Chromium(VI) reduction and accumulation on the kaolinite surface in the presence of cationic soil flocculant



Heavy metal soluble forms pose a threat to plants, soil microflora, and microfauna. To limit their toxicity and mobility, various immobilizing additives are being developed. The main aim of the study was to determine the influence of soil flocculant (cationic polyacrylamide (CtPAM)) on the hexavalent chromium ion reduction and accumulation on the kaolinite surface. In this way, the efficiency of the selected polymer conditioner in the soil remediation was determined.

Materials and methods

The adsorbed amounts of Cr(VI) and CtPAM on the kaolinite surface was determined spectrophotometrically (spectrophotometer UV/Vis) using specific indicators. The structure of electrical double layer formed on the kaolinite surface in the mixed system of cationic polyacrylamide and Cr(VI) ions was described based on the adsorptive measurements, zeta potential measurements, as well as potentiometric titration. The kaolinite aggregation in the presence of CtPAM and/or Cr(VI) ions was determined spectrophotometrically and proved using SEM microscopy. The reduction process of Cr(VI) to Cr(III) occurring in the adsorption layer was determined by diffuse reflectance spectroscopy (DRS).

Results and discussion

The obtained results indicated that cationic polyacrylamide contributes to Cr(VI) reduction to Cr(III) form in the kaolinite suspension. This heavy metal ions are strongly adsorbed by the applied clay mineral, especially at pH 5 (then the Cr(VI)-adsorbed amount equals 5.42 mg/g). The CtPAM addition favors the Cr(VI) ion immobilization on the kaolinite surface. In the conditioner presence, the heavy metal-adsorbed amount is even at 7.34 mg/g. The adsorption of CtPAM and chromium(VI) ions induces changes in the kaolinite surface charge density and electrokinetic potential. What is more, both substances favors the kaolinite aggregation.


Cationic polyacrylamide may be considered a substance reducing the toxicity of chromium(VI) ions in the natural environment and decreasing their availability for soil organisms. It can improve the soil structure (by stimulating aggregation) and reduce environment pollution with heavy metals simultaneously.

Graphical abstract


Soil environment pollution with heavy metals is a threat to the proper functioning of organisms (Kilic et al. 2011). In contrast to pollution with organic compounds (such as aromatic hydrocarbons) heavy metals are not biodegradable and remain in the soil for thousands of years. They limit the number, activity, and biodiversity of microorganisms and plants (Alkorta et al. 2004). Most of heavy metals such as Cr, Pb, Cd, and Hg have toxic effects on the organisms at minimal concentrations. The chromium toxicity depends on its oxidation stage. Chromium(VI) is much more hazardous than the chromium(III) one. Cr(VI) has a strong carcinogenic and mutagenic effects. It is considered as an allergenic factor which has high permeability through biological membranes and ability to oxidize unsaturated bonds in fatty acids, nucleic acids, and proteins (Vinutha et al. 2015; Hedberg et al. 2014; Dhal et al. 2013).

In response to the growing environment pollution, many remediation technologies for contaminated soils have been developed. One of them is immobilization (phytostabilization). This method involves the use of plants and various additives for stabilization of pollutants (Choppala et al. 2015; Borymski and Piotrowska-Seget 2014; Al-Mashqbeha et al. 2018). There are two types of immobilization: chemical and physical. They rely on metal ion binding and immobilizing based on covalent or ionic bonds as well as toxic forms capturing in complex polymer structures (Singh et al. 2012; Shi and Fernandez-Jimenez 2006; Hazrat et al. 2013; Ford and Neuman 2006; Weng et al. 2002). Materials used in such processes may be as follows: biochar, activated carbons, clay minerals, plant materials, polymers, and modern nanomaterials (Alkorta et al. 2004; Xiao et al. 2017; Roth et al. 2012; Fan et al. 2015). Owing to immobilization , the heavy metals uptake by plants and their leaching during surface runoff are reduced. This technique may be associated with sorption, ion exchange, redox processes, stable complex formation with organic matter, and their precipitation.

Toxic compound bioavailability depends mainly on their solubility in soil solution (Kwiatkowska-Malina and Maciejewska 2012; McLaughlin et al. 2000). Soluble forms are of particular importance because they pose a threat to plants, soil microflora, and microfauna. Soil organic matter content influences the substance solubility significantly (Ashworth and Alloway 2004; Cao et al. 2003; Xiao et al. 2017; Roth et al. 2012). Heavy metals associated with organic matter, mainly in the form of high-molecular organometallic complexes, are usually insoluble in water. Unfortunately, due to the constantly deteriorating soil condition, the organic matter content becomes lower and lower. What is more, soil acidification observed in many regions favors the mobility of toxic forms additionally. Thus, the study on innovative additives (e.g., clay minerals associated with polymers) that may immobilize heavy metals and reduce their bioavailability is of high importance. In the literature there is a lack of information about Cr(VI) mobility in the soil modified by flocculants.

Taking the above into consideration, the main aim of the study was to determine the influence of cationic polyacrylamide (CtPAM, soil flocculant) on the hexavalent chromium ion reduction and adsorption on the kaolinite surface. On the other hand, the Cr(VI) ion effect on the CtPAM-adsorbed amount on this mineral surface was also described. The structure of electrical double layer formed on the kaolinite surface in the presence of cationic polyacrylamide and/or Cr(VI) ions was studied using UV/Vis spectrophotometry, zeta potential measurements, as well as potentiometric titration. The kaolinite aggregation after the addition of cationic polymer and/or Cr(VI) ions was examined by spectrophotometric method and observed using SEM microscopy. The presented results provided information on sorption capacity of kaolinite relative to heavy metal ions and cationic polyacrylamide. It was examined whether the selected clay mineral may be used as soil additive which maintains its sorption capacity under specific environmental conditions (e.g., in the presence of soil flocculant). Performed experiments are part of the research on electrokinetic and adsorptive properties of various solids. Previous study concerned, inter alia, chromium(III) oxide adsorption capacity relative to anionic polyacrylamide (Wiśniewska et al. 2014b) and mixed flocculant (Wiśniewska et al. 2019).



CtPAM (Korona), characterized by different contents of dissociable groups (35 or 80% of quaternary amine groups) with an average molecular weight equal to 7000 kDa, was used in the study. The CtPAM containing 35% of ionizable groups was marked as CtPAM-35, whereas that containing 80% of ionizable groups—CtPAM-80. The pKb values of CtPAM-35 and CtPAM-80 equal 9.3 and 9.5, respectively. The dissociation degrees of cationic groups present in the polymer macromolecules are 99.9% (at pH 5) and 99.4–99.6% (at pH 7).

Kaolinite (Sigma-Aldrich)—a clay mineral belonging to the aluminosilicates, was used as an adsorbent. It has a 1:1 structure, in which tetrahedrons of silica and octahedrons of alumina form layers. The SiO4 and Al(OH)6 sheets are bonded together by shared common plane of oxygen atoms or hydrogen bonds. The specific surface area (SBET) and porosity of kaolinite were determined using the nitrogen adsorption/desorption isotherm method (Micromeritics ASAP 2020 analyzer). The elemental composition of kaolinite was obtained by means of XRF technique (Panalytical ED-XRF type Epsilon 3 spectrometer). Surface functional groups of kaolinite was determined using the Fourier-transform infrared spectroscopy (FTIR spectrometer, Nicolet 8700A, Thermo Scientific).


All experiments were performed at 25 °C in the presence of NaCl (with concentration 0.001 mol/dm3) as a supporting electrolyte.

Adsorption measurements were carried out at pH 5 and 7 (common pH values of cultivated soils). The Cr(VI)- or CtPAM-adsorbed amount on the kaolinite surface was determined based on the concentration changes in the solution noted after the adsorption. The Cr(VI) and CtPAM concentrations were established spectrophotometrically (spectrophotometer UV/Vis Carry 1000, Varian). In the case of chromium(VI) ions, the reaction with diphenylcarbazide (Gardner and Comber 2002) was used, whereas in the case of CtPAM, the procedure with brilliant yellow in alkaline environment (pH 9) was applied. The suspensions were prepared using 0.1 g of the solid (per 10 cm3 of the solution). The Cr(VI) ion concentration in the probes was in the range of 1–200 ppm, in turn the CtPAM one—20–200 ppm. The adsorption was conducted for 24 h under shaking conditions (250 rpm). After its completion, the samples were centrifuged and the Cr(VI)/CtPAM concentration was established in the obtained supernatants. The obtained data were fitted to selected theoretical models, i.e., Langmuir (Eq. 1) and Freundlich (Eq. 2) (Ościk 1969; Foo and Hameed 2010):

$$ {q}_{\mathrm{e}}=\frac{q_{\mathrm{m}}{K}_{\mathrm{L}}{C}_{\mathrm{e}}}{1+{K}_{\mathrm{L}}{C}_{\mathrm{e}}} $$
$$ {q}_{\mathrm{e}}={K}_{\mathrm{F}}{C}_{\mathrm{e}}^{1/n} $$

where KF (mg/g(mg/L)−1/nF) is the Freundlich parameter, KL (L/mg) is the Langmuir parameter, qe (mg/g) is the equilibrium adsorption capacity, Ce is the equilibrium liquid phase concentration (ppm), qm is the maximum adsorption capacity in Langmuir model (mg/g), and n is the Freundlich constant related to adsorption intensity.

Kinetics of Cr(VI) and CtPAM adsorption on the kaolinite surface were also examined. These measurements were performed at pH 5, using 100 ppm of CtPAM or 5 ppm of Cr(VI) ions. The kaolinite weight in the suspensions was 0.1 g (per 10 cm3 of the solution). After the samples preparation and the pH adjustment, the adsorption was conducted for 5, 10, 20, 30, 40, 50, 60, 90, 120, and 180 min under shaking conditions. After the process completion, the suspensions were centrifuged and the Cr(VI) ions or CtPAM concentration was established in the obtained solutions. The kinetics results were fitted to the pseudo-first-order (Eq. 3) and pseudo-second-order equations (Eq. 4) (Ho and McKay 1998; Ho and McKay 2002):

$$ \frac{\mathrm{d}{q}_t}{\mathrm{d}t}={k}_2\left({q}_{\mathrm{e}}-{q}_{\mathrm{t}}\right) $$
$$ \frac{\mathrm{d}{q}_t}{\mathrm{d}t}={k}_2{\left({q}_{\mathrm{e}}-{q}_{\mathrm{t}}\right)}^2 $$

where qe is the adsorbed amount at equilibrium (mg/g), qt is the adsorbed amount after time “t” (mg/g), and k1 (1/min) and k2 (g/(mg* min) are the equilibrium rate constants.

The surface charge density (σ0) of kaolinite in the absence and presence of cationic polyacrylamide and/or Cr(VI) ions was determined using the potentiometric titration method, which was carried out applying an automated set co-working with the Titr_v3 software (Janusz 1994). A single titration was performed in the pH range of 3–11. The suspensions (with a volume of 50 cm3) were prepared using 2.5 g of kaolinite. The Cr(VI) ion concentration was 1 ppm, whereas the CtPAM one—100 ppm.

The electrophoretic mobility of the kaolinite particles dispersed in the solution non-containing and containing polyacrylamide and/or Cr(VI) ions was measured using the zetasizer Nano ZS (Malvern Instruments). At first, 100 cm3 of the suspension was prepared using 0.1 g of kaolinite. Then, the system was sonicated for 3 min and divided into several parts, in which different pH values were adjusted (changing in the range 3–9). Based on the measured electrophoretic mobility values, the electrokinetic potential (ζ) was calculated using a special software and Henry’s equation (Ohshima 1994).

The reduction process of Cr(VI) to Cr(III) occurring in the CtPAM adsorption layer was determined by diffuse reflectance spectroscopy (DRS). The DRS spectra were measured using the Jasco V-660 spectrometer equipped with diffuse reflectance attachment PIV-756 (Jasco, Japan). After the adsorption process, the solid samples were centrifuged, dried, and exposed to the UV-Vis beam. The deconvolution procedure of the obtained spectra was applied to separate the signals coming from various forms of chromium.

The changes in the soil suspension stability without and with CtPAM and/or Cr(VI) ions was monitored using spectrophotometry method (spectrophotometer Carry 1000, Varian). The absorbance of clay mineral suspension was measured over time at a wavelength equal to 500 nm. The cationic polyacrylamide concentration in the examined systems was 100 ppm, in turn the Cr(VI) ion one—1 ppm. The kaolinite aggregation was also observed using SEM microscope (Quanta 3D FEG, FEI Company).

The electrokinetic mobility, stability, and surface charge density measurements were performed three times for a given system. The measurement error did not exceed 2–3%, and therefore, error bars were not added to the result diagrams. Adsorption measurements (adsorption kinetics and isotherms) were also performed three times for the selected system. The measurement error was larger—about 5–6%, and thus error bars were added to the diagrams.

Results and discussion

Kaolinite characteristics

Based on the obtained nitrogen adsorption/desorption isotherms, it was stated that specific surface area (SBET) of kaolinite equals to 8.02 m2/g. The mineral contains two groups of mesopores of the following average diameters, 3.8 and 11.7 nm. The XRF measurements indicated that kaolinite was composed of Si (22.2 wt%), Al (19.6 wt%), K (1.5 wt%), Fe (0.337 wt%), and P (0.189 wt%) and trace elements such as Na, Mg, Cr, Rb, or Zn.

The FTIR analysis showed the specific functional groups of the examined kaolinite. The obtained spectrum, presented in Fig. 1, contains the bands corresponding with: (1) the Si–O stretching vibrations (429, 469, and 597 cm−1), (2) the Mg/Al-OH vibrations (698 cm−1), (3) the Si–O–Al group deformation (765 and 796 cm−1), (4) the OH bending vibrations of Al-OH (911 cm−1), (5) the Si–O stretching vibrations (1006, 1030, and 1114 cm−1) (Gild et al. 2017; Tironi et al. 2012; Ogundiran and Winjobi 2015). The four bands present at 3619, 3651, 3671, and 3696 cm−1 corresponds with the stretching of OH groups. They are well defined, which confirmed that the kaolinite structure is ordered (Bich et al. 2009).

Fig. 1

FTIR spectrum of kaolinite

The σ0 and zeta potential (ζ) of kaolinite in the supporting electrolyte solution are presented in Fig. 2. The obtained results showed that both σ0 and ζ parameters depend strictly on the solution pH. When the pH value increases, the surface charge density of kaolinite reaches more negative values. It is connected with dissociation of functional groups present on the mineral surface. The pHpzc (point of the zero charge) of kaolinite equals 3.37. At this pH value, the concentrations of positively and negatively charged surface groups are identical. The obtained pHpzc parameter is consistent with the literature reports (Yukselen-Aksoy and Kaya 2003). Electrokinetic potential of kaolinite in the supporting electrolyte solution assumes only negative values in the whole studied pH range. What is more, the absolute values of negative zeta potential become higher and higher when the system pH increases. The obtained data indicated that the isoelectric point (pHiep) of kaolinite assumes the value lower than 3. According to the literature, pHiep of kaolinite is in the range of 2.8–4 (Ndlovu et al. 2015).

Fig. 2

Surface charge density (open points) and zeta potential (solid points) of kaolinite in the supporting electrolyte solution

Cr(VI) ions adsorption on the kaolinite surface and its effect on the solid σ0 and ζ parameters

Figure 3a presents the kinetics of Cr(VI) ion adsorption on the kaolinite surface at pH 5. The obtained results showed that the system reaches the equilibrium state after 50 min. After this time, the adsorbed amount of heavy metal ions on the kaolinite surface does not change. The obtained results were fitted to the pseudo-second-order model with R2 value equal to 0.963 (Table 1). This indicates that Cr(VI) adsorption involves chemisorption (Wang et al. 2007).

Fig. 3

Chromium(VI) ions adsorbed amount (a) and adsorption kinetics (b) on the kaolinite surface

Table 1 Kinetics parameters acquired from pseudo-first- and pseudo-second-order models of Cr(VI) ion adsorption on the kaolinite surface at pH 5

Figure 3b shows the Cr(VI) adsorption isotherms on the mineral surface obtained at pH 5 and 7. These results were fitted to Langmuir and Freundlich models (Table 2). The best fitting was obtained for Langmuir model—R2 is 0.953 at pH 5 and 0.994 at pH 7. This means that chromium(VI) ions form a monolayer on the kaolinite surface during the adsorption. Moreover, the adsorption energy distribution in the formed monolayer is uniform (Ościk 1969). In aqueous solutions, chromium occurs in various species depending on the pH value. In the examined pH range (3–9), the most stable forms of this heavy metal are HCrO4 and CrO42− anions (Weng et al. 2008; Fijałkowski et al. 2012). Due to higher values of negative surface charge of the mineral at pH 7, the affinity of chromium(VI) ions to the kaolinite surface is lower under these conditions (compared to pH 5). The σ0 parameter of kaolinite is about − 9 μC/cm2 at pH 5 and − 33 μC/cm2 at pH 7. At pH 5, for the initial chromium(VI) ion concentration equal to 100 ppm, their adsorbed amount on the kaolinite surface was equal to 5.42 mg/g, which means that the examined mineral adsorbs 54.2% of the heavy metal ions. In turn at pH 7, for the same initial concentration, the Cr(VI)-adsorbed amount was 4.71 mg/g, which indicated that 47.1% of the ions are adsorbed.

Table 2 Langmuir and Freundlich isotherm parameters for Cr(VI) ion adsorption on the kaolinite surface

In Figs. 4 and 5, the surface charge density and zeta potential of the kaolinite particles without and with hexavalent chromium ions are presented. The addition of Cr ions to the system causes significant changes in the σ0 and ζ parameters. The negative electrokinetic potential of the mineral in the heavy metal presence has higher absolute values than that observed in the supporting electrolyte solution. This is probably caused by the presence of inorganic anions in the slipping plane area formed around kaolinite particles. The changes in surface charge density of kaolinite after the Cr(VI) addition were also observed (Fig. 5). The decrease in the negative σ0 values in the chromium anion presence was noted in the whole examined pH range (3–9). Based on the site-binding model (Wiśniewska et al. 2017), the above phenomenon is associated with interaction of chromium(VI) ions with the kaolinite surface groups resulting in the creation of additional number of positively charged surface sites.

Fig. 4

Zeta potential of kaolinite in the absence and presence of Cr(VI) ions and/or cationic polyacrylamide

Fig. 5

Surface charge density (σ0) of kaolinite in the absence and presence of Cr(VI) ions and/or cationic polyacrylamide

Cationic polyacrylamide adsorption on the kaolinite surface and its effect on the solid σ0 and ζ parameters

The cationic polyacrylamide adsorption kinetics on the kaolinite surface are presented in Fig. 6a. Based on these results, it can be stated that the examined systems containing CtPAM (CtPAM-35 or CtPAM-80) reach equilibrium after 1 h. The kinetics results were the best fitted to the pseudo-second-order model. R2 was 0.964 for CtPAM-35 and 0.978 for CtPAM-80 (Table 3).

Fig. 6

Cationic polyacrylamide adsorption size (a) and kinetics (b) on the kaolinite surface

Table 3 Kinetics parameters acquired from pseudo-first- and pseudo-second-order models of cationic polyacrylamide adsorption on the kaolinite surface at pH 5

The polymer-adsorbed amounts on the kaolinite surface obtained at pH 5 and 7 are presented in Fig. 6b. The CtPAM adsorption on the kaolinite surface is the result of several interactions: compensation or neutralization of solid surface charge, solid-polymer complexes creation, and hydrogen bridges formation. At the examined pH values (5 and 7), cationic polyacrylamide has expanded conformation due to high dissociation degree value (over 99%). The electrostatic repulsion occurs between CtPAM functional groups and, owing to it, the polymer segments are spaced apart. The examined cationic polyacrylamide samples differs in the dissociable group content, i.e., CtPAM-35 contains 35% of quaternary amine groups, whereas CtPAM-80—80% ones. When these groups undergo dissociation, the polymeric chains are positively charged (the –N(CH3)3+ groups are present in the macromolecules). Therefore, the CtPAM adsorption on the kaolinite surface is mainly affected by the electrostatic attraction between dissociated hydroxyl groups of the solid (–SO) and positively charged polymer moieties. The affinity of cationic macromolecules to the negatively charged kaolinite is stronger for the polymer containing higher number of positively charged groups. At pH 5, the CtPAM-35 adsorbed amount equals 2.31 mg/g, whereas the CtPAM-80 one—3.05 mg/g. At pH 7, the observed polymer-adsorbed amounts were slightly higher. They were 2.91 mg/g of CtPAM-35 and 3.37 mg/g of CtPAM-80. This phenomenon is dictated by stronger electrostatic attraction between adsorbate and adsorbent at higher pH value (the negative solid surface charge is higher).

The electrokinetic properties of the kaolinite/supporting electrolyte/CtPAM system are presented in Figs. 4 and 5. The addition of both cationic polymers to the suspension changes the surface charge density and zeta potential of the examined aluminosilicate. Electrokinetic potential of the solid assumes only positive values in the whole pH range. This is due to the presence of positively charged groups of the polymer in the slipping plane area. The absolute values of surface charge of kaolinite after the CtPAM addition are lower than those observed without the polymer. This effect is induced by positively charged moieties of “loop” and “tail” structures of the adsorbed macromolecules located in by-surface layer. The polymer with higher content of dissociable amine groups (CtPAM-80) has a stronger impact on the σ0 and ζ values—larger changes in these parameters are noted (Wiśniewska et al. 2014a).

Cr(VI) and cationic polyacrylamide adsorption on the kaolinite surface in the mixed systems

The Cr(VI) ion influence on the cationic polyacrylamide adsorption on the kaolinite surface at pH 5 and 7 is presented in Table 4. Heavy metal ions affect both CtPAM-35 and CtPAM-80 adsorbed amounts. In the experiments the concentrations of both the polymer and Cr(VI) ions were 100 ppm. Both adsorbates were added to the studied suspensions simultaneously or at the time interval of 1 h. Based on the obtained results, it can be stated that the chromium(VI) ions strongly determine the polymer-adsorbed amount on the kaolinite surface. When Cr(VI) ions were added after 1 h, the polymer-adsorbed amount is twice higher (compared with the system without heavy metal ions). This dependence is observed for both CtPAM-35 and CtPAM-80. When the adsorbates are added at the same time, the CtPAM-adsorbed amount increase is also clear. These observations can be related to the interaction between inorganic anions (HCrO4 and CrO42−) and positively charged macromolecules (containing –N(CH3)3+ groups). As a result, the formation of polymer-metal ion complexes occurs. Hydrogen bond creation between neutral undissociated amide groups of the polymer and chromium anions may also take place. What is more, the adsorbed polyacrylamide chains can capture heavy metal ions from the solution by hydrogen bridge formation.

Table 4 CtPAM-adsorbed amount on the kaolinite surface in the mixed Cr(VI)/CtPAM systems (Cr(VI) and CtPAM initial concentrations were equal to 100 ppm)

Chromium(VI) ion-adsorbed amount on the kaolinite surface is strictly dependent on the CtPAM presence. The obtained results are presented in Table 5. The noticeable increase in the chromium(VI) adsorption was obtained. A slightly higher Cr(VI)-adsorbed amount was observed when the polymer was added firstly to the kaolinite suspension. Similarly to the cationic PAM adsorption, due to interaction between opposite charged adsorbates, the heavy metal-polymer complexes are probably formed. Besides, negatively charged chromium(VI) ions have higher affinity to the kaolinite surface modified by polyacrylamide macromolecules containing positively charged moieties. This indicates that cationic polyacrylamide may be considered a substance favoring the chromium(VI) ion immobilization on the kaolinite surface.

Table 5 Cr(VI)-adsorbed amount on the kaolinite surface in the mixed Cr(VI)/CtPAM systems (Cr(VI) and CtPAM initial concentrations were equal to 100 ppm)

Electrokinetic potential of kaolinite in the presence of CtPAM and Cr(VI) ions assumes positive values. During the adsorption, the formed polymer-chromium(VI) ion complexes have such conformation that positively charged polymer groups are located in the slipping plane area of electrical double layer. They contribute to the described changes in the kaolinite zeta potential. On the other hand, the absolute values of surface charge of the mineral are lower after Cr(VI)/CtPAM addition (compared with the values noted without adsorbates). This is associated with the presence of CtPAM-positive groups in the non-adsorbed segments of the heavy metal-polymer complexes.

Cationic polyacrylamide influence on Cr(VI) reduction

Figure 7 presents the DRS spectra obtained in the kaolinite/cationic polyacrylamide/chromium(VI) ion system. They indicated that in the cationic polymer presence there is a clear reduction of chromium(VI) to chromium(III) in the mixed adsorption layer formed on the kaolinite surface. The peak corresponding with chromium(III) ions is visible in the diagram. The free electron pair located on the nitrogen atom of the polymeric amide group is involved in the described process. The Cr(VI) reduction to Cr(III) is highly desirable in environment protection because this process decreases the chromium toxicity for organisms.

Fig. 7

DRS spectra obtained in the kaolinite/cationic polyacrylamide/chromium(VI) ion system

Cr(VI) and cationic polyacrylamide impact on kaolinite aggregation

The stability of examined kaolinite suspension in the absence and presence of CtPAM/Cr(VI) ions is presented in Fig. 8. The system without any additives are more stable at pH 7 (the absorbance changes over time are slower), which is mainly connected with higher absolute values of zeta potential. The polymer addition (without or with chromium(VI) ions) changes the system stability—a significant reduction is observed both at pH 5 and 7. The absorbance decreases over time rapidly and remains at low level. Due to interaction between kaolinite surface groups and CtPAM moieties, the creation of large aggregates occurs. In the presence of Cr(VI), the kaolinite/CtPAM suspension becomes more unstable in comparison with those without heavy metal ions. This effect is greater for CtPAM-80 because in such a case the polymer-metal ion complexes are effectively formed and adsorbed on the solid particle surface, causing more efficient flocculation.

Fig. 8

Stability changes of the kaolinite suspension in absence and presence of Cr(VI) ions and/or cationic polyacrylamide at pH 5 (a) and pH 7 (b)

In Fig. 9, the SEM images of kaolinite particles in the presence and absence of cationic flocculant are presented. They also showed the solid aggregation process. There is a formation of flocs consisting of kaolinite particles covered with the CtPAM layers.

Fig. 9

SEM images of the kaolinite particles without (a) and with (b) cationic polyacrylamide


Based on the obtained results, the following conclusions can be drawn:

  1. (1)

    The adsorption of both CtPAM forms and chromium(VI) ions induces changes in the kaolinite surface charge density and electrokinetic potential (and also in the structure of electrical double layer of the mineral particles).

  2. (2)

    Cationic polyacrylamide adsorbs on the kaolinite surface. The CtPAM affinity to the mineral surface increases when the content of positively charged groups in the macromolecules as well as the pH value are higher.

  3. (3)

    Chromium(VI) ions are adsorbed on the kaolinite surface both at pH 5 and 7. When the pH value is lower, the larger adsorption capacity of the solid relative to Cr(VI) ions is observed.

  4. (4)

    Chromium(VI) ions favors the CtPAM adsorption on the kaolinite surface. Similarly, cationic polymer induces the Cr(VI) adsorption on the solid surface. These phenomena are associated with the polymer-heavy metal ion complex formation.

  5. (5)

    Cationic polyacrylamide causes the Cr(VI) reduction to the Cr(III) form in the mixed adsorption layer.

  6. (6)

    CtPAM presence (and also Cr(VI) ions in the mixed system) contributes to strong kaolinite aggregation.

  7. (7)

    The Cr(VI) ions are successfully immobilized and reduced in the soil mineral/cationic polyacrylamide system, which limits considerably this heavy metal availability for plants.


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Correspondence to Katarzyna Szewczuk-Karpisz.

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Szewczuk-Karpisz, K., Fijałkowska, G., Wiśniewska, M. et al. Chromium(VI) reduction and accumulation on the kaolinite surface in the presence of cationic soil flocculant. J Soils Sediments (2020).

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  • Cr(VI) reduction
  • Soil flocculant adsorption
  • Kaolinite aggregation
  • Heavy metal ion immobilization
  • Mixed layer of PAM and Cr(VI)