Evaluation of the Usefulness of Sorbents in the Remediation of Soil Exposed to the Pressure of Cadmium and Cobalt

An undesirable side effect of economic progress is increasingly severe pollution with heavy metals, responsible for the degradation of ecosystems, including soil resources. Hence, this research focused on examining six adsorbents in order to distinguish a reactive mineral with the highest capacity to remediate soils contaminated with heavy metals. To this end, the soil was polluted with Co2+ and Cd2+ by applying the metals in concentrations of 100 mg kg−1 d.m. The extent of soil equilibrium disturbances was assessed by evaluating the response of the soil microbiome, activity of seven soil enzymes, and the yields of Helianthus annuus L. Six sorbents were evaluated: a molecular sieve, expanded clay (ExClay), halloysite, zeolite, sepiolite and biochar. Co2+ and Cd2+ proved to be significant inhibitors of the soil’s microbiological and biochemical parameters. Organotrophic bacteria among the analysed groups of microorganisms and dehydrogenases among the soil enzymes were most sensitive to the effects of the metals. Both metals significantly distorted the growth and development of sunflower, with Co2+ having a stronger adverse impact on the synthesis of chlorophyll. The molecular sieve and biochar were the sorbents that stimulated the multiplication of microorganisms and enzymatic activity in the contaminated soil. The activity of enzymes was also stimulated significantly by zeolite and sepiolite, while the growth of Helianthus annuus L. biomass was stimulated by the molecular sieve, which can all be considered the most useful reactive materials in the remediation of soils exposed to Co2+ and Cd2+.


Introduction
Soil is a natural resource with an immeasurable value, albeit it is also finite and nonrenewable [1]. Rapid and uncontrollable urbanisation and industrialisation threaten the quality of soil and its long-term use, leading to the loss of its priority functions [2]. Excessive exploitation of soil by unsustainable agriculture inducing global-scale soil degradation is progressing at an alarming pace. Every year, around 10 million ha of arable land is considered to be unproductive [3], and the total growing area of degraded soils is now estimated at over 24% of the world's soils [2]. The key challenge is, therefore, to increase or maintain crop yields without causing further degradation of the Earth's ecosystems, in particular soils [4]. The challenge is further exacerbated by the growing demand for agricultural products for the rapidly growing human population in the world, predicted to reach 8.9 billion people in 2050 [5].
The problem of agricultural soil contamination with heavy metals calls for drastic and effective solutions [6]. Concentrations of these heavy metals surpassing the threshold values have negative effects on both the fertility of soils and on the growth, photosynthesis and productivity of crops, which in consequence, affects the health of humans and animals [7]. Apart from Cr, Ni, Cu, Zn, Pb, Hg and As, the list of most toxic heavy metals includes cadmium and cobalt [8,9]. ondary metabolites of plants and bacteria, bind heavy metals, including cadmium, or else enhance their mobilisation, thereby stimulating phytoextraction [39,40]. Furthermore, metallothioneins, rich in cysteine with four Zn 2+ or Cd 2+ binding sites, are engaged in the detoxication and storage of heavy metals. Cadmium is a metal that induces the synthesis of metallothioneins [41]. Microorganisms transform heavy metals to less toxic forms by methylation or redox reactions, which alter the solubility of heavy metals in soil [1,40]. During the process of biosorption, metal cations attach to the negatively charged cell surfaces and release exopolysaccharides (EPS) from cells, which stimulate the non-specific binding of metals [42]. It is also worth underlining that the pollution of soil with heavy metals creates a selective pressure, promoting species of bacteria that are resistant to this pool of heavy metals [43]. Because studies on changes in the quality of soil induced by heavy metals must be based on properties that respond rapidly to changes in the environmental stress, the biological indicator most often recommended, other than the response of microbiomes, is the activity of soil enzymes [44,45]. Heavy metals may produce an inhibitory effect on soil enzymes by interacting with the active sites of enzymes, complexes of substrates and by denaturation of proteins of these enzymes [46].
Two facts, namely the sunflower (Helianthus annunus L.) showing high tolerance to heavy metals [47] and the use of a wide range of sorbents for remediation of soils [23], gave rise to the imperative to conduct comprehensive studies in order to determine and compare the sensitivity of microorganisms and soil enzymes to the pressure of cadmium and cobalt in soil cropped with sunflower and submitted to remediation with the application of a molecular sieve, halloysite, sepiolite, expanded clay and biochar.

Soil
The type of soil used in the experiment is common in the north-eastern part of Poland. According to the FAO taxonomy [48], it is a Eutric Cambisol. The soil in a controlled plant-growing experiment was taken from the arable humic horizon, from a depth of 0-20 cm, at the Experimental Station in Tomaszkowo (NE, Poland, 53.713 • N, 20.432 • E). It was then transported to the Teaching and Experimental Centre of the University of Warmia and Mazury in Olsztyn (NE, Poland, 53.759 • N, 20.453 • E). In terms of the grain-size composition, it was sandy loam, containing 60.63% of sand (fractions 0.05-2.0 mm), 35.99% of silt (fractions 0.05-0.002 mm) and 3.38% of clay (fraction < 0.002 mm). The basic properties of the soil are presented in Table 1.

Procedure for Setting Up and Conducting the Experiment
Pot trials were conducted in a greenhouse in polyethene pots with a capacity of 3.0 dm 3 . The yearly average air temperature in the months when the experiment was carried out (June-July) in NE Poland was 17.7 • C, and the average rainfall was ca 83.5 mm. The experiment was conducted in three series with three replicates. The first series was composed of non-polluted soil, and the second one was set up on non-polluted soil with the sorbents, i.e., a molecular sieve, halloysite, sepiolite, expanded clay, biochar and zeolite Bio.Zeo.S.01, the third series consisted of soils polluted with cadmium and cobalt and four series were composed of polluted soil with cadmium and cobalt treated with the sorbents, i.e., a molecular sieve, halloysite, sepiolite, expanded clay, biochar and zeolite Bio.Zeo.S.01. All sorbents were applied in doses of 10 g kg −1 d.m. of soil. The heavy metals were applied in amounts of 0 and 100 mg kg −1 d.m. of soil. Cadmium was applied as 3CdSO 4 ·8H 2 O, and cobalt as CoSO 4 ·7H 2 O. Prior to packing soil, previously sifted through a sieve (5 mm mesh) to polyethene pots, each batch was mixed thoroughly with the sorbents, heavy metals and fertilisers, according to the experiment's design. The fertilisers N, P, K and Mg were applied in all series of the experiment once before sowing the crops. The soil was enriched with 110 mg N as CO(NH 2 ) 2 , 45 mg P as KH 2 PO 4 , 110 mg K as KH 2 PO 4 and KCl, and 20 mg Mg as MgSO 4 ·7H 2 O. Afterwards, the soil moisture content was raised to 60% by adding distilled water. The test plant was the sunflower Helianthus annuus L. The emergence of Helianthus annuus L. took place 5 days after sowing. The earliest pathological symptoms (yellowing) in the pots with cobalt were observed after 12 days. The sunflower's greenness index (SPAD) was determined at the stage of six leaves unfolded, that is, BBCH (Biologische Bundesanstalt, Bundessortenamt and Chemical Scale) 16, based on the content of chlorophyll determined with a MINOLTA SPAD 502Plus (KON-ICA MINOLTA, Langenhagen, Germany). The harvest of the sunflower's aboveground parts and roots was performed at stage BBCH 35.

Characteristics of Sorbents
A molecular sieve (Grace Davison Company, Columbia, New York, NY, USA) is hydrated aluminosilicate with micropores of a diameter less than 0.3 nm. This is a product sold under the trade name Silosiv A3. It is a zeolite with a three-dimensional pore system with pH KCl -8.5. Halloysite (Halosorb minerals sorbents, Intermark, Gliwice, Poland) is a silicate mineral (kaolinite group). This mineral is classified as a representative of clay minerals, Al 2 Si 2 O 5 (OH 4 ). It is the weathering product of the Tertiary basaltic rock. The pore diameter is 10-20 nm [62] [63,64]. Biochar (Fluid, Sędziszów, Poland) is produced from organic waste, such as wood production waste in sawmills, energy willow and miscanthus. It possesses a well-developed internal network of pores with a diameter of 5 to 50 nm [65]. Expanded clay (GardenGURU, Piła, Poland) is a light aggregate of grains 1.6-8 mm in size. It is burnt from loamy clay at 1150-1200 • C. Zeolite Zeolit Bio.Zeo.S.01 (BioDrain, Rzeszów, Poland) is a aluminosilicate mineral (the silicates). More detailed specification of the sorbents can be found in our earlier papers [66][67][68][69].

Microbiological Analyses
The microbiological assays of soil were made in 4 replications. The following were determined in soil samples: counts of organotrophic bacteria (Org), actinomycetes (Act) and fungi (Fun). Amounts of 10 g of soil were weighed and placed in flasks with sterile saline (90 cm 3 0.85% NaCl) and shaken on a laboratory shaker type 358A (Elpin, Mińsk Mazowiecki, Poland) for 30 min at 120 revolutions per minute. Dilutions of 10 −5 and 10 −6 were prepared to determine the counts of organotrophic bacteria and actinobacteria. Bacteria were isolated in Bunt and Rovira medium [56], actinomycetes-on Kuster and Williams medium (1971) with added nystatin and actidione [57]. In order to determine counts of fungi, dilutions of 10 −3 and 10 −4 were prepared. Fungi were isolated on Martin medium [58]. In order to verify the correctness of the sterilisation of media and 0.85% of NaCl during microbiological analyses, verification tests were carried out. All Petri plates with cultures were placed in an incubator (PSelecta Incudigit, Barcelona, Spain) at a temperature of 28 • C. The number of colony-forming units (cfu) was determined with a colony counter. Sums of colonies of microorganisms were calculated from the formula ISO 7218:2007/AMD 1:2013 [70]. In order to compute the colony development (CD) and ecophysiological diversity (EP) indices, colony-forming units of microorganisms were counted every day for 10 days. The CD (Formula (1)) and EP (Formula (2)) indices were determined according to De Leij et al. [71]: CD = [N 1 /1 + N 2 /2 + N 3 /3 . . . N 10 /10] × 100 (1) where: N 1 , N 2 , N 3 , . . . , N 10 is the sum of the ratios of the number of microbial colonies identified on individual days (1, 2, 3, . . . , 10) to the total number of colonies identified over the entire study period. EP = −Σ(pi × log 10 pi) (2) where: pi is the ratio of the number of colonies of microorganisms identified on individual days to the total number of colonies identified over the entire study period.

Enzymatic Analyses
The biochemical analyses of soil included determination of the activity of dehydrogenases (Deh), catalase (Cat), acid phosphatase (Pac), alkaline phosphatase (Pal), β-glucosidase (Glu) and arylsulphatase (Aryl). All determinations were repeated 3 times. The analysis of the activity of dehydrogenases (EC 1.1) was carried out in line with Lenhard's method modified by Öhlinger [59]. This method consists of the incubation of soil with water-soluble 2,3,5-triphenylthethrazole chloride (TTC), which is reduced to water-insoluble triphenylformazan (TPF). After 24 h soil incubation with calcium carbonate (in order to maintain conditions similar to natural ones), formazan is extracted from soil with ethyl alcohol. The results obtained in our study are expressed in µmol TPF kg −1 d.m. of soil h −1 . The method applied to determine the activity of urease (EC 3.5.1.5) involves the incubation of soil for 24 h with 10% urea solution as a substrate. The number of ammonium ions produced was measured using the Nessler reagent. The results were expressed in mmol N-NH 4 kg −1 d.m. of soil h −1 . Determinations of the activity of urease, acid phosphatase (EC 3.1.3.2), alkaline phosphatase (EC 3.1.3.1), arylosulphatase (EC 3.1.6.1) and β-glucosidase (EC 3.2.1.21) were made according to the procedure developed by Alef et al. [60]. The determination of the activity of acid phosphatase and alkaline phos-phatase consists of the incubation of soil in the presence of 4-nitrophenyl phosphate disodium salt 6-hydrate (PNPNa) as a substrate, which undergoes hydrolysis to 4-nitrophenol (PNP). The determination of the activity of arylsulphatase consists of the incubation of soil in the presence of potassium 4-nitrophenyl sulfate (PNS), β-glucosidase 4-nitrophenyl-β-Dglucopiranoside (PNG) as substrates. These substrates, same as in the case of phosphatases, hydrolyse to 4-nitrophenol (PNP). The activity of catalase (EC 1.11.1.6) was determined with the manganometric method according to Johnson and Temple [61]. This method consists of the decomposition of a solution of hydrogen peroxide into hydrogen and oxygen. The soil oxidation state was determined based on the reaction of decomposition of hydrogen peroxide using 0.02 M of a solution of potassium permanganate (KMnO 4 ). The results obtained from these analyses were presented in mol O 2 kg −1 d.m. h −1 . Determinations of the activity of all enzymes, except catalase, were made on a Perkin-Elmer Lambda 25 spectrophotometer (Waltham, MA, USA).

Physicochemical and Chemical Soil Analyses
Prior to the plant growing trials, the basic characteristics of the soil had been determined, and the results of these determinations are comprised in Table 1. The textural composition of the soil was determined with a laser molecular size meter Malvern Mastersizer 2000 Laser Diffraction (Malvern, Worcestershire, UK), while the hydrolytic acidity (HAC) and exchangeable base cations (EBC) of soil were measured according to the Kappen method [55]. Based on the HAC and EBC values, the cation exchange capacity (CEC) and base saturation (BS) were calculated. The content of total N (N tot ) was determined on a distillation unit Buchi B-324 (Buchi, Flawil, Switzerland), organic carbon (C org )-on a spectrophotometer Genesis 6 (Thermo Electron Corporation, Waltham, MA, USA), available phosphorus-on a spectrophotometer SQ118, potassium-Jenway PFP 7 flame photometer (Jenway LTD, Staffordshire, UK), and magnesium-on an atomic absorption spectrophotometer GBC 932AA, (GBC Scientific Equipment Australia. Exchangeable cations: K + , Ca 2+ and Na + , were determined using a flame photometer Jenway PFP 7 (Jenway LTD, Staffordshire, UK), and Mg 2+ -on an atomic absorption spectrophotometer Agilent 280 FS AA, (Agilent Technologies, Mulgrave, Australia). pH was measured with a HI 2221 pH meter (Hanna Instruments, Washington, UK). The content of cobalt in soil was determined on an ICI (International Electrotechnical Commission) spectrometer (Thermo Scientific; Waltham, MA, USA) according to standard ISO 11047:1998 [53].

Statistical Analyses
The results were processed statistically in a Statistica 13.0 software package [72]. Homogenous groups were distinguished with Tukey's test at p = 0.05. The analysis of variance ANOVA was run to calculate the coefficient η 2 , which reflected the contribution of particular independent variables to the shaping of dependent variables. By using the determined activity of soil enzymes, an index was calculated to display the effect of the tested sorbents and heavy metals on the activity of soil enzymes and crop yields. The following formula was employed: where: IF Ad -index of the influence of the adsorbent. IF Hm -index of the influence of heavy metals. Po-the activity of enzymes in the soil or the yield of plants after the use of sorbents/ contaminated with heavy metals. Co-enzyme activity or plant yield in unpolluted soil (no heavy metals) and without sorbents.
The calculated values of the indices IF Ad and IF Hm were presented with the help of software RStudio v1.2.5033 (Boston, MA, USA) [73], R v3.6.2 system (Vienna, Austria) [74] Materials 2022, 15, 5738 7 of 22 and the gplots library [75] on heat maps. The lowest values of the indices were shown in yellow colour, while the highest ones were in black. The blue line depicted in the colour key and histogram shows how many times each of the data appears in the matrix used in the heat map.

Counts of Microorganisms
The percent contribution of independent variables (η 2 ) determined in the study exposed the significant effect of heavy metals on the counts of fungi (50.62%) and organotrophic bacteria (53.26%) ( Figure 1). The application of reactive minerals and biochar induced slightly smaller changes in the counts of microorganisms. The extent of the moderating influence of the adsorbents oscillated between 29.88% for organotrophic bacteria to 35.66% for fungi. key and histogram shows how many times each of the data appears in the matrix used in the heat map.

Counts of Microorganisms
The percent contribution of independent variables (η 2 ) determined in the study exposed the significant effect of heavy metals on the counts of fungi (50.62%) and organotrophic bacteria (53.26%) ( Figure 1). The application of reactive minerals and biochar induced slightly smaller changes in the counts of microorganisms. The extent of the moderating influence of the adsorbents oscillated between 29.88% for organotrophic bacteria to 35.66% for fungi. Among the six analysed sorbents, few proved to be effective in stimulating the activity of the groups of microorganisms (Tables S1-S3). In non-polluted soil, the molecular sieve and biochar had the best effect on the count of organotrophic bacteria (Table S1) and expanded clay was most beneficial for actinobacteria (Table S2), while fungi responded positively to both expanded clay and biochar (Table S3). The stimulating effect of the reactive minerals and biochar on organotrophic bacteria was 36% and 25%, respectively, compared to 39% in the case of actinobacteria and 53% and 57% with respect to fungi. In the pots contaminated with Cd 2+ and Co 2+ , the positive effects of the sorbents were less spectacular, as demonstrated by the identified homogenous groups. Organotrophic bacteria were the most sensitive, while actinomycetes were the most tolerant to the heavy metals applied to the soil. In the latter group of microorganisms, the molecular sieve and biochar achieved the expected role by mollifying the inhibitory impact of Cd 2+ . Both materials induced an increase in the counts of actinomycetes by 84% and 60%, respectively, compared to the control pots polluted with this heavy metal. In turn, under the pressure of Co 2+ , expanded clay showed a particular remedial ability, contributing to an increase in the count of fungi by as much as 77%.
Values of the colony development (CD) indices obtained for the analysed groups of microorganisms revealed the inhibitory effect of both Cd 2+ and Co 2+ on this parameter ( Figure 2). Although sepiolite stimulated the multiplication of organotrophic bacteria, it was ineffective in alleviating the negative influence of the heavy metals applied to the soil, in which it resembled the other tested sorbents. Among the six analysed sorbents, few proved to be effective in stimulating the activity of the groups of microorganisms (Tables S1-S3). In non-polluted soil, the molecular sieve and biochar had the best effect on the count of organotrophic bacteria (Table S1) and expanded clay was most beneficial for actinobacteria (Table S2), while fungi responded positively to both expanded clay and biochar (Table S3). The stimulating effect of the reactive minerals and biochar on organotrophic bacteria was 36% and 25%, respectively, compared to 39% in the case of actinobacteria and 53% and 57% with respect to fungi. In the pots contaminated with Cd 2+ and Co 2+ , the positive effects of the sorbents were less spectacular, as demonstrated by the identified homogenous groups. Organotrophic bacteria were the most sensitive, while actinomycetes were the most tolerant to the heavy metals applied to the soil. In the latter group of microorganisms, the molecular sieve and biochar achieved the expected role by mollifying the inhibitory impact of Cd 2+ . Both materials induced an increase in the counts of actinomycetes by 84% and 60%, respectively, compared to the control pots polluted with this heavy metal. In turn, under the pressure of Co 2+ , expanded clay showed a particular remedial ability, contributing to an increase in the count of fungi by as much as 77%.
Values of the colony development (CD) indices obtained for the analysed groups of microorganisms revealed the inhibitory effect of both Cd 2+ and Co 2+ on this parameter ( Figure 2). Although sepiolite stimulated the multiplication of organotrophic bacteria, it was ineffective in alleviating the negative influence of the heavy metals applied to the soil, in which it resembled the other tested sorbents.  A reverse dependence was noted in the case of actinomycetes. None of the sorbents stimulated the multiplication of this group of microorganisms in soil free from heavy metals. On the other hand, the complication of the exposure to Cd 2+ and soil remediation with expanded clay or soil contamination with Co 2+ and the application of a molecular sieve contributed to a rise in the CD value for actinomycetes. In the pots unpolluted with heavy metals, expanded clay also induced the multiplication of fungi (CD = 78.329). None of the sorbents managed to alleviate the negative effects of such spectacular pressure by Cd 2+ and Co 2+ . It is worth underlining that the broader pool of applied reactive minerals, including a molecular sieve, expanded clay and zeolite as well as biochar was more effective in constraining the inhibitory impact of Co 2+ than that of Cd 2+ on the multiplication rate of fungi.
The response of microorganisms to the tested factors was also traced through the prism of the ecophysiological diversity (EP) values (Figure 3). In the pots free from contamination with the heavy metals, none of the tested sorbents had a positive effect on the EP of organotrophic bacteria comparable to that obtained with the molecular sieve in soil exposed to 100 mg Cd 2+ kg −1 d.m. of soil (EP = 0.945). In turn, the pressure of 100 mg Co 2+ kg −1 d.m. of soil on this parameter was mollified by halloysite, expanded clay, zeolite and biochar. It is worth emphasising that the response of actinomycetes to the compilation of soil contamination with Co 2+ and its remediation with a molecular sieve was completely opposite. The ecophysiological diversity index in this pool of objects was observed to have decreased. Among fungi, which were characterised by the lowest EP values, a comparable trend was observed in the objects with sepiolite in the soil polluted with Cd 2+ and Co 2+ .

Enzyme Activity
The differentiated response of soil enzymes, demonstrated by the η 2 values was another manifestation of the extent of biotic stress induced by soil contamination with Cd 2+ and Co 2+ (Figure 1). Having assessed the percentage contribution of the variables, the response of enzymes to the applied adsorbents was evaluated and arranged in the following order: Glu > Cat > Pac > Deh > Aryl = Ure > Pal. The heavy metals had the highest moderating effect on Pal (91%), Deh (86%) and Ure (84%), and the weakest one-on the activity of Glu (17%). Co 2+ proved to be less toxic to Deh and Ure (Tables S4 and S6), and Cd 2+ was less toxic to Pal (Table S7). The activity of enzymes declined by 94% (Deh) and 48% (Ure) under the pressure of Co 2+ and by 58% (Pal) under the influence of Cd 2+ relative to the control objects. With respect to the remaining enzymes, the inhibitory effect of both heavy metals was similar (Tables S5 and S8-S10). The index of the effect of heavy metals on the activity of soil enzymes (IF Hm ) attested to the particular sensitivity of Deh, Pal and Ure to being exposed to Cd 2+ and Co 2+ (Figure 4). Values of the IF Hm also distinguished the most stable enzymes in soil exposed to the pressure of the heavy metals, which were β-glucosidase and catalase.
Based on the values of the index showing the effect of sorbents on the activity of enzymes (IF Ad ), the sorbents which improved the condition of the soil were identified ( Figure 5). However, none of the adsorbents applied restored the equilibrium of the soil after it had been polluted with heavy metals. Zeolite in unpolluted soil stimulated the activity of Deh, Ure, Aryl and Pal, inducing its increase by 56%, 24%, 18% and 17%, respectively, in comparison to the control objects. Sepiolite and halloysite raised the activity of Pac and Glu by 38%, whereas biochar contributed to a rise in the activity of catalase by 12%. When reviewing the remediation potential of the tested adsorbents, it was concluded that all the reactive minerals and biochar only alleviated the inhibitory impact of the heavy metals, except expanded clay added to the soil exposed to the pressure of Cd 2+ , but did not completely eliminate the impact of heavy metals. The extent of their influence varied. Regardless of the metal applied to soil, the molecular sieve and biochar decreased the toxic effect of Cd 2+ and Co 2+ on the activity of dehydrogenases. However, the highest value of IF Ad = 8.048 was obtained in the soil polluted with Co 2+ and amended with zeolite. Halloysite caused an increase in the activity of urease. The activity of this enzyme in the objects with Co 2+ contaminated soil was also stimulated by zeolite and sepiolite. Higher effectiveness of these three sorbents was also noted regarding catalase, but only in the soil contaminated with Cd 2+ . In this pool of objects, the molecular sieve proved to be the remediation factor that mostly enhanced the activity of Pac and Pal. The adsorbents which were ineffective in stimulating the activity of particular soil enzymes were also identified. The objects polluted with Co 2+ halloysite did not significantly stimulate the activity of Ure, Pal and Aryl, sepiolite-Cat and Glu, expanded clay-Deh, and biochar-Pac. In the soil contaminated with Cd 2+ , the expected effects were not achieved by expanded clay as regards Pal and Glu, and zeolite as regards Pac and Arul. Sepiolite, biochar and molecular sieve generated the lowest values of the IF Ad for Deh (IF Ad = 0.15), Cat (IF Ad = 0.10) and Ure (IF Ad = 0.11), respectively.
A more comprehensive character of this study was achieved when the response of the sunflower to the pressure of Cd 2+ and Co 2+ was analysed, and the usefulness of the tested adsorbents in remediation of soils polluted with heavy metals was verified, including the yields of the test plant (Tables S11 and S12, Figure 6). Co 2+ had a stronger inhibitory effect on the growth and development of the sunflower's aboveground parts, whose yields were lower by as much as 73% under the pressure of this metal relative to the control, in comparison to a 59% lower yield in soil polluted with Cd 2+ (Table S11). Out of the six adsorbents applied to the soil not exposed to heavy metals, biochar and zeolite induced an increase in the crop's aboveground parts by 18% and 15%, respectively, relative to the control. Notwithstanding this, both adsorbents mitigated the least the toxic effect of Cd 2+ on this parameter. The values of the index illustrating the impact of the heavy metals on the sunflower yields (IF Hm ) revealed that the extent of the negative influence of both Cd 2+ (IF Hm = −0.32) and Co 2+ (IF Hm = −0.52) was the smallest in the compilation with the molecular sieve (Figure 7a). Determination of the usefulness of adsorbents based on the IF Ad exposed their potential to alleviate the toxic effect of the heavy metals on the yield of the cultivated crop ( Figure 8a). However, this potential was varied and dependent on the type of heavy metal. The lowest value of the IF Ad in soil exposed to the pressure of Cd 2+ was noted for zeolite (IF Ad = 0.10) and to Co 2+ -for sepiolite and expanded clay (IF Ad = 0.18).
When evaluating the response of sunflowers through the prism of the mass of sunflower roots, different relationships emerged (Table S12). Cd 2+ proved to be a stronger inhibitor to the crop's root system. The application of this heavy metal generated the root mass lower by 77%, compared to 70% in response to Co 2+ , relative to the unpolluted objects. The usefulness of the adsorbents for remediation of soil was traced following the response of the sunflower roots, which displayed two significant relationships: halloysite induced an increase in the root biomass by 44% and zeolite by 38% in unpolluted soil (1) and according to the IF Hm values, none of these adsorbents was as effective in the alleviation of the negative impact of the heavy metals (2) (Figure 6). The pool of the objects contaminated with Cd 2+ , sepiolite, expanded clay, and molecular sieve generated the lowest values of the IF Hm = −0.63, and the molecular sieve was the most effective in alleviating the toxic effect of cobalt in Co 2+ contaminated soil (IF Hm = −0.571). Having traced the values of the index showing the effect of sorbents (IF Ad ) on the development of the sunflower's root system, we were able to identify the reactive minerals that played the least significant role in the simulation of the root's growth (Figure 7b). These include expanded clay in unpolluted soil (IF Ad = 0.09) and in soil exposed to Co 2+ (IF Ad = 0.11), as well as halloysite in the objects contaminated with Cd 2+ (IF Ad = 0.18). Co 2+ disturbed the synthesis of chlorophyll spectacularly, as evidenced by the low values of the greenness index (4.45) ( Table 2). However, this process was significantly mollified by the molecular sieve, same as in the objects polluted with Cd 2+ , although the inhibitory effect of this metal (SPAD = 21.62) was not as large as the one produced by Co 2+ . soil exposed to 100 mg Cd 2+ kg −1 d.m. of soil (EP = 0.945). In turn, the pressure of 100 mg Co 2+ kg −1 d.m. of soil on this parameter was mollified by halloysite, expanded clay, zeolite and biochar. It is worth emphasising that the response of actinomycetes to the compilation of soil contamination with Co 2+ and its remediation with a molecular sieve was completely opposite. The ecophysiological diversity index in this pool of objects was observed to have decreased. Among fungi, which were characterised by the lowest EP values, a comparable trend was observed in the objects with sepiolite in the soil polluted with Cd 2+

Enzyme Activity
The differentiated response of soil enzymes, demonstrated by the η 2 values was another manifestation of the extent of biotic stress induced by soil contamination with Cd 2+ and Co 2+ (Figure 1). Having assessed the percentage contribution of the variables, the response of enzymes to the applied adsorbents was evaluated and arranged in the following order: Glu > Cat > Pac > Deh > Aryl = Ure > Pal. The heavy metals had the highest stable enzymes in soil exposed to the pressure of the heavy metals, which were βglucosidase and catalase. Based on the values of the index showing the effect of sorbents on the activity of enzymes (IFAd), the sorbents which improved the condition of the soil were identified ( Figure 5). However, none of the adsorbents applied restored the equilibrium of the soil after it had been polluted with heavy metals. Zeolite in unpolluted soil stimulated the activity of Deh, Ure, Aryl and Pal, inducing its increase by 56%, 24%, 18% and 17%, respectively, in comparison to the control objects. Sepiolite and halloysite raised the The adsorbents which were ineffective in stimulating the activity of particular soil enzymes were also identified. The objects polluted with Co 2+ halloysite did not significantly stimulate the activity of Ure, Pal and Aryl, sepiolite-Cat and Glu, expanded clay-Deh, and biochar-Pac. In the soil contaminated with Cd 2+ , the expected effects were not achieved by expanded clay as regards Pal and Glu, and zeolite as regards Pac and Arul. Sepiolite, biochar and molecular sieve generated the lowest values of the IFAd for Deh (IFAd = 0.15), Cat (IFAd = 0.10) and Ure (IFAd = 0.11), respectively. A more comprehensive character of this study was achieved when the response of the sunflower to the pressure of Cd 2+ and Co 2+ was analysed, and the usefulness of the tested adsorbents in remediation of soils polluted with heavy metals was verified, including the yields of the test plant (Table S11 and S12, Figure 6). Co 2+ had a stronger inhibitory effect on the growth and development of the sunflower's aboveground parts, whose yields were lower by as much as 73% under the pressure of this metal relative to the control, in comparison to a 59% lower yield in soil polluted with Cd 2+ (Table S11). Out of the six adsorbents applied to the soil not exposed to heavy metals, biochar and zeolite induced an increase in the crop's aboveground parts by 18% and 15%, respectively, When evaluating the response of sunflowers through the prism of the mass of sunflower roots, different relationships emerged (Table S12). Cd 2+ proved to be a stronger inhibitor to the crop's root system. The application of this heavy metal generated the root mass lower by 77%, compared to 70% in response to Co 2+ , relative to the unpolluted objects. The usefulness of the adsorbents for remediation of soil was traced following the response of the sunflower roots, which displayed two significant relationships: halloysite When evaluating the response of sunflowers through the prism of the mass of sunflower roots, different relationships emerged (Table S12). Cd 2+ proved to be a stronger inhibitor to the crop's root system. The application of this heavy metal generated the root mass lower by 77%, compared to 70% in response to Co 2+ , relative to the unpolluted objects. The usefulness of the adsorbents for remediation of soil was traced following the response of the sunflower roots, which displayed two significant relationships: halloysite When evaluating the response of sunflowers through the prism of the mass of sunflower roots, different relationships emerged (Table S12). Cd 2+ proved to be a stronger inhibitor to the crop's root system. The application of this heavy metal generated the root mass lower by 77%, compared to 70% in response to Co 2+ , relative to the unpolluted objects. The usefulness of the adsorbents for remediation of soil was traced following the response of the sunflower roots, which displayed two significant relationships: halloysite

Microorganisms
Contamination of soil with Co 2+ or with Cd 2+ caused undesirable changes in the soil's microbiological parameters. They included depressed counts of organotrophic bacteria and, to a lesser extent, of fungi and actinomycetes. Admittedly, negative effects of the impact of these heavy metals on the soil microbiome were expected, as suggested by reports on the damage of the integrity of the cell membrane in microorganisms, inactivation or oxidation of cellular enzymes, protein denaturation, or inhibition of the process of transcription by heavy metals [76]. However, it is known that one of the common adaptation strategies of microorganisms relies on the extracellular production of metallophores and polysaccharides [77] and on horizontal gene transfer, where mobile genetic elements, such as transposons and integrons, play an important role [78]. Co 2+ proved to be a stronger inhibitor of the multiplication of actinomycetes and fungi than Cd 2+ . Considering the fact that Co 2+ is absorbed by microorganisms in order to produce enzyme cofactors (cobamide) participating in the metabolic reactions essential for live cells [79], it shows affinity to thiol groups of peroxiredoxins aggregated after hyperoxidation to protect proteins from denaturation [80], opposite tendencies were expected. Kosiorek and Wyszkowski [81] also report that Co 2+ may retard or stimulate the division of cells depending on its dose. However, the correlations obtained in this study correspond well to the research results achieved by Wyszkowska et al. [44], Boros-Lajszner et al. [82] and Zaborowska et al. [83]. It has been demonstrated that the toxicity of Co 2+ in the periplasm regulated by the cytochromes GSU 1538 and GSU 2513 is associated with the diffusion of this metal through non-selective pores of the external membrane, leading to the rapid accumulation of Co 2+ in the periplasm space, thereby interfering with basic cellular functions [84]. The toxicity of Cd 2+ towards microorganisms raises fewer questions as it has been confirmed by numerous scientific reports [44,82,85,86]. Furthermore, Gunina and Kuzyakow [87] observed that Cd 2+ pressure caused a rapid rate of the uptake of sugars from the soil by microorganisms, which stimulated microbial activity and accelerated the decomposition of SOM. The depressed availability of organic matter could evoke a strong stress response in microorganisms. Thus, the application of adsorbents as a remediation factor is highly justified, particularly the use of a molecular sieve and biochar, which not only induced the growth of organotrophic bacteria but also mollified the toxic effect of Cd 2+ . In addition, the molecular sieve enhanced the rate of multiplication of actinomycetes and had a beneficial influence on the ecophysiological diversity of organotrophic bacteria. The effectiveness of biochar was most probably connected with its unique parameters responsible for the adsorption potential of heavy metals in arable soils, such as surface loads and pore spaces correlated with the content of nutrients and the ability to exchange cations (CEC) [88,89]. In their studies, Strachel et al. [66] and Steiner et al. [90] also demonstrated that biochar enhanced the activity of the soil microbiome. A molecular sieve owes its effectiveness to silanol groups (Si-OH) localised on the surface of the mineral, which can strongly immobilise Cd 2+ in soil [91]. Strachel et al. [66] showed that a molecular sieve, same as biochar, had the strongest positive effect on the counts of organotrophic bacteria and actinomycetes, which supports the results of our experiment. The effect produced by expanded clay should not be neglected either, as it alleviated the negative impact of Co 2+ on counts of all analysed groups of microorganisms and contributed to a more intensive proliferation of both fungi and actinomycetes. The usefulness of expanded clay as a bioremediation substance arises from the double porosity of this mineral, both the porous core and the intercrystallite space [92]. Expanded clay is increasingly often used as a material for amending wetlands owing to its ability to remove phosphates and its structure that supports the activity of the microbiome [93].

Soil Enzymes
Being able to conduct a reliable analysis of the potential of microorganisms in soil transformations requires adequate quantification of the activity of soil enzymes [94]. Priority is given to soil ecosystems with distorted homeostasis. The response of the analysed soil enzymes exposed the negative effect of Co 2+ and Cd 2+ on the condition of the soil. Among the seven analysed soil enzymes, dehydrogenases, urease, acid, and alkaline phosphatase appeared to be particularly sensitive to the pressure of both heavy metals. Different responses of the broad pool of enzymes to the two heavy metals reflected the complexity of the forms in which these enzymes occur in soil. Extracellular enzymes are released from cells of microorganisms undergoing lysis. They are also associated with enzymesubstrate complexes or are complex with organic matter through the process of adsorption or copolymerisation. Some enzymes also bind to condensed tannins or are adsorbed on clay materials [95]. The highest sensitivity of dehydrogenases to the toxicity of Co 2+ and Cd 2+ could be attributed to the fact that these enzymes are the basic elements of the enzymatic system of all living microorganisms [96]. It is also known that one of the key abiotic environmental factors moderating the activity of all enzymes is the soil pH [97]. A rise in this parameter can contribute to the damage of ionic and hydrogen bonds in the active centre of dehydrogenases [98]. In turn, the negative effect of Co 2+ on the activity of urease could be a consequence of interactions of complexes containing this metal with sulfhydryl groups of cysteines, histidine nitrogen atoms or oxygen atoms of glutamic acid residues of urease amino acids [99].
While the application of adsorbents did not restore the equilibrium of soil, some of these substances stood out by their ability to alleviate the toxic effect of heavy metals. Apart from a molecular sieve and biochar, which determined the activity of Deh, other reactive minerals were distinguished as being able to minimise the adverse impact of Co 2+ on the activity of Deh and Cat (zeolite) or Ure (halloysite, sepiolite and zeolite), and were also effective against the negative influence of Cd 2+ in soil. The effectiveness of a molecular sieve and zeolite might be attributed to the homogenous structure of these sorbents [100] and heavy metal binding affinity [101]. Of importance for the bioremediation potential is the three-dimensional skeleton of tetrahedral bonds [SiO 4 ] 4− and [AlO 4 ] 5− of zeolite studded with spaces for cation exchange, which creates the catalytic characteristics of this material and facilitates the process of adsorption, desorption and ionic exchange [102]. Boros-Lajszner et al. [69] also implicate an important role of zeolite in the remediation of soil contaminated with heavy metals. In turn, Strachel et al. [66] maintain that halloysite is a significant stimulator of Pac, Deh and Ure. Yuan et al. [103] claim that this clay mineral is effective in absorbing pollutants by creating surface complexes, which resemble sepiolite, which causes changes in the activity of alkaline phosphatase, β-glucosidase [66], urease [104] and dehydrogenase [105].

Sunflower (Helianthus annuus L.) against Soil Contamination with Co 2+ and Cd 2+
The choice of the sunflower (Helianthus annuus) as a test plant was dictated by its ability to remove heavy metals from soils [106,107]. It was demonstrated that both Co 2+ and Cd 2+ significantly disturbed the yielding of the test plant. Similar relationships were noted by Forte and Mutiti in soil polluted by Cd 2+ [106]. Under the pressure of 200 mg Cd 2+ kg −1 d.m. of soil, the dry matter of the stem decreased by 64.30%, and that of the root was lowered by 80.80%. Higher toxicity of Co 2+ towards the sunflower is certainly a consequence of the heavy metal interfering with the structure and number of chloroplasts, damage to the morphology of plastids and inhibition of the synthesis of the RNA as well as amounts of the RNA and DNA through the modification of the activity of endo-and exonucleases [108]. In turn, Cd 2+ depresses the activity of the oxidative enzymes CAT or SOD [36]. Stimulation of ROS in a plant induces an increase in the synthesis of the mitogen-activated protein (MAP) kinase [109], and the Cd 2+ stimulated synthesis of the radicals H 2 O 2 and OH eventually leads to the necrosis of plant tissues [110]. Due to the competition with Cd 2+ , the uptake and, consequently, concentrations of K, Ca, Mn, Zn, Cu and Fe in plants decrease, causing their deficiencies [111]. This study proves that the response of the sunflower to the contamination of soil with heavy metals, including Co 2+ , is manifested by the yellowing of leaves correlated with the decreasing content of chlorophyll, as evidenced by the SPAD values. According to Palit et al. [108], the role of this metal in the process of photosynthesis is controversial. However, the toxic effect of Co 2+ on this parameter is manifested by the inhibition of the acceptor PS 2 , thereby slowing down the Hill reaction and by the reduced export of photo assimilators. Furthermore, Cd 2+ has an inhibitory effect on photosynthesis by retarding the activity of the Calvin cycle enzymes. In addition, it induces changes in the lipid composition of thylakoid membranes [112].
The molecular sieve manifested its remediation properties in the soil contaminated with Co 2+ and Cd 2+ . Interestingly, biochar and zeolite significantly induced the growth and development of the sunflower in unpolluted soil. However, the compilation of these sorbents did not yield the expected results, which would be a higher yield of this crop. This could be explained by the fact that biochar produced by pyrolysis may contain small amounts of toxic substances, usually As, Cr, Pb and Cd. Hence, before its application as a biosorbent, it is recommended to leach metals from biochar [113].

Conclusions
Co 2+ and Cd 2+ significantly interfered with the soil's microbiome, distorting its balance. Organotrophic bacteria proved to be the least sensitive to soil contamination with Cd 2+ , while fungi and actinomycetes were least sensitive to the pollution of soil with Co 2+ . The inhibitory effect of Cd 2+ was also manifested by the decreasing CD values of actinomycetes and organotrophic bacteria, thereby implicating a change in the structure of these groups of microorganisms from r strategists to K strategists. Dehydrogenases and urease were most sensitive to the pressure of Cd 2+ , while dehydrogenases and alkaline phosphatase-to Co 2+ . The response of Helianthus annuus to soil pollution with heavy metals consisted in the significantly disturbed growth and development of this plant, both the aboveground parts and the roots, although Co 2+ inhibited the synthesis of chlorophyll more spectacularly. None of the tested adsorbents restored the balance of soil after the contamination with the heavy metals, although all of them, to a different extent, alleviated the toxic influence of the metals on the soil's microbiological activity and biochemical activity and yields of the sunflower. A molecular sieve and biochar demonstrated remediation potential towards microorganisms and enzymatic activity. The activity of soil enzymes was also stimulated by zeolite and sepiolite. The use of a molecular sieve induced an increase in the biomass of Helianthus annuus of both aboveground organs and roots. Having analysed all the parameters included in this experiment, it was concluded that a molecular sieve might be the most useful sorbent in the remediation of soils polluted with Co 2+ and Cd 2+ . The obtained results set the direction for further research, which should be carried out under environmental conditions. The use of sorbents in the reclamation of Cd 2+ and Co 2+ contaminated soils should also be preceded by an economic calculation in connection with the impact of these pollutants on the environment.

Conflicts of Interest:
The authors declare no conflict of interest. The funders had no role in the design of the study; in the collection, analyses, interpretation of data; in the writing of the manuscript; or in the decision to publish the results.