Experimental Study on the Optimum Preparation of Bentonite–Steel Slag Composite Particles

: Novel multifunctional adsorbent bentonite–steel slag composite particles (BSC) were developed for highly e ﬃ cient and synergistic treatment of heavy metal ions in acid mine drainage (AMD). Single-factor experiments were performed to examine the inﬂuence of di ﬀ erent parameters on the adsorption e ﬀ ect, alkalinity release quantity, and loss rate of the composite particles. Based on these results, an L9(4 3 ) orthogonal experiment was carried out, and the optimum levels and order of the factors were determined by range analysis. Finally, the optimum preparation process of the composite particles was determined: a bentonite–steel slag proportion of 5:5, Na 2 CO 3 content of 5%, aging time of 12 h, calcination particle size of 2 mm, calcination temperature of 500 ◦ C, and calcination time of 60 min. The isothermal adsorption of optimum BSC ﬁt well with Langmuir and Brunauer–Emmett–Teller (BET) isotherms ( R 2 R 2 > 0.997). A synergistic adsorption–coagulation e ﬀ ect occurs, leading to the appearance of multiple layers locally on the surface of BSC, which satisﬁes the BET model. To understand the preparation mechanism of the BSC, bentonite, steel slag, uncalcined BSC, and the optimum BSC were characterized using scanning electron microscopy (SEM), Brunauer–Emmett–Teller (BET) surface area analysis, X-ray powder di ﬀ raction (XRD), and Fourier-transform infrared spectroscopy (FTIR). The results indicate that calcination led to an increase in the average pore radius, total pore volume, and speciﬁc surface area ( S BET ) in the optimum BSC; numerous pores were present on its layered surface. Although the layer spacing increased after calcination, the structure of the dioctahedra remained unchanged. Exchangeable Na + , montmorillonite, and alkaline components were present between the optimum BSC layers. Water and impurities were removed after calcination. The BSC not only released an alkalinity-neutralising acid but also induced a synergistic adsorption–coagulation e ﬀ ect that removed heavy metal ions. It is an excellent multifunctional protective material for the mining environment, that can treat AMD-containing heavy metal ions. removal of heavy metal ions. The adsorption quantities of Pb, Cd, and Cr were 4.98 mg / g, 4.95 mg / g, and 4.82 mg / g, respectively, at 120 min. The composite particle loss rate was lowest at 0.98%, and the alkalinity release quantity was highest at 12.26 mg / g. The adsorption quantities of Pb, Cd, and Cr by composite particles with the proportion of 6:4 were 4.83 mg / g, 4.79 mg / g, and 4.53 mg / g, respectively; the loss rate was 1.27%, and the alkalinity release quantity was 11.04 mg / g. The adsorption quantities of Pb(II), Cd(II), and Cr(III) of composite particles with the proportion of 7:3 were 4.71 mg / g, 4.64 mg / g, and 4.32 mg / g, respectively. The loss rate was 2.77%, and the alkalinity release quantity was 10.06 mg / g. The composite particles with proportions of 8:2 and 9:1 had lower adsorption quantity and alkalinity, and the loss rate was above 3.4%. The experimental results showed that steel slag plays an active role in the removal of heavy metal ions by releasing alkalinity, increasing ion removal, and reducing the loss rate. However, if the composite material had more steel slag than bentonite it could not be made into particles, and the particles were easily pulverized before being calcined. shows the textural properties of bentonite, steel slag, BSC before calcination, and optimum BSC. BET adsorption studies show that the speciﬁc surface area ( S BET ) of the optimum BSC is 130.6 m 2 / g with an average pore radius of 8.4 nm, and the total pore volume is 5.14 cm 3 / g. These values are signiﬁcantly higher than those of bentonite, steel slag, and uncalcined BSC. Upon calcination of BSC, water evaporates, and Na 2 CO 3 is decomposed into CO 2 , resulting in the formation of numerous pores in BSC. This reﬂects the observed increase in the pore radius, total pore volume, and S BET values.


Introduction
Acid mine drainage (AMD) is a major pollution source in mining areas [1,2]. AMD has a pH < 3, and contains high concentrations of toxic elements, such as heavy metal ions, which cannot be reused [3,4]. If AMD is discharged into the environment without treatment, it can directly harm humans, animals, and plants [5,6], especially when it contains heavy metals like Pb(II), Cd(II), and Cr(III) [7,8]. Highly efficient synergistic treatment methods and novel and cheap protective materials against AMD for the mining environment are a topic of cutting-edge research in academia and practice [9,10].

Calculation
The quantity of heavy metal ions adsorbed by the BSC was calculated as follows: where q t is the amount of solute adsorbed per unit adsorbent at any time (mg/g); C 0 and C t are the initial concentration and concentration at any time, respectively, of the solute in the solution (mg/L); V is the volume of the water sample (L); and m is the mass of the BSC (g). The alkalinity (measured in CaCO 3 ) in this experiment was determined through acid-base titration (SL 83-1994) and was calculated as follows: Total alkalinity (mg/L) = C × (P + M) × 50.05 V × 1000 (2) where C is the concentration of the HCl standard solution (mol/L); P is the HCl consumption after the addition of the phenolphthalein reagent (mL); M is the HCl consumption after the addition of the methyl orange reagent (mL); V is the volume of the water sample (mL), and 50.05 is the molar mass of calcium carbonate (1/2CaCO 3 ) (g/mol). The loss rate of the composite particles was calculated as follows: where η is the loss rate of composite particles (%), m 1 is the initial mass of composite particles (g), and m 2 is the mass of the composite particles after drying (g).

Preparation of the BSC
Bentonite and steel slag powder were mixed at a given proportion, to which a given mass of Na 2 CO 3 was added. Herein, bentonite functioned as the adsorbent, steel slag imparted alkalinity, and Na 2 CO 3 was employed as the pore-opening agent and decomposed into CO 2 upon heating. After the mixture was evenly mixed, an appropriate amount of deionized water was added and stirred, and composite particles with the same particle size (calcination particle size) were made with an extrusion granulator. Granular adsorbents are known to facilitate solid-liquid separation for industrial applications. The particles were aged for a given period of time (aging time); this was to achieve a complete permeation of the raw material particles by water. A deeper permeation resulted in the pores Sustainability 2020, 12, 18 4 of 27 being generated by the evaporation of water being significantly smaller during calcination; this was conducive to increasing the specific surface area of the particles. They were then heated in a crucible in a muffle furnace from the preheated temperature of 250 • C to a given temperature (calcination temperature) for a given time (calcination time). Calcination could not only increase the strength of the particles but also led to the production of a large amount of water vapor and CO 2 ; this resulted in an increase in the production of pores by the particles and enhanced the specific surface area, which in turn improved the adsorption performance. The particles were then cooled naturally after calcination to produce the adsorbent.

Single-Factor Experiment
Different bentonite and steel slag composite particles were prepared for different proportions of the bentonite and steel slag, contents of Na 2 CO 3 , aging times, calcination particle sizes, calcination temperatures, and calcination times. A batch test was performed to study the adsorption performances of the composite particles prepared under different conditions. The dosage was fixed at 10 g/L, and the initial concentration of the water sample containing heavy metal ions was 50 mg/L. A conical flask was placed in a thermostatic oscillator; the reaction temperature was 25 • C, and the rotating speed was 100 rpm. Water samples were then removed and filtered within the prescribed times of 20 min, 40 min, 60 min, 90 min, and 120 min. The concentration of residual ions in the filtrate was determined with a flame atomic absorption spectrophotometer (AAS) (Hitachi Z-2000, Tokyo, Japan), and the adsorption quantity was calculated according to Equation (1). An acid-base titration method (SL 83-1994) was performed, and the alkalinity was calculated according to Equation (2). The same amounts of composite particles and deionized water as in the adsorption experiment were added to the conical flask and reacted at a temperature of 25 • C and rotation speed of 100 rpm for 120 min. Particles were then dried in an oven at 105 • C until they reached a constant weight. The particle loss rate was calculated according to Equation (3). In order to ensure the reliability of the test results, the batch tests were conducted in parallel in two groups to obtain the mean values, and blank sample tests were conducted to test the initial concentration of the heavy metal ions.

Orthogonal Experiment
Based on the results of the single-factor experiment, the bentonite-steel slag proportion, Na 2 CO 3 content, calcination temperature, and calcination time were selected as the main influencing factors for an L9(4 3 ) orthogonal experiment [37,38]. Table 2 presents the design of the orthogonal experiment. The adsorption amount, alkalinity release amount, and loss rate at 120 min in the orthogonal experiment were measured and calculated in the same manner as that in the single-factor experiment.

Adsorption Isotherms
Batch tests were conducted to study Pb(II), Cd(II), and Cr(III) adsorption at different solution concentrations. The BSC dosage was fixed at 10 g/L with initial solute concentrations of 100 mg/L, 200 mg/L, 400 mg/L, 500 mg/L, and 600 mg/L. All samples were equilibrated for 24 h in a thermostatic shaker (25 • C, 100 rpm); then, the equilibrium Pb(II), Cd(II), and Cr(III) concentrations were measured using the AAS to calculate the amount of Pb(II), Cd(II), and Cr(III) adsorbed on the sorbent.

Microstructure Characterization
To investigate the modification mechanism of BSC, the raw materials and optimum BSC were characterized. The morphology and microstructure of the raw materials and optimum BSC were observed using an FEI Quanta 200 SEM. The specific surface area, average pore size, and total pore volume of the optimum BSC were estimated from Brunauer-Emmett-Teller (BET) nitrogen adsorption-desorption isotherms at 77.3 K using a Nova 2200e instrument (Quantachrome, Boynton Beach, FL, USA). X-ray diffraction (XRD) patterns were recorded in an XRD6100 (Shimadzu, Kyoto, Japan) diffractometer using monochromatic Cu Kα radiation (λ = 0.154 nm), operating at 40 kV and 30 mA over a 2θ range from 5 • to 80 • at a scanning rate of 6 • /min. Fourier-transform infrared spectroscopy (FTIR) studies were carried out on a Nicolet IS10 (Thermo Fisher, Waltham, MA, USA) FTIR spectrometer (KBr pellet, Houston, TX, USA) in the range of 4000-400 cm −1 .

Determination of the Bentonite-Steel Slag Proportion
To optimize the bentonite-steel slag proportion, the Na 2 CO 3 content was set to 5% of the total mass of the composite material, the aging time was set to 24 h, the calcination particle size was set to 1-2 mm, the calcination temperature was set to 500 • C, and the calcination time was set to 60 min. Different composite particles were produced with bentonite-steel slag proportions of 9:1, 8:2, 7:3, 6:4, and 5:5. Figure 1 shows the results for the adsorption amount, alkalinity release amount, and loss rate. Increasing the proportion of steel slag increased the adsorption quantity of heavy metal ions and alkalinity release quantity and decreased the loss rate. Composite particles with a proportion of 5:5 had the best removal of heavy metal ions. The adsorption quantities of Pb, Cd, and Cr were 4.98 mg/g, 4.95 mg/g, and 4.82 mg/g, respectively, at 120 min. The composite particle loss rate was lowest at 0.98%, and the alkalinity release quantity was highest at 12.26 mg/g. The adsorption quantities of Pb, Cd, and Cr by composite particles with the proportion of 6:4 were 4.83 mg/g, 4.79 mg/g, and 4.53 mg/g, respectively; the loss rate was 1.27%, and the alkalinity release quantity was 11.04 mg/g. The adsorption quantities of Pb(II), Cd(II), and Cr(III) of composite particles with the proportion of 7:3 were 4.71 mg/g, 4.64 mg/g, and 4.32 mg/g, respectively. The loss rate was 2.77%, and the alkalinity release quantity was 10.06 mg/g. The composite particles with proportions of 8:2 and 9:1 had lower adsorption quantity and alkalinity, and the loss rate was above 3.4%. The experimental results showed that steel slag plays an active role in the removal of heavy metal ions by releasing alkalinity, increasing ion removal, and reducing the loss rate. However, if the composite material had more steel slag than bentonite it could not be made into particles, and the particles were easily pulverized before being calcined.  The hydrolysis reaction of steel slag made the solution alkaline, and the heavy metal ions reacted to form metal hydroxides. As the proportion of steel slag increased, more alkalinity was released, more hydroxides were generated, and the removal efficiency of heavy metal ions improved. Meanwhile, the metal hydroxides adsorbed on the particle surfaces as a carrier to adsorb heavy metal ions; this resulted in a synergistic adsorption-coagulation effect. Because of the high mechanical  The hydrolysis reaction of steel slag made the solution alkaline, and the heavy metal ions reacted to form metal hydroxides. As the proportion of steel slag increased, more alkalinity was released, more hydroxides were generated, and the removal efficiency of heavy metal ions improved. Meanwhile, the metal hydroxides adsorbed on the particle surfaces as a carrier to adsorb heavy metal ions; this Sustainability 2020, 12, 18 7 of 27 resulted in a synergistic adsorption-coagulation effect. Because of the high mechanical strength of the steel slag, increasing its proportion reduced the particle loss rate [39,40]. In conclusion, the optimum proportion of bentonite and steel slag was 5:5.
The main hydrolysis reactions [41] of steel slag in the solution were as follows: Then, 3.1.2. Determination of the Na 2 CO 3 Content To optimize the Na 2 CO 3 content, the bentonite-steel slag proportion was set to 5:5, the aging time was set to 24 h, the calcination particle size was set to 1-2 mm, the calcination temperature was set to 500 • C, and the calcination time was set to 60 min. Different composite particles were produced with Na 2 CO 3 contents of 0%, 3%, 5%, 8%, and 10%. Figure 2 shows the results for the adsorption amount, alkalinity release amount, and loss rate. When the Na 2 CO 3 content was increased from 3% to 10%, the adsorption rate of the composite particles to ions increased significantly, the loss rate decreased, and the alkalinity release quantity increased. The composite particles with a Na 2 CO 3 content of 0% had the best adsorption effect on heavy metal ions, with the highest alkalinity release, but the loss rate was as high as 100%, so the required strength could not be achieved. Composite particles with 3% Na 2 CO 3 content had adsorption quantities of Pb(II), Cd(II), and Cr(III) of 4.65 mg/g, 3.72 mg/g, and 3.15 mg/g, respectively. The loss rate was 5.21%, and the alkalinity was 10.26 mg/g. Composite particles with Na 2 CO 3 contents of 5%, 8%, and 10% showed little difference in the adsorption amount, loss rate, and alkalinity release amount and could reach a high standard. Waste occurred when the Na 2 CO 3 content was 10%.
Sustainability 2020, 12, x FOR PEER REVIEW 7 of 26 strength of the steel slag, increasing its proportion reduced the particle loss rate [39,40]. In conclusion, the optimum proportion of bentonite and steel slag was 5:5.

Determination of the Na2CO3 Content
To optimize the Na2CO3 content, the bentonite-steel slag proportion was set to 5:5, the aging time was set to 24 h, the calcination particle size was set to 1-2 mm, the calcination temperature was set to 500 °C, and the calcination time was set to 60 min. Different composite particles were produced with Na2CO3 contents of 0%, 3%, 5%, 8%, and 10%. Figure 2 shows the results for the adsorption amount, alkalinity release amount, and loss rate. When the Na2CO3 content was increased from 3% to 10%, the adsorption rate of the composite particles to ions increased significantly, the loss rate decreased, and the alkalinity release quantity increased. The composite particles with a Na2CO3 content of 0% had the best adsorption effect on heavy metal ions, with the highest alkalinity release, but the loss rate was as high as 100%, so the required strength could not be achieved. Composite particles with 3% Na2CO3 content had adsorption quantities of Pb(II), Cd(II), and Cr(III) of 4.65 mg/g, 3.72 mg/g, and 3.15 mg/g, respectively. The loss rate was 5.21%, and the alkalinity was 10.26 mg/g. Composite particles with Na2CO3 contents of 5%, 8%, and 10% showed little difference in the adsorption amount, loss rate, and alkalinity release amount and could reach a high standard. Waste occurred when the Na2CO3 content was 10%. Because it is a pore-opening agent, increasing the Na2CO3 content increased the CO2 during calcine. Increasing the gas channels and pores inside the particles increased the active centers that could be provided for adsorption. A large number of channels and pores also facilitated the release of alkalinity of the particles. However, the Na2CO3 content needed to be controlled within a suitable range, otherwise a large amount of CO2 gas would collapse the internal structure of the particles. Na2CO3 also acted as a binder and could react with the mineral components of SiO2 and Al2O3 in the composite particles to form silicate compounds. Increasing the Na2CO3 content formed more silicate compounds. The cohesiveness of the composite particles increased, and the loss rate decreased [42,43]. Although Na2CO3 can improve the adsorption performance of composite particles and reduce the loss rate, industrial Na2CO3 costs $185/t, which is relatively expensive. In conclusion, the optimum Na2CO3 content was determined to be 5%.

Determination of the Aging Time
To determine the aging time, the bentonite-steel slag proportion was set to 5:5, the Na2CO3 content was set to 5%, the calcination particle size was set to 1-2 mm, the calcination temperature was set to 500 °C, and the calcination time was set to 60 min. Different composite particles were produced at aging times of 0 h, 6 h, 12 h, 18 h, 24 h, and 30 h. Figure 3 shows the results for the adsorption amount, alkalinity release amount, and loss rate. As the aging time increased, the Because it is a pore-opening agent, increasing the Na 2 CO 3 content increased the CO 2 during calcine. Increasing the gas channels and pores inside the particles increased the active centers that could be provided for adsorption. A large number of channels and pores also facilitated the release of alkalinity of the particles. However, the Na 2 CO 3 content needed to be controlled within a suitable range, otherwise a large amount of CO 2 gas would collapse the internal structure of the particles. Na 2 CO 3 also acted as a binder and could react with the mineral components of SiO 2 and Al 2 O 3 in the composite particles to form silicate compounds. Increasing the Na 2 CO 3 content formed more silicate compounds. The cohesiveness of the composite particles increased, and the loss rate decreased [42,43]. Although Na 2 CO 3 can improve the adsorption performance of composite particles and reduce the loss rate, industrial Na 2 CO 3 costs $185/t, which is relatively expensive. In conclusion, the optimum Na 2 CO 3 content was determined to be 5%.

Determination of the Aging Time
To determine the aging time, the bentonite-steel slag proportion was set to 5:5, the Na 2 CO 3 content was set to 5%, the calcination particle size was set to 1-2 mm, the calcination temperature was set to 500 • C, and the calcination time was set to 60 min. Different composite particles were produced at aging times of 0 h, 6 h, 12 h, 18 h, 24 h, and 30 h. Figure 3 shows the results for the adsorption amount, alkalinity release amount, and loss rate. As the aging time increased, the adsorption amount of heavy metal ions first increased and then decreased. The adsorption amount was highest at an aging time of 12 h. The alkalinity release amount first increased and then decreased with aging time. The range of variation was stable between 10.13 and 13.04 mg/g, and the alkalinity release amount was highest at 13.04 mg/g, with an aging time of 12 h. The loss rate first decreased and then increased with aging time and ranged from 1.62% to 1.07%. The composite particle loss rate was 1.19% when the aging time was 12 h, and the loss rate was lowest at 1.07% with an aging time of 18 h. Sustainability 2020, 12, x FOR PEER REVIEW 9 of 26 adsorption amount of heavy metal ions first increased and then decreased. The adsorption amount was highest at an aging time of 12 h. The alkalinity release amount first increased and then decreased with aging time. The range of variation was stable between 10.13 and 13.04 mg/g, and the alkalinity release amount was highest at 13.04 mg/g, with an aging time of 12 h. The loss rate first decreased and then increased with aging time and ranged from 1.62% to 1.07%. The composite particle loss rate was 1.19% when the aging time was 12 h, and the loss rate was lowest at 1.07% with an aging time of 18 h.  On the one hand, aging was performed to uniformly wet the composite particles with water so that they could expand. On the other hand, as the composite material was calcined, a large amount of internal moisture evaporated, which caused the particles to disintegrate. When the aging time was increased from 0 h to 12 h, the adsorption amount increased continuously to the maximum. This indicates that the materials had been uniformly infiltrated by water at 12 h, and the particle expansion reached its maximum. At this time, the particles had a large specific surface area after calcination, a high adsorption amount, a high alkalinity release amount, and a low loss rate. When the aging time was further increased, the amount of adsorption decreased, the amount of alkalinity decreased, and the loss rate increased. This indicates that an overly long aging time was detrimental to the adsorption of heavy metal ions by the composite particles [44][45][46]. It was concluded that the aging time may change the distribution and arrangement of the internal structure of the composite particles. Thus, the optimum aging time was determined to be 12 h.

Determination of the Calcination Particle Size
To determine the calcination particle size, the bentonite-steel slag proportion was 5:5, the Na 2 CO 3 content was 5%, the aging time was 12 h, the calcination temperature was 500 • C, and the calcination time was 60 min. Different composite particles were produced with calcination particle sizes of 1 mm, 2 mm, 3 mm, and 4 mm. Figure 4 shows the results for the adsorption amount, alkalinity release amount, and loss rate. The adsorption effect increased with a smaller calcination particle size when the reaction time was kept the same. As the calcination particle size decreased, the adsorption rate and adsorption quantity increased. The composite particles with a calcination particle size of 1 mm adsorbed 5 mg/g, 5 mg/g, and 4.95 mg/g of Pb(II), Cd(II), and Cr(III), respectively. The composite particles with a calcination particle size of 2 mm adsorbed 4.99 mg/g, 4.95 mg/g, and 4.85 mg/g of Pb(II), Cd(II), and Cr(III), respectively. The composite particles with particle sizes of 1 and 2 mm showed excellent metal ion removal. A smaller calcination particle size increased the external specific surface area of the particles [47], so they could adsorb aggregated heavy metal ions and precipitates. When the calcination particle size was increased, the alkalinity release amount increased slightly, and the range of variation was small. The effect of the calcination particle size on the release of alkalinity could be neglected. Increasing the calcination particle size reduced the loss rate; the composite particles with calcination particle sizes of 1 mm, 2 mm, 3 mm, and 4 mm had loss rates of 2.26%, 1.14%, 1.04%, and 0.96%, respectively. The composite particles with a particle size of 1 mm had a loss rate about twice that of the composite particles with a particle size of 2 mm. In conclusion, the optimum calcination particle size was determined to be 2 mm. On the one hand, aging was performed to uniformly wet the composite particles with water so that they could expand. On the other hand, as the composite material was calcined, a large amount of internal moisture evaporated, which caused the particles to disintegrate. When the aging time was increased from 0 h to 12 h, the adsorption amount increased continuously to the maximum. This indicates that the materials had been uniformly infiltrated by water at 12 h, and the particle expansion reached its maximum. At this time, the particles had a large specific surface area after calcination, a high adsorption amount, a high alkalinity release amount, and a low loss rate. When the aging time was further increased, the amount of adsorption decreased, the amount of alkalinity decreased, and the loss rate increased. This indicates that an overly long aging time was detrimental to the adsorption of heavy metal ions by the composite particles [44][45][46]. It was concluded that the aging time may change the distribution and arrangement of the internal structure of the composite particles. Thus, the optimum aging time was determined to be 12 h.

Determination of the Calcination Particle Size
To determine the calcination particle size, the bentonite-steel slag proportion was 5:5, the Na2CO3 content was 5%, the aging time was 12 h, the calcination temperature was 500 °C, and the calcination time was 60 min. Different composite particles were produced with calcination particle sizes of 1 mm, 2 mm, 3 mm, and 4 mm. Figure 4 shows the results for the adsorption amount, alkalinity release amount, and loss rate. The adsorption effect increased with a smaller calcination particle size when the reaction time was kept the same. As the calcination particle size decreased, the adsorption rate and adsorption quantity increased. The composite particles with a calcination particle size of 1 mm adsorbed 5 mg/g, 5 mg/g, and 4.95 mg/g of Pb(II), Cd(II), and Cr(III), respectively. The composite particles with a calcination particle size of 2 mm adsorbed 4.99 mg/g, 4.95 mg/g, and 4.85 mg/g of Pb(II), Cd(II), and Cr(III), respectively. The composite particles with particle sizes of 1 and 2 mm showed excellent metal ion removal. A smaller calcination particle size increased the external specific surface area of the particles [47], so they could adsorb aggregated heavy metal ions and precipitates. When the calcination particle size was increased, the alkalinity release amount increased slightly, and the range of variation was small. The effect of the calcination particle size on the release of alkalinity could be neglected. Increasing the calcination particle size reduced the loss rate; the composite particles with calcination particle sizes of 1 mm, 2 mm, 3 mm, and 4 mm had loss rates of 2.26%, 1.14%, 1.04%, and 0.96%, respectively. The composite particles with a particle size of 1 mm had a loss rate about twice that of the composite particles with a particle size of 2 mm. In conclusion, the optimum calcination particle size was determined to be 2 mm.   represents the change of Cr(Ⅲ) adsorption quantity with time. (d) represents the adsorption quantity by composite particles with different calcination particle sizes at 120min. (e) represents the alkalinity release amount and loss rate by composite particles with different calcination particle sizes at 120min.

Determination of the Calcination Temperature
To determine the calcination temperature, the bentonite-steel slag proportion was 5:5, the Na2CO3 content was 5%, the aging time was 12 h, the calcination particle size was 2 mm, and the calcination time was 60 min. Different composite particles were produced at calcination temperatures of 400 °C, 450 °C, 500 °C, and 550 °C. Figure 5 shows the results for the adsorption amount, alkalinity release amount, and loss rate. As the calcination temperature increased, the adsorption amount, alkalinity release amount, and loss rate decreased. The composite particles with a calcination temperature of 400 °C had the greatest adsorption and alkalinity release, but the loss rate was as high as 100%, so the required strength of the particles could not be achieved. The adsorption quantity reached 4.85 mg/g at the calcination temperatures of 450 °C and 500 °C, and the alkalinity release amounts were 16.52 mg/g and 14.26 mg/g, respectively. The composite particles calcined at 550 °C had a poor ion removal effect and the lowest alkalinity release amount at 6.25 mg/g. The loss rate was higher at 450 °C at 10.21%. The loss rates at 500 °C and 550 °C were 1.18% and 0.56%, respectively.  (d) represents the adsorption quantity by composite particles with different calcination particle sizes at 120 min. (e) represents the alkalinity release amount and loss rate by composite particles with different calcination particle sizes at 120 min.

Determination of the Calcination Temperature
To determine the calcination temperature, the bentonite-steel slag proportion was 5:5, the Na 2 CO 3 content was 5%, the aging time was 12 h, the calcination particle size was 2 mm, and the calcination time was 60 min. Different composite particles were produced at calcination temperatures of 400 • C, 450 • C, 500 • C, and 550 • C. Figure 5 shows the results for the adsorption amount, alkalinity release amount, and loss rate. As the calcination temperature increased, the adsorption amount, alkalinity release amount, and loss rate decreased. The composite particles with a calcination temperature of 400 • C had the greatest adsorption and alkalinity release, but the loss rate was as high as 100%, so the required strength of the particles could not be achieved. The adsorption quantity reached 4.85 mg/g at the calcination temperatures of 450 • C and 500 • C, and the alkalinity release amounts were 16.52 mg/g and 14.26 mg/g, respectively. The composite particles calcined at 550 • C had a poor ion removal effect and the lowest alkalinity release amount at 6.25 mg/g. The loss rate was higher at 450 • C at 10.21%. The loss rates at 500 • C and 550 • C were 1.18% and 0.56%, respectively. Sustainability 2020, 12, x FOR PEER REVIEW 12 of 26 The surface water of the composite particles, the internal bound water, and some impurities in the pores were removed by calcination at high temperature. This reduced the effect of the water film resistance on the adsorption, so the adsorption increased. The surface of the uncalcined particles had water molecules, and the water did not evaporate and disperse. Thus, the particles had fewer internal channels and surface pores. Composite particles without calcination or with a low calcination The surface water of the composite particles, the internal bound water, and some impurities in the pores were removed by calcination at high temperature. This reduced the effect of the water film resistance on the adsorption, so the adsorption increased. The surface of the uncalcined particles had water molecules, and the water did not evaporate and disperse. Thus, the particles had fewer internal channels and surface pores. Composite particles without calcination or with a low calcination temperature (400 • C) were easily pulverized in the aqueous solution and did not achieve the required strength. Increasing the calcination temperature increased the adhesiveness of the silicate compound formed by Na 2 CO 3 , SiO 2 , and Al 2 O 3 , and the mechanical strength of the particles increased. However, when the calcination temperature was too high (550 • C), the evaporation and decomposition were exacerbated. Moisture in the montmorillonite structure was removed, the structure was destroyed and collapsed, and the layered structure disappeared. This reduced the internal specific surface area, which decreased the adsorption quantity [48,49]. The destruction of the montmorillonite structure made the release of alkalinity difficult, which degraded the synergistic adsorption-coagulation effect. When the temperature was lower than 550 • C, the surface water and water in the pores were mainly lost, and Na 2 CO 3 decomposed into CO 2 . The water vapor and CO 2 were discharged, which left pores and channels inside and on the surface of the composite particles. The channels and voids provided more adsorption sites for heavy metal ions, which provided more channels for alkalinity release and facilitated the removal of heavy metal ions. In conclusion, the optimum calcination temperature was determined to be 500 • C.

Determination of the Calcination Time
To determine the calcination time, the bentonite-steel slag proportion was 5:5, the Na 2 CO 3 content was 5%, the aging time was 12 h, the calcination particle size was 2 mm, and the calcination temperature was 500 • C. Different composite particles were produced with calcination times of 40 min, 60 min, 90 min, and 120 min. Figure 6 shows the results for the adsorption amount, alkalinity release amount, and loss rate. Increasing the calcination time reduced the adsorption effect, speed, and amount. Composite particles with a calcination time of 120 min adsorbed 4.35 mg/g, 4.44 mg/g, and 3.56 mg/g of Pb(II), Cd(II), and Cr(III), respectively, so the adsorption effect was not satisfactory. Composite particles with a calcination time of 90 min adsorbed 4.82 mg/g, 4.67 mg/g, and 3.76 mg/g of Pb(II), Cd(II), and Cr(III), respectively, so the adsorption of Cr(III) was not satisfactory. Composite particles with calcination times of 40 min and 60 min adsorbed more than 4.82 mg/g of Pb(II), Cd(II), and Cr(III), so the removal effect was excellent. As the calcination time increased, both the loss rate and alkalinity release amount decreased. Composite particles with calcination times of 40 min, 60 min, 90 min, and 120 min had loss rates of 2.14%, 0.88%, 0.65%, and 0.44%, respectively. Composite particles with a calcination time of 40 min had a loss rate more than twice that of particles with a calcination time of 60 min. Composite particles with calcination times of 40 min, 60 min, 90 min, and 120 min had alkalinity release amounts of 16.52 mg/g, 14.26 mg/g, 13.51 mg/g, and 11.01 mg/g, respectively. As the calcination time increased, Na 2 CO 3 decomposed and released CO 2 , while the water evaporated continuously. A large amount of CO 2 and water vapor overflow increased the internal pore size, and the internal specific surface area decreased, which reduced the adsorption performance. Long calcination times caused a sufficient reaction between Na 2 CO 3 and Si and Al oxides, so the amount of silicate compound formed satisfied the requirements for particle cementation [50]. As the particle strength increased, the loss rate decreased; however, increasing the calcination time made it more difficult to release the alkalinity. In conclusion, the optimum calcination time was 60 min. calcination time of 60 min. Composite particles with calcination times of 40 min, 60 min, 90 min, and 120 min had alkalinity release amounts of 16.52 mg/g, 14.26 mg/g, 13.51 mg/g, and 11.01 mg/g, respectively. As the calcination time increased, Na2CO3 decomposed and released CO2, while the water evaporated continuously. A large amount of CO2 and water vapor overflow increased the internal pore size, and the internal specific surface area decreased, which reduced the adsorption performance. Long calcination times caused a sufficient reaction between Na2CO3 and Si and Al (d) represents the adsorption quantity by composite particles with different calcination times at 120min. (e) represents the alkalinity release amount and loss rate by composite particles with different calcination times at 120min.

Orthogonal Experimental Study
The orthogonal experimental design and results are shown in Table 3.

Orthogonal Experimental Study
The orthogonal experimental design and results are shown in Table 3.

Range Analysis of Orthogonal Experimental Results
Range analysis was performed to examine the results for the five indices: the Pb(II), Cd(II), and Cr(III) adsorption amounts (the larger the better), alkalinity release amount (the larger the better), and loss rate (the smaller the better). The optimum level and rank of dominant factors for each index were determined. Tables 4 and 5 present the results. The optimum level combinations for the Pb(II), Cd(II), and Cr(III) adsorption amounts were A 3 B 2 C 1 D 2 , A 3 B 2 C 1 D 1 , and A 3 B 2 C 1 D 1 , respectively. The optimum level combination for the alkalinity release amount was A 3 B 3 C 1 D 1 , and the optimum level combination for the loss rate was A 3 B 2 C 3 D 3 . Because the optimum level combinations of the five indices were inconsistent, the optimum conditions needed to be considered comprehensively according to the order of the factors of the five indices.  Note: k 1 represents the average adsorbent quantity, alkalinity, and loss rate values of level 7:3, 3%, 450 • C, and 40 min. k 2 represents the average adsorbent quantity, alkalinity, and loss rate values of level 6:4, 5%, 500 • C, and 60 min. k 3 represents the average adsorbent quantity, alkalinity, and loss rate values of level 5:5, 8%, 550 • C, and 90 min. R represents the range value, which is the difference between the maximum value of k 1 , k 2 , k 3 and the minimum value of k 1 , k 2 , k 3 . Optimum level represents the highest value of k 1 , k 2 , k 3 . Dominant factors rank represents the R values in descending order.

Factor A
The five indices showed no contradiction for the optimum level of factor A. Thus, A 3 was selected for factor A.

Factor B
The five indices were not uniform in the choice of factor B; thus, this factor needed to be considered comprehensively. According to the order of factors, factor B had the fourth-ranked influence on the adsorption amounts of Pb(II), Cd(II), and Cr(III) and the alkalinity release amounts, so it was a secondary factor. It had the third-ranked influence on the loss rate, so the loss rate was considered first. The optimum level for the loss rate was B 2 , which was also the optimum level for the Pb(II), Cd(II), and Cr(III) adsorptions. For the alkalinity release, B 2 was only beaten by B 3 , so it could also achieve a good alkalinity release effect. In conclusion, B 2 was selected for factor B.
3. Factor C Factor C had the first-ranked influence on all five indices. The optimum level of the Pb(II), Cd(II), and Cr(III) adsorptions and the alkalinity release was C 1 . The optimum level of the loss rate was C 3 . Thus, C 1 should generally be selected. However, the loss rate had a much larger k 1 value than the k 2 and k 3 values, which means that the loss rate would be large with C 1 and the strength requirement cannot be met. Thus, C 1 was excluded. If C 3 was selected, the Pb(II), Cd(II), and Cr(III) adsorption amounts and alkalinity amount would be the lowest. Thus, C 3 was excluded. Thus, C 2 was selected for factor C, so that good results would be achieved for all five indices.

Factor D
Factor D had the third-ranked effect on the alkalinity release quantity, and second-ranked influence on the other four indices. First, the adsorption amounts of Pb(II), Cd(II), and Cr(III) and the loss rate were considered. The optimum levels were D 2 for the Pb(II) adsorption amount, D 1 for the Cd(II) and Cr(III) adsorption amounts, and D 3 for the loss rate. Generally, D 1 should be selected. However, the loss rate with D 1 was too high to meet the strength requirement, so D 1 was excluded. Second, the adsorption amounts of Pb(II), Cd(II), and Cr(III) were lowest at D 3 , so D 3 was also excluded. Finally, since the values of k 2 and k 3 of the loss rate were not much different from each other and were far less than the k 1 value, and the amounts of Pb(II), Cd(II), and Cr(III) adsorption and alkalinity release at D 2 were second only to the optimum level, D 2 was selected for factor D.
The optimum process conditions for the orthogonal experiment were finally determined to be A 3 B 2 C 2 D 2 . This converts to a bentonite-steel slag proportion of 5:5, Na 2 CO 3 content of 5%, calcination temperature of 500 • C, and calcination time of 60 min. Based on the single-factor experimental results, the aging time was set to 12 h, and the calcination particle size was set to 2 mm. Finally, a verification test was carried out under the above optimum process conditions. The adsorption amounts of Pb(II), Cd(II), and Cr(III) were 4.98 mg/g, 4.95 mg/g, and 4.86 mg/g, respectively. The alkalinity release amount was 14.28 mg/g, and the loss rate was 0.86%. These were the best values among the test results, so the optimum process conditions were successfully verified.
The optimum preparation process for BSC was determined via single-factor and orthogonal experiments. The simulated AMD with an initial concentration of Pb(II), Cd(II), and Cr(III) of 50 mg/L and initial PH from 3.0 to 3.5 was treated with the optimum BSC. After treatment, the ion removal effect was more than 97%, the PH of the solution was from 6.5 to 8.5, and the particles were easy to separate. Thus, it is an excellent and cheap adsorbent that can be used for the treatment of AMD with heavy metal ions.

Adsorption Isotherms
The Langmuir, Freundlich, Dubinin-Radushkevich (D-R), and Brunauer-Emmett-Teller (BET) models were used to analyze the experimental data to explain the adsorption mechanism of Pb(II) on BSC.
The Langmuir isotherm model [51] can be expressed as follows: where C e is the equilibrium solute concentration (mg/L), q e is the adsorption amount at equilibrium (mg/g), q m is the monolayer saturation capacity (mg/g), and b is the Langmuir constant (L/mg). The Freundlich isotherm model can be expressed as follows: ln q e = lnK F + 1 n lnC e (9) where C e and q e are defined in the same manner as in Equation (8), K F is the Freundlich constant (L/g) indicating the adsorption capacity, and n is the isotherm constant indicating the adsorption intensity.
The D-R model can be expressed as follows: where q m is the monolayer saturation capacity (mol/g), k is the model constant of adsorption energy (mol 2 /kJ 2 ), and ε is the Polanyi potential, which is given by: where the unit for E should in mol/L. The mean free energy of adsorption E is: The BET model can be expressed as follows: where C e and q e are defined in the same manner as in Equation (8), q 0 is the monolayer saturation capacity (g/g), C s is the saturated concentration of the adsorbate (g/L), and B is the BET constant. It can be seen from Table 6 that the fitting effect of the four isothermal models is good, and the correlation coefficients of Langmuir and BET models are relatively high, indicating that the Langmuir and BET models are more suitable to describe the isothermal adsorption process than the other models. It should be noted that the adsorption of heavy metal ions by bentonite satisfied the Langmuir model. In addition, the alkalinity released by BSC reacted with Pb(II), Cd(II), and Cr(III) to form a hydroxide, which accumulated layer by layer on BSC, which continued to adsorb Pb(II), Cd(II), and Cr(III). A synergistic adsorption-coagulation effect occurred, leading to the appearance of multiple layers locally on the surface of BSC, which satisfied the BET model. For Pb(II), Cd(II), and Cr(III) adsorption by BSC, the monolayer saturated adsorption capacities calculated via the Langmuir isothermal model were 53.53 mg/g, 28.97 mg/g, and 17.81 mg/g, respectively, which was, in essence, the same as that calculated using the BET model. The adsorption of Pb(II), Cd(II), and Cr(III) on BSC satisfied the BET model.  Figure 7 shows the SEM image of the raw materials and optimum BSC used in the study. From Figure 7a, it can be seen that there is no layered structure in bentonite, and there are only a few pores on its surface. Steel slag (Figure 7b) has a non-layered, irregular, and loose structure. Before calcination (Figure 7c), water molecules were present in BSC, and the particles had a compact internal structure. However, after calcination, layer formation was visible in optimum BSC (Figure 7d), and its surface was rough and had many pores that were conducive to adsorption. Table 7 shows the textural properties of bentonite, steel slag, BSC before calcination, and optimum BSC. BET adsorption studies show that the specific surface area (S BET ) of the optimum BSC is 130.6 m 2 /g with an average pore radius of 8.4 nm, and the total pore volume is 5.14 cm 3 /g. These values are significantly higher than those of bentonite, steel slag, and uncalcined BSC. Upon calcination of BSC, water evaporates, and Na 2 CO 3 is decomposed into CO 2 , resulting in the formation of numerous pores in BSC. This reflects the observed increase in the pore radius, total pore volume, and S BET values. textural properties of bentonite, steel slag, BSC before calcination, and optimum BSC. BET adsorption studies show that the specific surface area (SBET) of the optimum BSC is 130.6 m 2 /g with an average pore radius of 8.4 nm, and the total pore volume is 5.14 cm 3 /g. These values are significantly higher than those of bentonite, steel slag, and uncalcined BSC. Upon calcination of BSC, water evaporates, and Na2CO3 is decomposed into CO2, resulting in the formation of numerous pores in BSC. This reflects the observed increase in the pore radius, total pore volume, and SBET values.    Figure 8 shows the XRD patterns of bentonite, steel slag, and optimum BSC. The main mineral components of bentonite are montmorillonite, quartz, and feldspar. The bentonite used in this study was sodium bentonite and the spacing between its layers was found to be d (001) = 1.287 nm. The position of the d (060) peaks varies for the different types of montmorillonites. When d (060) is between 0.149 and 0.151 nm, montmorillonite has a dioctahedral structure; whereas if d (060) is between 0.153 and 0.155 nm, then the crystal structure is trioctahedral. In the XRD pattern of bentonite ( Figure 8a) the d (060) value was 0.1498 nm, this confirms that the montmorillonite had a dioctahedral structure [52]. In steel slag (Figure 8b), Ca2SiO4, Na4SiO4, and Ca(OH)2 are the main mineral components, whereas it is SiO2, Ca2SiO4, Na2AlSi3O8OH, NaAlSi2O6, NaFeSi2O6, Ca3Fe3(SiO4)3 for optimum BSC (Figure 8c). The position of the d (001) peak was found to be 1.549 nm for the optimum BSC (Figure 8c). This indicates that the layer spacing increased after the composite particles were calcined and modified, and some new substances entered the interlayer of montmorillonite. In optimum BSC, d (060) = 0.1505 nm (Figure 8c) and the montmorillonite retained its dioctahedral structure, indicating that the structure of the composite particles did not change after calcination. Upon calcination some minerals remained the same, whereas a few new minerals, such as NaAlSi2O6, NaFeSi2O6, and Ca3Fe3(SiO4)3, were generated. The composition of quartz is SiO2 and Na2AlSi3O8OH. Montmorillonite and Ca2SiO4 are the alkaline phases. The newly formed silicates satisfied the requirements for BSC   Figure 8 shows the XRD patterns of bentonite, steel slag, and optimum BSC. The main mineral components of bentonite are montmorillonite, quartz, and feldspar. The bentonite used in this study was sodium bentonite and the spacing between its layers was found to be d (001) = 1.287 nm. The position of the d (060) peaks varies for the different types of montmorillonites. When d (060) is between 0.149 and 0.151 nm, montmorillonite has a dioctahedral structure; whereas if d (060) is between 0.153 and 0.155 nm, then the crystal structure is trioctahedral. In the XRD pattern of bentonite ( Figure 8a) the d (060) value was 0.1498 nm, this confirms that the montmorillonite had a dioctahedral structure [52]. In steel slag (Figure 8b), Ca 2 SiO 4 , Na 4 SiO 4 , and Ca(OH) 2 are the main mineral components, whereas it is SiO 2 , Ca 2 SiO 4 , Na 2 AlSi 3 O 8 OH, NaAlSi 2 O 6 , NaFeSi 2 O 6 , Ca 3 Fe 3 (SiO 4 ) 3 for optimum BSC (Figure 8c). The position of the d (001) peak was found to be 1.549 nm for the optimum BSC (Figure 8c). This indicates that the layer spacing increased after the composite particles were calcined and modified, and some new substances entered the interlayer of montmorillonite. In optimum BSC, d (060) = 0.1505 nm (Figure 8c) and the montmorillonite retained its dioctahedral structure, indicating that the structure of the composite particles did not change after calcination. Upon calcination some minerals remained the same, whereas a few new minerals, such as NaAlSi 2 O 6 , NaFeSi 2 O 6 , and Ca 3 Fe 3 (SiO 4 ) 3 , were generated. The composition of quartz is SiO 2 and Na 2 AlSi 3 O 8 OH. Montmorillonite and Ca 2 SiO 4 are the alkaline phases. The newly formed silicates satisfied the requirements for BSC cementation. Thus, the optimum BSC obtained by calcination retained its dioctahedral structure. Since the layer spacing increased in the optimum BSC, its adsorption performance for heavy metal ions enhanced significantly. Moreover, the presence of alkaline substances in the optimum BSC shows that it has the common characteristics of bentonite and steel slag, which can absorb heavy metal ions and reduce the acidity at the same time.

FT-IR Analysis
In the FTIR spectrum of bentonite (Figure 9a), a strong hydroxyl stretching vibration peak (Al-OH) appeared at 3826.94 cm −1 . The stretching vibration peak of the hydroxyl group from the adsorbed

FT-IR Analysis
In the FTIR spectrum of bentonite (Figure 9a), a strong hydroxyl stretching vibration peak (Al-OH) appeared at 3826.94 cm −1 . The stretching vibration peak of the hydroxyl group from the adsorbed water between the layers occurred at 3439.84 cm −1 , whereas the H-O-H bending vibration peak of the water present between the layers of montmorillonite occurred at 1638.06 cm −1 . The Si-O-Si stretching vibration absorption peak near 1040 cm −1 showed two splits at 1087.74 cm −1 and 1037.74 cm −1 . This split peak indicates that the montmorillonite layers contained Na + ions [53]. In the FTIR spectrum of steel slag (Figure 9b), the hydroxyl stretching vibration peak of internal water occurred at 3386. 32  In the infrared spectrum of BSC before calcination (Figure 9c), the hydroxyl stretching vibration of the interlayer water at 3439.84 cm −1 moved to a low frequency of 3429.14 cm −1 , indicating that the interlayer water changed. After calcination (Figure 9d), the characteristic peaks of the hydroxyl water at 3429.14 cm −1 and 1638.83 cm −1 became weaker. This implies that calcination removed the water between the layers, making the layer spacing larger. Also, the two split peaks near 1040 cm −1 shifted to 1088.88 cm −1 and 1035.60 cm −1 . This was attributed to the reaction of the components in steel slag with the interlayer Na + of montmorillonite. After calcination, the bimodal peaks still existed, suggesting the presence of exchangeable Na + in the interlayers. Before calcination, the characteristic absorption peaks of Si-O and Al-O in the montmorillonite structure were between 1000 and 450 cm −1 . The coupled vibration absorption of M-O formed by metal ions with oxygen was also present in the spectrum. After calcination, only the Si-O stretching vibration absorption peak near 792.47 cm −1 and Si-O bending vibration absorption peak near 471.54 cm −1 were obvious. Other vibration peaks weakened or disappeared after calcination, due to the removal of the impurities between the layers of montmorillonite.

Conclusions
The preparation procedure and mechanism for optimizing the BSC were studied thoroughly in this experiment. The single-factor experimental results determined an optimum aging time of 12 h and optimum calcination particle size of 2 mm. The optimum bentonite-steel slag proportion was 5:5. The optimum Na2CO3 content was 5%. The optimum calcination temperature was 500 °C. The optimum calcination time was 60 min.
Based on the results of the single-factor experiment, an orthogonal experiment was performed. The optimum process conditions for preparing the composite particles were determined by range analysis: a bentonite-steel slag proportion of 5:5, Na2CO3 amount of 5% of the total mass, aging time of 12 h under lightproof conditions, calcination particle size of 2 mm, calcination temperature of 500 °C, and calcination time of 60 min. In terms of the adsorption performance and particle strength, the composite particles under the optimum process conditions performed better than the particles prepared by other processes and were defined as the optimum BSC.
The isothermal adsorption data of the optimum BSC were analyzed using the Langmuir, Freundlich, D-R, and BET models. The Langmuir and BET models led to the best isotherms. A synergistic adsorption-coagulation effect occurred, leading to the appearance of multiple layers locally on the surface of BSC, which satisfied the BET model. SEM and BET analysis revealed that after calcination, the surface of the optimum BSC was rough and had a layered structure. The SBET, average pore radius, and the total pore volume were found to  In the infrared spectrum of BSC before calcination (Figure 9c), the hydroxyl stretching vibration of the interlayer water at 3439.84 cm −1 moved to a low frequency of 3429.14 cm −1 , indicating that the interlayer water changed. After calcination (Figure 9d), the characteristic peaks of the hydroxyl water at 3429.14 cm −1 and 1638.83 cm −1 became weaker. This implies that calcination removed the water between the layers, making the layer spacing larger. Also, the two split peaks near 1040 cm −1 shifted to 1088.88 cm −1 and 1035.60 cm −1 . This was attributed to the reaction of the components in steel slag with the interlayer Na + of montmorillonite. After calcination, the bimodal peaks still existed, suggesting the presence of exchangeable Na + in the interlayers. Before calcination, the characteristic absorption peaks of Si-O and Al-O in the montmorillonite structure were between 1000 and 450 cm −1 . The coupled vibration absorption of M-O formed by metal ions with oxygen was also present in the spectrum. After calcination, only the Si-O stretching vibration absorption peak near 792.47 cm −1 and Si-O bending vibration absorption peak near 471.54 cm −1 were obvious. Other vibration peaks weakened or disappeared after calcination, due to the removal of the impurities between the layers of montmorillonite.

Conclusions
The preparation procedure and mechanism for optimizing the BSC were studied thoroughly in this experiment. The single-factor experimental results determined an optimum aging time of 12 h and optimum calcination particle size of 2 mm. The optimum bentonite-steel slag proportion was 5:5. The optimum Na 2 CO 3 content was 5%. The optimum calcination temperature was 500 • C. The optimum calcination time was 60 min.
Based on the results of the single-factor experiment, an orthogonal experiment was performed. The optimum process conditions for preparing the composite particles were determined by range analysis: a bentonite-steel slag proportion of 5:5, Na 2 CO 3 amount of 5% of the total mass, aging time of 12 h under lightproof conditions, calcination particle size of 2 mm, calcination temperature of 500 • C, and calcination time of 60 min. In terms of the adsorption performance and particle strength, the composite particles under the optimum process conditions performed better than the particles prepared by other processes and were defined as the optimum BSC.
The isothermal adsorption data of the optimum BSC were analyzed using the Langmuir, Freundlich, D-R, and BET models. The Langmuir and BET models led to the best isotherms. A synergistic adsorption-coagulation effect occurred, leading to the appearance of multiple layers locally on the surface of BSC, which satisfied the BET model.
SEM and BET analysis revealed that after calcination, the surface of the optimum BSC was rough and had a layered structure. The S BET , average pore radius, and the total pore volume were found to be 130.6 m 2 /g, 8.4 nm, and 5.14 cm 3 /g respectively. From XRD analysis, the optimum BSC layer spacing was calculated to be 1.549 nm, and the dioctahedral structure remained unaltered. Besides this, the XRD pattern showed the presence of both montmorillonite and alkaline substances. The silicates formed satisfied the conditions for BSC cementation. From the FTIR spectrum, exchangeable Na + between the layers of the optimum BSC was detected. Moisture and impurities were removed by calcination.
The optimum BSCs have the synergistic adsorption-coagulation effect and overcome the limitations of a single material, single method, and single function. It is a new multifunctional protective material for mining environments that can simultaneously remove heavy metal ions and reduce acidity. The experimental study reported in this paper provides a new material for treatment of AMD containing heavy metal ions. Quantification of the optimal conditions and factors for AMD remediation by BSC will improve the cost effectiveness of this method. This work will be of broad interest to AMD remediation specialists in the coal and sulfide metal mining sectors.