the intensity of contaminant removal was performed in two series: (1) for low initial concentrations of contaminants (Zn--7.5 mg/L, Cu--30 mg/L, PO\({}_{4}\)-P--10 mg/L, NH\({}_{4}\)-N--10 mg/L), insufficient for the exhaustion of the maximum adsorption capacity of the materials, at 3 \({}^{\circ}\)C, 6 \({}^{\circ}\)C, 10 \({}^{\circ}\)C, 15 \({}^{\circ}\)C, 22 \({}^{\circ}\)C, 30 \({}^{\circ}\)C and 40 \({}^{\circ}\)C; and (2) for high initial concentrations of the contaminants, in the range from 0.5 to 100 mg/L for heavy metals, phosphates from 0.25 to 50 mg/L, and ammonium ions from 0.5 to 100 mg/L at 3 \({}^{\circ}\)C, 10 \({}^{\circ}\)C, 22 \({}^{\circ}\)C and 40 \({}^{\circ}\)C. The concentration of heavy metals and biogenic components in stormwater is varied and can range from 0.007 to 0.963 mg Cu/L, 0.015 to 5.070 mg Zn/L, 0.73 to 17.00 mg NH\({}_{4}\)-N/L and from 0.02 to  
Figure 1: Reactive materials used in the studies. 14.30 mgP/L (from 0.10 to 0.40 mg PO\({}_{4}\)-P/L) [8; 9; 10; 15; 17]. The concentrations of tested components, assumed here, exceeded the concentrations observed in-situ, but they ensured the unification of the test scheme and, in most cases, the exhaustion of materials capacity. In both series, 0.500 \(\pm\) 0.001 g of reactive material was shaken with 50 \(\pm\) 0.5 mL of the solution for 24 h on a DOS orbital shaker (Elmi, Bergstrasse, Germany) at 160 rpm within a thermostatic cabinet ST 1 (Pol-Eko, Wodzislaw Slaski, Poland) to ensure a stable temperature (\(\pm\)0.1\({}^{\circ}\)C) for the duration of the experiment. All analyses were performed in triplicate, for which arithmetic means and standard deviations were calculated and presented on charts as error bars. Chemical reagents (CuCl\({}_{2}\cdot\)2H\({}_{2}\)O, ZnCl\({}_{2}\), NH\({}_{4}\)Cl, K\({}_{2}\)HPO\({}_{4}\)) and demineralized water were used in all analyses. Following the experiment, samples were collected and filtered through a 0.45 \(\upmu\)m filter for quantitative analyses ([PERSON], Maidstone, UK). Samples containing heavy metals were acidified by adding 0.5 mL concentrated nitric acid and stored at 3 \({}^{\circ}\)C for later analysis.