Nettle (NE) and mint (MT) herb residues were dried at 110 °C and then their stalks were cut into 1.5–2.0 cm long pieces. Fifteen-gram samples of the precursors were placed in nickel boats and subjected to simultaneous pyrolysis and physical activation in a horizontal resistance furnace equipped with a quartz tube reactor (one-zone model PRW75/LM, Czylok, Jastrzębie-Zdrój, Poland). The process involved annealing the sample at 800 °C for 30 min in a CO₂ atmosphere with a flow rate of 250 cm³/min. After the completion of the one-step activation process, the materials were cooled to room temperature under a nitrogen flow (flow rate of 170 cm³/min). The resulting activated products were designated as NE_AP and MT_AP.

Polyethyleneimine (PEI) (Sigma Aldrich, Saint Louis, MO, United States) is a cationic polymer with an average molecular weight of 2000 Da, containing amine groups along its chains. This weak polyelectrolyte has a pK_b value at pH 9, at which 50% of its functional groups are dissociated. As the pH decreases, the number of dissociated amine groups increases, leading to the spatial expansion of the polymer chain (Von Harpe et al., 2000).

Poly(acrylic acid) (PAA) (Fluka, Saint Louis, MO, United States) represents the group of anionic polymers and it is characterized by an average molecular weight of 2000 Da. It is also a weak polyelectrolyte and its macromolecules contain carboxyl functional groups, 50% of which dissociate at pH 4.5, to the pK_a value of PAA. Below this pH value, the degree of dissociation decreases, leading to the formation of a coiled conformation of the polymer chains. In turn, at pH values above 4.5, the number of dissociated carboxyl groups increases, resulting in a more extended chain conformation (Chibowski et al., 2003).

Cadmium nitrate tetrahydrate (CdN₂O₆·4H₂O, Sigma Aldrich, Saint Louis, United States) was used as a source of Cd(II) cations. This compound dissolves well in water at pH below 8, while above this value, cadmium ions precipitate. As a result, experiments involving Cd(II) were limited to the pH range from 3 to 7.

The As(V) anions used in the study were introduced by potassium dihydrogen arsenate (KH₂AsO₄, Sigma Aldrich, Saint Louis, United States). This salt is highly water-soluble over a wide pH range. However, the form of arsenate ions varies with pH changes. At higher pH values, the As(V) ion is fully dehydrated and exists as AsO₄ ^3- anion. As the pH decreases, the degree of hydration increases, resulting in the occurrence of the following forms: HAsO₄ ^2-, H₂AsO₄ ⁻ and H₃AsO₄ (Das and Bezbaruah, 2020).

The surface morphology of the activated biocarbons was examined using scanning electron microscopy (SEM) (Quanta 250 FEG, FEI, Waltham, MA, United States). The porosity characteristics, including the total/micropore surface area, total pore/micropore volume, and average pore diameter, were assessed by low-temperature (−196 °C) nitrogen adsorption-desorption measurements performed using an ASAP 2420 apparatus (Micromeritics, Norcross, GA, United States). The functional groups present on the surface of the biocarbons were quantified using the Boehm back titration method (Boehm et al., 1964). In this analytical procedure, NaOH and HCl solutions (both at a concentration of 0.1 mol/dm³, Avantor Performance Materials, Gliwice, Poland) were used as titrants. To analyze the surface chemistry and identify C-, N-, and O-containing functional groups present on the tested materials, X-ray photoelectron spectroscopy (XPS) (Gammadata Scienta, Uppsala, Sweden) was applied. The ash content was determined according to the ISO 1171:2002 standard, using a muffle furnace FCF-V70C (Czylok, Jastrzębie Zdrój, Poland). The total content of C, N, H, and S was determined using an elemental analyzer Vario EL III (Elementar Analysen Systeme GmbH, Germany). The chemical composition of the materials was also studied by means of X-ray fluorescence (XRF) spectrometry (Axios mAX, PANanalytical, Almelo, Netherlands).

The adsorbed amounts of PAA and PEI polymers, as well as Cd(II) and As(V) ions, were determined using the static method. This approach involved measuring the change in adsorbate concentration in the solution before and after the adsorption process.

The concentrations of the polymers were determined using a Carry 100 UV–Vis spectrophotometer (Varian, Palo Alto, Santa Clara, CA, United States). For poly(acrylic acid), its reaction with hyamine 1622 was carried out. As a result, a white-coloured complex, absorbing light at a wavelength of 500 nm, was formed (Crummett and Hummel, 1963). In turn, the concentration of polyethyleneimine was determined based on its reaction with copper(II) chloride, which results in a blue-coloured complex absorbing light at 285 nm (Patkowski et al., 2016). The calibration curves used to determine the polymer concentration determination are presented in Figure 1. The presence of heavy metal ions causes a shift of calibration curves (especially in the case of PAA). These effects were described in details in the previous paper (Gęca et al., 2024c).

The concentrations of Cd(II) and As(V) ions were determined using Inductively Coupled Plasma-Optical Emission Spectrometry (ICP-OES) with the iCAP™ 7200 analyser (Thermo Fisher Scientific, Waltham, United States). The measurement wavelengths were 228.8 nm for cadmium and 189 nm for arsenic ions, respectively. The operational parameters for the ICP-OES included the plasma with the following settings: flow rate of 15 dm³/min, a nebulizer flow rate of 0.75 dm³/min and a power setting of 1 kW. The presence of the polymers reduced the analytical signal by 5% and this interference was taken into account in the calculations.

Adsorption isotherms were studied over a 24-h period of time. For these tests, 10 cm³ of solutions containing the adsorbate (with initial concentrations ranging from 10 to 300 ppm) and a 0.001 mol/dm³ NaCl supporting electrolyte were prepared. The weights of activated biocarbons used were 0.02 g for polymers and 0.05 g for metal ions. Experiments were conducted at pH 3, 6 and 9, but studies involving Cd(II) ions were limited to pH 3 and 6. At pH above 7, cadmium(II) ions precipitate in the solution. Therefore, their loss from solution at alkaline pH values is the result not only of Cd(II) ions adsorption but also of precipitation. Before the adsorption test, the pH value of all tested samples was adjusted using 0.1 mol/dm³ NaOH or HCl solutions and measured using a Φ360 pH meter (Beckman, Brea, United States). A constant pH level was maintained throughout the adsorption process by continuous monitoring and correction as necessary. The adsorption isotherms data obtained for heavy metal ions were fitted to theoretical models. The Langmuir (Equation 1), Freundlich (Equation 2), Temkin (Equation 3) and Dubinin-Radushkevich (Equation 4) equations were applied (Awad et al., 2019): q e = q m K L C e 1 + K L C e (1) q e = K F C e 1 / n (2) q e = R T b T ln ⁡ A T + R T b T ln ⁡ C e (3) q e = q m ⁡ exp ⁡ − β ε 2 (4) where: q _e –the adsorbed amount at the equilibrium state [mg/g], q _m –the maximum adsorption capacity in the Langmuir model [mg/g], K _L –the Langmuir parameter [m³/mg], C _e –the equilibrium aqueous phase concentration [mg/dm³], K _F –the Freundlich parameter [mg/g (mg/dm³)^1/n], n–the Freundlich constant, R–gas constant (8.314 J/(mol K), T–temperature [K], A _T –Temkin constant [J/mol], b _T –Temkin constant [dm³/g], β–Dubinin-Radushkevich constant, ε–adsorption potential [kJ/mol].

Based on the obtained results, pH 3 at which the adsorbed amounts of polymers were the greatest, was chosen for the kinetics studies. In these tests, an appropriate mass of activated biocarbon was added to 10 cm³ of a solution containing 0.001 mol/dm³ NaCl as the supporting electrolyte. The initial concentration of both polymers was 200 ppm. Adsorption progress was monitored over time intervals ranging from 0.5 to 7 h. Kinetics data for polymers were fitted to the pseudo-first-order (Equation 5) and pseudo-second-order (Equation 6) models (Wang and Guo, 2020), according to the equations: d q t d t = k 1 q e − q t (5) d q t d t = k 2 q e − q t 2 (6) where: q _e –the adsorbed amount in the equilibrium state [mg/g], q _t –the adsorbed amount after time “t” [mg/g], k ₁ – the equilibrium rate constant [1/min], k ₂ – the equilibrium rate constant [g/(mg⋅min)].

Adsorption studies in single and binary adsorbate systems were conducted for 24 h at pH 3. The 10 cm³ of the suspensions consisted of: 200 ppm adsorbate (polymers and/or metal ions), 0.001 mol/dm³ NaCl and appropriate mass of activated biocarbon, were prepared. After the adsorption process, activated biocarbon was separated using a microcentrifuge (Centrifuge MPW 233e, MPW Med. Instruments, Warsaw, Poland). The concentrations of adsorbates in the supernatants were measured. For polymers, desorption from the surface of biocarbon materials was also investigated, while for metal ions, desorption studies were not conducted due to the small amounts adsorbed and the high associated errors. The H₂O, HNO₃ or NaOH solutions (acidic and basic solutions with a concentration of 0.1 mol/dm³) were used as desorbing agents, and the process lasted 24 h. After that time activated biocarbon was again separated and the concentrations of PAA or PEI in the supernatants were determined. The NE_AP activated biocarbon was dried after the desorption process and performed to the adsorption-desorption cycle studies. All adsorption and desorption tests were carried out at 25 °C. Each sample was measured 3 times and the differences between the obtained result values do not exceed 5%.

The determinations of surface charge density (σ₀), zeta potential (ζ) and aggregates size were carried out at 25 °C for the following systems: NE_AP, NE_AP + PEI, NE_AP + PAA, NE_AP + PAA + PEI, NE_AP + Cd(II), NE_AP + Cd(II)+PEI, NE_AP + Cd(II)+PAA, NE_AP + As(V), NE_AP + As(V)+PEI, NE_AP + As(V)+PAA, MT_AP, MT_AP + PEI, MT_AP + PAA, MT_AP + PAA + PEI, MT_AP + Cd(II), MT_AP + Cd(II)+PEI, MT_AP + Cd(II)+PAA, MT_AP + As(V), MT_AP + As(V)+PEI and MT_AP + As(V)+PAA.

To determine the surface charge density (σ₀), 50 cm³ of suspensions were prepared, each containing the given adsorbate at an initial concentration of 100 ppm, supporting electrolyte NaCl at a concentration of 0.001 mol/dm³ and 0.054 g of NE_AP or 0.03 g of MT_AP. The prepared suspension was placed in a thermostated Teflon vessel (RE 204 thermostat, Lauda Scientific, Lauda-Königshofen, Germany). The glass and calomel electrodes (Beckman Instruments, Brea, United States) were introduced into the vessel to monitor pH changes using a pH-meter (pHM 240, Radiometer, Warsaw, Poland). The pH was adjusted by gradually adding 0.1 mol/dm³ NaOH (titrant), using an automatic microburette (Dosimat 765, Metrohm, Herisau, Switzerland). The dependence of the σ₀ value on the pH of the suspension was determined using the Titr_v3 computer program, which also controlled the titration process. These calculations were based on the difference in the volume of NaOH added to the suspension and to the supporting electrolyte solution to achieve the same pH value (Janusz, 1994), using the following equation (Equation 7): σ 0 = ∆ V c F m S (7) where: ΔV–the difference in the volume of NaOH added to the suspension and to the supporting electrolyte solution to achieve the appropriate pH value [dm³]; c–NaOH concentration [mol/dm³], F–Faraday constant [C/mol], m–solid mass [g], S–solid surface area [m²/g].

The zeta potential (ζ) and aggregate size of activated biocarbon particles, both in the presence and absence of adsorbates, were evaluated using the procedure described below. Initially, a suspension of 200 cm³ volume was prepared, containing 200 ppm of tested polymer/s and/or metal ions, 0.001 mol/dm³ NaCl as a supporting electrolyte, and 0.03 g of the carbonaceous material. The suspension was subjected to ultrasonic treatment using an ultrasonic head (XL 2020; Misonix, Farmingdale, United States) for 3 min. Appropriate adsorbates were then introduced into the suspension. The obtained suspension was divided into smaller portions, and the pH of each portion was adjusted to a value ranging from 3.0 to 10.0 (±0.1), using 0.1 mol/dm³ HCl and NaOH solutions. pH adjustment was performed using a Φ360 pH meter (Beckman, Brea, United States). The zeta potential was determined using the laser Doppler electrophoresis technique with a Zetasizer Nano ZS (Malvern Instruments, Malvern, United Kingdom). This instrument measured the electrophoretic mobility of solid particles, both covered with adsorption layers and without them. The zeta potential (ζ) was then calculated from the electrophoretic mobility data using Henry’s equation (Equation 8): (Ohshima, 1994): U e = 2 ε 0 ε ζ 3 η f κ a (8) where: U _e –solids electrophoretic mobility [cm²/(V⋅s)], ε ₀ – the electric permittivity of a vacuum [F/m], ε–dielectric constant, η–viscosity of dispersive phase [Pa⋅s], f(κa) – Henry’s function.

The measurement was carried out 9 times and the error did not exceed 5%.

Additionally, the stability of the suspension was investigated by determining the average size of solid particles aggregates at pH 3, 6, and 9. In this case, the measurements were based on the static light scattering phenomenon. Each sample was measured three times and the error was less than 5%.

Both obtained activated biocarbons have a mesoporous structure and well-developed specific surface area (Table 1). The material obtained from the mint herb residue shows significantly better textural parameters (surface area 666 m²/g), while the adsorbent derived from the nettle herb remains is characterized by a greater concentration of the functional groups on its surface (Table 2). Both of these parameters have a strong impact on the activated biocarbons adsorption capacity. The average pore size of both adsorbents is approximately 2 nm, which allows to classify these materials as mesoporous. The surface of examined solids is dominated by basic functional groups, the concentration of which for NE_AP material is about 14 times higher than acid groups. The points of zero charge (pzc) occur at pH 8.5 and 9.7 for nettle- and mint-based samples, respectively, which confirmed the alkaline properties of both adsorbents. On the other hand, the isoelectric points (iep) of activated biocarbons (iep) are located at pH below 3 for NE-AP activated biocarbon and at pH 3.5 for MT_AP one, which are significantly lower than the pzc values. It may be the result of partial overlapping of the electrical double layers (edl) formed on the walls of the pores, which is a phenomenon often observed for mesoporous materials (Skwarek et al., 2014; Szewczuk-Karpisz et al., 2021).

Figure 2 presents the SEM images of the activated biocarbons. Despite the elongated shapes present in the structure of both materials, their surface layers differ significantly. The structure of NE_AP biocarbon is characterized by the presence of round holes and small pieces/particles on the surface. In the case of MT_AP material, the accumulation of smaller pieces on the surface is greater, beneath which a ribbed structure can be observed. These varied textural structures correspond to the activated biocarbons surface area, which is much greater in the case of the MT_AP sample.

According to the data presented in Table 3 and in Figure 3, both materials are characterized by a high carbon content exceeding 75 at%. The structure of both activated biocarbons is clearly dominated by C=C groups. Furthermore, the contents of C-C, C-H, C-OH, C-O-C, C=O and carbonate species are similar in both solids. The second most abundant element is oxygen, with a concentration of about 13 at%. In the case of NE_AP activated biocarbon the contribution of carbonyl groups is the highest, while for the material obtained from mint herb residue, the contents of hydroxyl, carbonyl, and ether groups are at a similar level. In turn, the share of carboxyl groups is the lowest in both solids. The content of nitrogen does not exceed 2 at%, although the XPS tests confirm the presence of pyridinic, pyrrolic and amine groups. XPS analysis also revealed the presence of mineral admixtures in the structure of the obtained activated biocarbons, which is a fairly typical phenomenon for carbonaceous materials produced from plant-derived waste biomass.

The results of elemental analysis (summarized in Table 4) confirmed that carbon is the main component of the obtained materials. The high oxygen content is related to the large number of functional groups introduced as a result of partial gasification of the carbon matrix during heat treatment in the CO₂ atmosphere. The obtained data also indicate a high ash content in the obtained activated biocarbons. This is a consequence of the presence of numerous mineral admixtures in the structure of the starting materials, which do not decompose during the activation process.

Table 5 presents the results of the XRF analysis. No heavy metals were found in the composition of activated biocarbons, which proves that the obtained materials will not have a negative impact on the environment and their disposal should not pose any problems. The data show that, in addition to elements such as C, H, N, S, and O, both biocarbons also contain considerable amounts of phosphorus, calcium (particularly the sample derived from nettle) and potassium (especially the MT_AP material).

The greatest adsorption of polyethyleneimine occurs at pH 3 (Figure 4a). Under these conditions, positively charged polymer chains are repulsed electrostatically by the positively charged adsorbent surface, forming an adsorption layer with perpendicular-orientated macromolecules. In turn, the increasing pH value causes the surface charge of the activated biocarbon to become negative, which results in the attractive interaction between the cationic polymer and adsorbent. The number of macromolecules adsorbed in parallel orientation increases, while the packing density of the adsorption layer decreases. Poly(acrylic acid) is also adsorbed in the greatest amount at pH 3 and its adsorption efficiency decreases with increasing pH. In this case, similarly to PEI, it is related to changes in the polymeric chain conformation (Figure 4b). At low pH values, most of the carboxyl groups is fully protonated and poly(acrylic acid) chains occur in a coiled conformation. The higher the pH is, the more PAA functional groups dissociate. This causes significant development of polymer chains, which create loosely packed adsorption layers and consequently lead to a reduction in the amount of adsorbed substance (Gęca et al., 2024a). The maximum adsorbed amounts of polymers observed in this study are higher than most values reported in the literature. The adsorption capacity of inorganic materials (such as metal oxides) towards ionic polymers does not exceed 30 mg/g (Alemdar et al., 2005; Chibowski et al., 2009; Liufu et al., 2005; Santhiya et a. 1999). In the case of activated carbons, the obtained results are comparable to our previous findings for carbonaceous materials derived from sage and lemon balm stalks via physical activation (Groszek et al., 2025).

The removal of cadmium(II) ions from an aqueous solution is less influenced by pH value compared to the polymers, but it is slightly more efficient at pH 6 (Figure 4c). In the case of As(V) ions, their adsorbed amounts are very low and similar in all systems (Figure 4d). The obtained isotherms data were fitted to theoretical models (Table 6). Both heavy metal ions’ adsorption is best described by Freundlich and Dubinin-Radushkevich models, which indicates that the adsorption process takes place inside the pores and leads to the formation of multilayer adsorbate films (Foo and Hameed, 2010). The maximum adsorbed amounts of cadmium ions reported in the literature often exceed 100 mg/g, but the adsorbents used in these studies were mainly synthesized using aggressive chemical reagents (Meng et al., 2024; Tan et al., 2022; Yin et al., 2023). The amounts of Cd(II) ions adsorbed on the surface of environmentally friendly adsorbents are comparable to the values obtained in the presented studies (Anwar et al., 2010; Farasati et al., 2016). The adsorption of As(V) ions has been studied primarily using novel, chemically modified inorganic materials, whose adsorption capacity ranges from 30 to 200 mg/g (Đolić et al., 2021; He et al., 2023; Wu et al., 2022). In contrast, the application of eco-friendly carbonaceous materials for As(V) ions removal has been investigated to a very limited extent.

The adsorption kinetics results of the examined polymers are shown in Figure 5. The equilibrium state was reached after 6 h in the case of PEI and after 2 h in the case of PAA. This difference can be related to the size of both macromolecules at pH 3. The coiled poly(acrylic acid) molecules migrate faster through the bulk solution towards the adsorbent surface layer than the developed polyethyleneimine chains. The calculated theoretical parameters are listed in Table 7. Both polymers adsorption kinetics are better described by pseudo second-order model. This indicates that the polymer’s adsorption on the activated biocarbons surface involved mainly electron exchange between adsorbent and adsorbate (chemical adsorption mechanism). Due to the presence of functional groups–carboxyl in the case of PAA, and amine in the case of PEI, hydrogen bonds can be formed between the polymeric chains and the functional groups present on the activated biocarbons surface (Wiśniewska et al., 2021).

According to the analysis of data presented in Figure 6, for most of the tested systems, activated biocarbon obtained from the nettle herb is a more effective adsorbent from both single and mixed adsorbate solutions. This confirms that the concentration of surface functional groups is of great importance for the adsorption capacity of carbonaceous material.

Poly(acrylic acid) and polyethyleneimine have a positive influence on their mutual adsorption (Santhiya et al., 1999). The adsorbed polymer chains can bind other macromolecules from the solution, forming multilayer adsorption structures (Gęca et al., 2024b). This effect is more noticeable in the case of PAA adsorption in the presence of PEI. Cationic polymer macromolecules are characterized by the larger linear dimensions at pH 3, which results in a greater number of amine functional groups that can interact with carboxyl groups of PAA. In the opposite situation, the coiled chains of the anionic polymer have fewer available functional groups, resulting in a smaller increase in PEI adsorption.

In solutions containing both the cationic polymer PEI and Cd(II) ions, the adsorbed amounts of each component from the binary mixture are lower than in the corresponding single-component systems. This behaviour is characteristic of cadmium cations in multicomponent systems. In solutions containing Cd(II) together with Pb(II)/Zn(II), the amount of adsorbed cadmium ions is reduced by 40%–80% compared to a single-component Cd(II) systems (Lee and Shin, 2021; Wang et al., 2022; Li et al., 2023). Both substances with the same ionic character compete for active sites, which negatively impacts their simultaneous removal from the aqueous phase. In a binary solution of poly(acrylic acid) and cadmium(II) ions, polymer-metal complexes are created, which depending on the type of adsorbent can be adsorbed on the activated biocarbons surface or remain in the solution. However, PAA is generally adsorbed in greater amounts from the binary solution than the Cd(II) cations. The presence of As(V) anions causes a decrease in the amounts of both polymers adsorbed. Moreover, the presence of the macromolecular compounds completely inhibits the adsorption of inorganic anions. This phenomenon can be attributed to the formation of complexes between arsenic(V) ions and organic substances, which rather tend to remain in the solution than adsorb on the surface (Gęca et al., 2024c). Conversely, it has been shown that the presence of small amounts of inorganic compounds can increase the amount of As(V) adsorbed on the surface of chemically modified adsorbents. These findings emphasize the need for more detailed studies on the removal mechanisms operating in multicomponent systems (Wei et al., 2021; Zeng et al., 2024).

The desorption efficiency of the polymers is presented in Figure 7. Due to the impossibility of determining the concentration of polyethyleneimine in a solution with high ionic strength, in the case of this polymer only water was used for desorption tests. The most efficient desorption was observed in systems with As(V) ions, which can be related both to the small amount of adsorbed PEI and the weak binding of the polymer-metal complex to the adsorbent surface. The lowest desorption obtained in the NE_AP + PEI + PAA system indicates the strongest polyethyleneimine affinity to the surface of activated biocarbon derived from the nettle herb in the presence of poly(acrylic acid). In other systems the PEI desorption efficiency was about 50%.

In the case of PAA, H₂O was the least effective desorption agent. HNO₃ turned out the most effective substance in the single and PAA + PEI systems. In the presence of metal ions, NaOH allowed achieving the highest level of desorption. In general, the anionic polymer is better desorbed from the surface of MT_AP activated biocarbon, which proved that more than twice lower concentration of the adsorbent functional groups is crucial for the PAA removal from the aqueous solution.

According to the data presented in Figure 8 the adsorbed amount of PEI increases with the increasing number of cycles. Due to the incomplete desorption (Figure 8b) of the cationic macromolecule and its perpendicular adsorption, the number of solid active sites increases. The permanently bonded PEI chains modify activated biocarbons’ surface, increasing their adsorption capacity. On the other hand, the PAA adsorbed amount decreases in the subsequent cycles. It is related to the adsorption of coiled polymeric chains in the solid pores, which remain not desorbing, blocking these sites for other PAA macromolecules.

The dependencies of the surface charge density (σ₀) of the activated biocarbons, for the systems without as well as with single and binary adsorbates, as the function of solution pH are presented in Figure 9. Polyethyleneimine causes an increase in activated biocarbons surface charge density value, whereas the presence of poly(acrylic acid) decreases this parameter value. In both cases, it is related to the fact that not all segments of the adsorbed macromolecules are directly bound to the adsorbent active sites. The functional groups are also present in the loop and tail structures, located in the by-surface area, which increase or decrease the σ₀ parameter, according to the adsorbate chain charge (Wiśniewska and Nowicki, 2020). In the binary solution of two polymers, the intermediate value of the σ₀ is observed. However, the predominant impact of PAA is noticeable, due to its greater adsorption in the studied system.

In the solution containing As(V) ions, a slight increase in the surface charge density is observed. The adsorbing arsenic anions induce the creation of an additional number of surface groups with a positive charge. On the other hand, the adsorption of Cd(II) cations favours formation of additional number of negatively charged sites on the activated biocarbons surface, resulting in a decrease of surface charge density. It is a typical behaviour observed for small inorganic ions (Fijałkowska et al., 2019). In the systems of ionic polymers and heavy metal ions, the effects accompanying macromolecules adsorption have a predominant impact on the σ₀ value, due to their large sizes and significantly greater adsorbed amounts.

The changes of zeta potential (ζ) of the activated biocarbons particles dispersed in the systems without as well as with single and binary adsorbates as the function of solution pH are shown in Figure 10. Polyethyleneimine adsorption causes an increase in zeta in zeta potential value, which can be explained by the presence of polymeric chains with the positively charged amine groups in the slipping plane area. Anionic polymer binding leads to a decrease in the ζ value as a result of the analogous mechanism (Gęca et al., 2022). The zeta potential in the suspension containing both polymers increases at low pH values, at which the dissociation of the PEI chain is the greatest. The higher the pH value is, the greater the dissociation of carboxyl groups present in the PAA molecules is, and the resultant lowering of electrokinetic potential value is noted.

In the presence of Cd(II) ions the zeta potential value increases. The change of the ζ value to less negative after divalent cations (Cd²⁺) adsorption in comparison to monovalent supporting electrolyte ones (Na⁺) is a common effect, described in the literature before (Yalçınkaya and Güler, 2006; Yukselen-Aksoy and Kaya, 2011). Due to the small adsorbed amount of the As(V) ions, their influence on the zeta potential value is not very noticeable. In the system containing Cd(II) ions and polymers, an intermediate effect to their single solutions is observed, whereas the simultaneous presence of polymers and arsenic(V) ions results in obtaining dependencies similar to those observed for single PAA or PEI systems.

The aggregate sizes of activated biocarbons suspensions without as well as with single and binary adsorbates are included in Table 8. In single adsorbate systems, the adsorbent aggregate sizes increase in comparison to the suspensions without additives. The adsorption layers of organic/inorganic substances can cause the attraction between activated biocarbons particles resulting in suspension destabilization. The small metal ions neutralize the activated biocarbons’ surface charge which results in the coagulation of solid particles, whereas the polymeric chains in addition to the charge neutralization can also cause the bridging flocculation. Similar effects are observed in the binary systems containing As(V) ions, whereas the influence of Cd(II) ions in the presence of ionic polymers depends on the adsorbent type. On the other hand, the simultaneous presence of PEI and PAA has a stabilizing influence on the suspension. It can be explained by the interchain complexes creation which prevents the attraction between adsorbent particles (oppositely charged polymers neutralize each other’s charge).