Synthesis of Magnetic Microspheres with Sodium Alginate and Activated Carbon for Removal of Methylene Blue

Based on the adsorption performance of composite microspheres with activated carbon (AC) and sodium alginate (SA), as well as the magnetic property of Fe3O4, we designed and explored an efficient strategy to prepare a unique, multifunctional Fe3O4/AC/SA composite absorbent (MSA-AC) that extracted dye from aqueous solution. The composite exhibited the following advantages: rapid and simple to prepare, environmentally friendly process, low-cost, recyclability, and multi-functionality. The physicochemical properties of the prepared magnetic microspheres were measured, and methylene blue (MB) was selected to investigate the performance of the magnetic absorbent. The results showed a maximum adsorption capacity of 222.3 mg/g for MB. Adsorption studies revealed that the data of adsorption isotherms and kinetics fit the pseudo-second-order kinetic model and Langmuir isotherm model.


Introduction
Dyes are indispensable chemical compounds in textiles, paper-making, cosmetics and other industries, and their use leads to large quantities of wastewater [1]. Due to the number of organic contaminants, dye wastewater is toxic, carcinogenic, and causes serious environmental problems. Furthermore, dye wastewater has been linked to genetic mutation in human beings [2][3][4] because the organic contaminants can accumulate in living tissues [1,5]. The development of a method to separate and break down the individual organic constituents in order to reuse dye wastewater is not only of great importance for environmental safety but also as a sustainable development strategy [5,6].
Undoubtedly, the removal of dye from waste effluents is an environmental concern, and various dye wastewater treatment technologies have been investigated, such as chemical precipitation, adsorption [2,7,8], membrane filtration [9,10], biological treatment [11] and photocatalytic degradation [4,12]. However, most of these methods are not widely utilized because of efficiency, environmental impact and cost. Adsorption is one of the most effective and feasible methods for wastewater treatment due to its relatively low cost, ease of operation, fewer harmful secondary products [13] and toxic pollutants. Activated carbon (AC) is one of the most extensively investigated materials for the removal of various pollutants problems because of its high surface area, porous texture to accommodate large organic molecules, non-toxicity, chemical inertness, and high capability for adsorbing a broad range of contaminants [14][15][16]. Numerous studies have been conducted in an effort to develop high surface area AC from a myriad of inexpensive precursors, such as sugarcane, bamboo, straw, fruit peel, and excess sludge [1,13,17,18]. However, the optimization of the activation reaction for the adsorption of dyes is restricted because of aggregate formation and regeneration cost.
Sodium alginate (SA) is an interesting natural polymer that is abundant, biodegradable, hydrophilic, low-cost, and easily processed into various shapes [19]. SA is widely used as a bioaffinity carrier material, and due to the abundant and easily modified carboxyl and hydroxyl groups on the backbone of the molecule, it was investigated to enhance the adsorption preference of dyes [20,21]. Additionally, SA is sensitive to temperature and pH [22]. Compared with traditional hydrogels, direct preparation of SA/AC microsphere hydrogels is simpler, produces more uniform particles, and reduces AC aggregation [23]. Moreover, for dye wastewater treatment, AC and SA have attracted much attention due to their unique pore structures and extremely large surface areas, properties that allow for the effective adsorption of dyes.
While SA/AC microspheres have a large reactive surface area and high adsorption capability, their recovery and reusability from aqueous solution are crucial factors for further applications. Fe 3 O 4 , as a magnetic material, has gained much attention as a means to provide fast and efficient adsorption [5,24,25]. Yang et al. [26] prepared Fe 3 O 4 /histidine composite nanoclusters, which exhibited remarkably efficient adsorption of proteins. Wan et al. [27] successfully fabricated a hydrophilic enrichment composite that demonstrated robustness and feasibility for profiling glycoproteomics in real biological samples. With the increasing number of environmental problems, a new, facile, and environmentally friendly method of synthetic polymerization is urgently needed.
To our knowledge, there has been no report of the application of Fe 3 O 4 /AC/SA particles for adsorbing dyes. In this study, we prepared Fe 3 O 4 /SA/AC microspheres and extracted dyes from aqueous solution via a simple two-step route: synthesis of Fe 3 O 4 by coprecipitation and synthesis of advanced composite materials incorporated with AC and SA, as well as Fe 3 O 4 . Methylene blue (MB) was selected as a target dye to investigate the performance of the magnetic microspheres because of its toxicity, mutagenicity and carcinogenic potential.

Materials Characterization
Powder X-ray diffraction (XRD, Shimadzu XRD-7000, SHIMADZU LIMITED Hitachi High Technologies, Tokyo, Japan) analyses were performed with Cu-Kα radiation (λ = 1.5418 Å, 40 kV, 30 mA), and patterns were recorded in the range of 2θ = 10 • -80 • with a step size of 0.02 • . Scanning electron microscopy (SEM) measurements were carried out on a Hitachi S-3400N detector (Hitachi High Technologies, Tokyo, Japan). Fourier transform infrared spectroscopy (FT-IR, Nicolet 380, Nanjing Lear Instrument Equipment Co., Nanjing, China) spectra were recorded by using the KBr pellet method. Magnetic properties of the samples were tested on a vibrating sample magnetometer (VSM, MPMS3 SQUID, Quantum Design, San Diego, CA, USA). Brunauer-Emmett-Teller (BET, Micromeritics asap2460, Micromeritics Instrument Corp, Atlanta, GA, USA) specific surface area of the materials was determined from nitrogen gas adsorption-desorption at the boiling point of liquid nitrogen (−196 • C).

Synthesis of the Fe 3 O 4
The superparamagnetic nanoparticles (Fe 3 O 4 ) were obtained by the aqueous co-precipitation method with minor modifications [27,28]. In a three-necked flask, 1.72 g FeCl 2 ·4H 2 O and 4.72 g FeCl 3 ·6H 2 O were dissolved in 80 mL deionized water. Under a nitrogen atmosphere, the mixture was vigorously stirred (1000 rpm) at 80 • C until the salts were completely dissolved. Then, 20 mL of ammonium hydroxide (25% in water) was added dropwise to the reaction mixture with vigorous stirring. A change in color from an orange-red solution to a black suspension signified the formation and precipitation of magnetic particles. After 30 min, the reaction was stopped and the suspension was cooled to room temperature. The final products were collected by a permanent magnet and were thoroughly washed with ethanol and deionized water several times. The obtained Fe 3 O 4 particles were dried at 25 • C under vacuum oven for 24 h.

Synthesis of SA and Fe 3 O 4 -SA-AC Microsphere
A 2.0 g amount of sodium alginate was added to 100 mL distilled water and stirred vigorously for 12 h. A 50 mL aliquot of sodium alginate solution was added slowly into 2% CaCl 2 solution with a syringe (1 mL). Then, the product (SA) was cured for 30 min, washed several times with deionized water, and sublimated for 12 h. The 50 mL sodium alginate was added into a 250 mL three-neck flask with 0.1 g Fe 3 O 4 . Next, three different amounts of AC (0.1, 0.2 and 0.3 g) were added in the solution, then sonicated and stirred for 1 h. Then, they were stirred an additional 1 h without sonication. The mixed solution was slowly added dropwise into 2% CaCl 2 solution with a syringe (1 mL). The final products (MSA-AC1, MSA-AC2, and MSA-AC3) were cured for 30 min, collected by a permanent magnet, washed several times with deionized water, and sublimated 12 h.

Batch Experiments
Removal of MB was carried out in a 150 mL Erlenmeyer flask containing MB solution (50 mL) and adsorbent (100 mg). A required amount of experimental parameters influencing the MB dye adsorption, including contact time (0-270 min), initial pH (3)(4)(5)(6)(7)(8)(9)(10)(11) of the dye solution, initial concentration (500-700 mg/L), and temperature (298-310 K) were examined. In the adsorption experiments, the pH value of MB solution was maintained by using HCl (0.1 mol/L) or NaOH (0.1 mol/L) solutions. All batch experiments were fully agitated on a BSD-TX345 Thermostat oscillator (Shanghai Instruments Inc., Shanghai, China) at a fixed speed of 150 r/min to attain adsorption equilibrium. Afterward, the adsorbent was separated from the solution by a permanent magnet after adsorption, and the residual concentration of dyes in the solution was analyzed by a UV-Vis spectrophotometer (SHIMADZU, UVmini-1240, Shimadzu Instrument Co., Tokyo, Japan) at the maximum absorbance wavelength of 664 nm (for MB). All samples were measured three times and average values were taken. Adsorption capacity and dye removal efficiency (DRE) were calculated according to Equations (1) and (2): where q e (mg/g) is adsorption capacity; C 0 (mg/L) and C e (mg/L) are MB concentrations at initial and equilibrium; V (L) is the volume of solution, and W (g) is the mass of the adsorbent (dry).

FT-IR
FT-IR spectra were measured to further investigate the fabrication process ( Figure 1). Characteristic peaks at 1070, 1620 and 3416 cm −1 are caused by -OH stretching vibration, 1430 cm −1 is attributed to -CH2-stretching vibration [20,25]. Compared to the spectra of AC and SA, the new band at 564 cm −1 can be attributed to the stretching vibrations of Fe-O in MSA-AC2, and the enhanced peaks 3416 cm −1 and 1620 cm −1 indicate the presence of Fe3O4. This result indicated that the MSA-AC composite microspheres successfully cross-linked Fe3O4 and AC with sodium alginate, and Fe3O4 had not changed in the cross-linking process.

SEM Analysis
The SEM image of the prepared SA, AC and MSA-AC2 materials is shown in Figure 2. The AC displays a fluffy and rough surface with irregular patches and obvious pores. The combination of Fe3O4 and AC with the cross-linking of sodium alginate (MSA-AC2) has a porous, spongy structure. Additionally, many pores are observed on the outer surface, and the distribution of Fe3O4 particles were exclusively inset on the surface of hydrogel fiber. This may give rise to some aggregation of Fe3O4 on the surface, making particles appear larger, as seen in the image [29][30][31].

SEM Analysis
The SEM image of the prepared SA, AC and MSA-AC2 materials is shown in Figure 2. The AC displays a fluffy and rough surface with irregular patches and obvious pores. The combination of Fe 3 O 4 and AC with the cross-linking of sodium alginate (MSA-AC2) has a porous, spongy structure. Additionally, many pores are observed on the outer surface, and the distribution of Fe 3 O 4 particles were exclusively inset on the surface of hydrogel fiber. This may give rise to some aggregation of Fe 3 O 4 on the surface, making particles appear larger, as seen in the image [29][30][31].

FT-IR
FT-IR spectra were measured to further investigate the fabrication process ( Figure 1). Characteristic peaks at 1070, 1620 and 3416 cm −1 are caused by -OH stretching vibration, 1430 cm −1 is attributed to -CH2-stretching vibration [20,25]. Compared to the spectra of AC and SA, the new band at 564 cm −1 can be attributed to the stretching vibrations of Fe-O in MSA-AC2, and the enhanced peaks 3416 cm −1 and 1620 cm −1 indicate the presence of Fe3O4. This result indicated that the MSA-AC composite microspheres successfully cross-linked Fe3O4 and AC with sodium alginate, and Fe3O4 had not changed in the cross-linking process.

SEM Analysis
The SEM image of the prepared SA, AC and MSA-AC2 materials is shown in Figure 2. The AC displays a fluffy and rough surface with irregular patches and obvious pores. The combination of Fe3O4 and AC with the cross-linking of sodium alginate (MSA-AC2) has a porous, spongy structure. Additionally, many pores are observed on the outer surface, and the distribution of Fe3O4 particles were exclusively inset on the surface of hydrogel fiber. This may give rise to some aggregation of Fe3O4 on the surface, making particles appear larger, as seen in the image [29][30][31].

Thermogravimetric analyzer Analysis
Thermogravimetric analyzer (TGA) measurements were carried out by weighing a powder sample of 5-10 mg and loading it into a platinum pan. The mass change in the temperature range from 30 to 800 °C at a heating rate of 10 °C·min -1 under a nitrogen flow was monitored and recorded.
The result of TGA on the microspheres was investigated and presented in Figure 4. The TGA curves of the prepared microspheres gave four mass loss processes before 800 °C. The first mass loss, which was approximately 13.3% at <100 °C, is due to the evaporation of water in the magnetite MSA-AC2. In the second mass loss of about 6.5% between 100 and 220 °C, the decarboxylation of SA released carbon dioxide and part of the products were carbonized. The third mass loss of about 10.7%

Thermogravimetric analyzer Analysis
Thermogravimetric analyzer (TGA) measurements were carried out by weighing a powder sample of 5-10 mg and loading it into a platinum pan. The mass change in the temperature range from 30 to 800 °C at a heating rate of 10 °C·min -1 under a nitrogen flow was monitored and recorded.
The result of TGA on the microspheres was investigated and presented in Figure 4. The TGA curves of the prepared microspheres gave four mass loss processes before 800 °C. The first mass loss, which was approximately 13.3% at <100 °C, is due to the evaporation of water in the magnetite MSA-AC2. In the second mass loss of about 6.5% between 100 and 220 °C, the decarboxylation of SA released carbon dioxide and part of the products were carbonized. The third mass loss of about 10.7%

Thermogravimetric Analyzer Analysis
Thermogravimetric analyzer (TGA) measurements were carried out by weighing a powder sample of 5-10 mg and loading it into a platinum pan. The mass change in the temperature range from 30 to 800 • C at a heating rate of 10 • C·min -1 under a nitrogen flow was monitored and recorded.
The result of TGA on the microspheres was investigated and presented in Figure 4. The TGA curves of the prepared microspheres gave four mass loss processes before 800 • C. The first mass loss, which was approximately 13.3% at <100 • C, is due to the evaporation of water in the magnetite MSA-AC2. In the second mass loss of about 6.5% between 100 and 220 • C, the decarboxylation of SA released carbon dioxide and part of the products were carbonized. The third mass loss of about 10.7% between 220 and 450 • C is attributed to the thermal decomposition of the aminopropyl groups and bisaldehyde in the nanomaterial. Fourthly, the TGA curve above 600 • C indicates that the organic species in the magnetic composite nanoparticles have been completely decomposed and that the Fe 3 O 4 nanoparticles remain [33,34].
Materials 2016, 9,84 6 of 14 between 220 and 450 °C is attributed to the thermal decomposition of the aminopropyl groups and bisaldehyde in the nanomaterial. Fourthly, the TGA curve above 600 °C indicates that the organic species in the magnetic composite nanoparticles have been completely decomposed and that the Fe3O4 nanoparticles remain [33,34].

VSM Analysis
The magnetic characteristics of the particles were measured by a vibration sample magnetometer (VSM) under an applied magnetic field.
The saturation magnetization (Ms) of Fe3O4 nanoparticles (MNPs) and Fe3O4-SA-AC (MSA-AC) microspheres was taken at 298 K as shown in Figure 5. The VSM curves of MNPs and MSA-AC resemble those of typical superparamagnetic behavior. Both curves present very narrow hysteresis loops and no remnant magnetization could be observed. The maximum saturation magnetization value of MSA-AC2 (9.01 emu/g) is lower than that for bulk magnetite particles (93 emu/g); however, the MSA-AC2 still has adequate magnetization to be easily and quickly separated from the complex sample. The maximum saturation magnetization value of MSA-AC2 decreases due to the magnetically reducing AC combination; and the assembly of the Fe3O4 with AC composite microspheres, using sodium alginate as the cross-linker, was beneficial for retaining high saturation magnetization [26,28]. This result might be explained by the unique structure of the MSA-AC2.   Figure 5. The VSM curves of MNPs and MSA-AC resemble those of typical superparamagnetic behavior. Both curves present very narrow hysteresis loops and no remnant magnetization could be observed. The maximum saturation magnetization value of MSA-AC2 (9.01 emu/g) is lower than that for bulk magnetite particles (93 emu/g); however, the MSA-AC2 still has adequate magnetization to be easily and quickly separated from the complex sample. The maximum saturation magnetization value of MSA-AC2 decreases due to the magnetically reducing AC combination; and the assembly of the Fe 3 O 4 with AC composite microspheres, using sodium alginate as the cross-linker, was beneficial for retaining high saturation magnetization [26,28]. This result might be explained by the unique structure of the MSA-AC2. between 220 and 450 °C is attributed to the thermal decomposition of the aminopropyl groups and bisaldehyde in the nanomaterial. Fourthly, the TGA curve above 600 °C indicates that the organic species in the magnetic composite nanoparticles have been completely decomposed and that the Fe3O4 nanoparticles remain [33,34].

VSM Analysis
The magnetic characteristics of the particles were measured by a vibration sample magnetometer (VSM) under an applied magnetic field.
The saturation magnetization (Ms) of Fe3O4 nanoparticles (MNPs) and Fe3O4-SA-AC (MSA-AC) microspheres was taken at 298 K as shown in Figure 5. The VSM curves of MNPs and MSA-AC resemble those of typical superparamagnetic behavior. Both curves present very narrow hysteresis loops and no remnant magnetization could be observed. The maximum saturation magnetization value of MSA-AC2 (9.01 emu/g) is lower than that for bulk magnetite particles (93 emu/g); however, the MSA-AC2 still has adequate magnetization to be easily and quickly separated from the complex sample. The maximum saturation magnetization value of MSA-AC2 decreases due to the magnetically reducing AC combination; and the assembly of the Fe3O4 with AC composite microspheres, using sodium alginate as the cross-linker, was beneficial for retaining high saturation magnetization [26,28]. This result might be explained by the unique structure of the MSA-AC2.

BET Analysis
The N 2 adsorption/desorption isotherms and pore diameter distribution curves of AC and MSA-AC are shown in Figure 6, and the corresponding parameters of porous structures are listed in Table 1. The pore size distribution suggests that the pore distributions of AC and MSA-AC are 3.826 nm and 3.799 nm, respectively, which is similar to the peak horizontal position (approximately 3.80 nm). Conversely, the pore channels of MSA-AC are more uniform. The surface area and total pore volume are 590.70 m 2 /g, 60.03 m 2 /g, 183.63 m 2 /g, 179.37 m 2 /g and 0.424 cm 3 /g, 0.054 cm 3 /g, 0.153 cm 3 /g, 0.145 cm 3 /g for AC, MSA-AC1, MSA-AC2 and MSA-AC3 respectively. Although the N 2 adsorption amount of MSA-AC is significantly less than AC, the pore size distribution is basically the same. The N 2 adsorption/desorption isotherms of AC and MSA-AC2 correspond to a similar Type IV isotherm with Type H2 hysteresis loop behavior (IUPAC, 1984) [35,36], which indicates that (1) the pores of AC and MSA-AC are with predominantly mesopores; (2) capillary condensation will occur in the pores; and (3) compared with AC, the micropore area of MSA-AC had decreased. Thus, MSA-AC has lower surface area and pore volume when compared with AC.

BET Analysis
The N2 adsorption/desorption isotherms and pore diameter distribution curves of AC and MSA-AC are shown in Figure 6, and the corresponding parameters of porous structures are listed in Table 1. The pore size distribution suggests that the pore distributions of AC and MSA-AC are 3.826 nm and 3.799 nm, respectively, which is similar to the peak horizontal position (approximately 3.80 nm). Conversely, the pore channels of MSA-AC are more uniform. The surface area and total pore volume are 590.70 m 2 /g, 60.03 m 2 /g, 183.63 m 2 /g, 179.37 m 2 /g and 0.424 cm 3 /g, 0.054 cm 3 /g, 0.153 cm 3 /g, 0.145 cm 3 /g for AC, MSA-AC1, MSA-AC2 and MSA-AC3 respectively. Although the N2 adsorption amount of MSA-AC is significantly less than AC, the pore size distribution is basically the same. The N2 adsorption/desorption isotherms of AC and MSA-AC2 correspond to a similar Type IV isotherm with Type H2 hysteresis loop behavior (IUPAC, 1984) [35,36], which indicates that (1) the pores of AC and MSA-AC are with predominantly mesopores; (2) capillary condensation will occur in the pores; and (3) compared with AC, the micropore area of MSA-AC had decreased. Thus, MSA-AC has lower surface area and pore volume when compared with AC.

Adsorption Efficiency of Different MNPs with Different Time on Adsorption of MB
The adsorption efficiencies of AC, SA, MSA, MSA-AC1, MSA-AC2, and MSA-AC3 for MB were evaluated in Figure 7. The adsorption process is divided into two parts. First, MB was quickly adsorbed over 40 min, and the adsorption efficiency of MSA-AC2 achieved was 80%. In the subsequent steps, removal of 89.5% MB was achieved in 150 min. The adsorption percentage was basically unchanged after 150 min. The results were as follows: (1) AC < MSA < SA < MSA-AC1 < MSA-AC3 < MSA-AC2 under the same experimental conditions; (2) adsorption increases with time

Adsorption Efficiency of Different MNPs with Different Time on Adsorption of MB
The adsorption efficiencies of AC, SA, MSA, MSA-AC1, MSA-AC2, and MSA-AC3 for MB were evaluated in Figure 7. The adsorption process is divided into two parts. First, MB was quickly adsorbed over 40 min, and the adsorption efficiency of MSA-AC2 achieved was 80%. In the subsequent steps, removal of 89.5% MB was achieved in 150 min. The adsorption percentage was basically unchanged after 150 min. The results were as follows: (1) AC < MSA < SA < MSA-AC1 < MSA-AC3 < MSA-AC2 under the same experimental conditions; (2) adsorption increases with time and an equilibration time of 150 min. Therefore, MSA-AC2 was employed in subsequent experiments. This increase in adsorption is attributed to the synergistic effect of SA and AC, and increase of surface area [15]. and an equilibration time of 150 min. Therefore, MSA-AC2 was employed in subsequent experiments. This increase in adsorption is attributed to the synergistic effect of SA and AC, and increase of surface area [15].

Effect of pH on Adsorption of MB
The pH condition is an important factor during the adsorption process. According to the previous studies [20,31], adsorption of MB was investigated over a pH range from 3 to 11. While pH values were varied, all other conditions were constant: the optimal temperature was 298 K, the initial concentration was 500 mg/L, the optimal time was 150 min, the volume was 50 mL and the adsorbent dose was 100 mg. The adsorption experiments were carried out in triplicate. As shown in Figure 8, the adsorption efficiency varied for pH range 3-7, while efficiency was unaffected for pH range 7-11. At pH 3, the efficiency of MB was only 21.2%. This is likely due to a large number of hydrogen ions in solution that impart a positive charge on the MSA-AC2 microsphere surface, making attachment of MB to the active sites of MSA-AC2 unfavorable [31,37]. The adsorption efficiency of MB increased from 21.2% to 89.5% with increasing pH from 3 to 7, and this can be attributed to protonation of the hydroxyl and carboxyl groups, allowing the formation of a negative surface charge. In short, the adsorption capability was increased at higher pH values because of the stronger electrostatic interaction that existed between MSA-AC2 active sites and MB. This suggested that the optimal adsorption condition of MB, a cationic dye, via MSA-AC2, was under neutral or alkaline pH [38]. Ultimately, pH 7 that was selected as the absorption via MSA-AC2 was highest at 89.5%.

Effect of pH on Adsorption of MB
The pH condition is an important factor during the adsorption process. According to the previous studies [20,31], adsorption of MB was investigated over a pH range from 3 to 11. While pH values were varied, all other conditions were constant: the optimal temperature was 298 K, the initial concentration was 500 mg/L, the optimal time was 150 min, the volume was 50 mL and the adsorbent dose was 100 mg. The adsorption experiments were carried out in triplicate. As shown in Figure 8, the adsorption efficiency varied for pH range 3-7, while efficiency was unaffected for pH range 7-11. At pH 3, the efficiency of MB was only 21.2%. This is likely due to a large number of hydrogen ions in solution that impart a positive charge on the MSA-AC2 microsphere surface, making attachment of MB to the active sites of MSA-AC2 unfavorable [31,37]. The adsorption efficiency of MB increased from 21.2% to 89.5% with increasing pH from 3 to 7, and this can be attributed to protonation of the hydroxyl and carboxyl groups, allowing the formation of a negative surface charge. In short, the adsorption capability was increased at higher pH values because of the stronger electrostatic interaction that existed between MSA-AC2 active sites and MB. This suggested that the optimal adsorption condition of MB, a cationic dye, via MSA-AC2, was under neutral or alkaline pH [38]. Ultimately, pH 7 that was selected as the absorption via MSA-AC2 was highest at 89.5%.

Effect of pH on Adsorption of MB
The pH condition is an important factor during the adsorption process. According to the previous studies [20,31], adsorption of MB was investigated over a pH range from 3 to 11. While pH values were varied, all other conditions were constant: the optimal temperature was 298 K, the initial concentration was 500 mg/L, the optimal time was 150 min, the volume was 50 mL and the adsorbent dose was 100 mg. The adsorption experiments were carried out in triplicate. As shown in Figure 8, the adsorption efficiency varied for pH range 3-7, while efficiency was unaffected for pH range 7-11. At pH 3, the efficiency of MB was only 21.2%. This is likely due to a large number of hydrogen ions in solution that impart a positive charge on the MSA-AC2 microsphere surface, making attachment of MB to the active sites of MSA-AC2 unfavorable [31,37]. The adsorption efficiency of MB increased from 21.2% to 89.5% with increasing pH from 3 to 7, and this can be attributed to protonation of the hydroxyl and carboxyl groups, allowing the formation of a negative surface charge. In short, the adsorption capability was increased at higher pH values because of the stronger electrostatic interaction that existed between MSA-AC2 active sites and MB. This suggested that the optimal adsorption condition of MB, a cationic dye, via MSA-AC2, was under neutral or alkaline pH [38]. Ultimately, pH 7 that was selected as the absorption via MSA-AC2 was highest at 89.5%.

Effect of Initial Concentration on Adsorption of MB
The adsorption efficiency of the MSA-AC2 is shown in Figure 9. The adsorption process reached equilibrium after approximately 150 min (Figure 7), and 298 K was the optimal temperature for all MB solutions. The adsorption efficiency of MSA-AC2 was about 89.0%, 88.5%, 87.3%, 85.5%, and 81.7% at concentrations of 500, 550, 600, 650 and 700 mg/L, respectively. The results indicate that, for MSA-AC2, the adsorption efficiency of MB decreased with increasing MB concentration.

Effect of Initial Concentration on Adsorption of MB
The adsorption efficiency of the MSA-AC2 is shown in Figure 9. The adsorption process reached equilibrium after approximately 150 min (Figure 7), and 298 K was the optimal temperature for all MB solutions. The adsorption efficiency of MSA-AC2 was about 89.0%, 88.5%, 87.3%, 85.5%, and 81.7% at concentrations of 500, 550, 600, 650 and 700 mg/L, respectively. The results indicate that, for MSA-AC2, the adsorption efficiency of MB decreased with increasing MB concentration.

Adsorption Kinetics Studies
To evaluate the adsorption behavior of MB onto MSA-AC2, a pseudo-first-order (Equation (3)) and pseudo-second-order model (Equation (4)) have been applied to analyze the experimental data [39].
Here, qe (mg/g) is the equilibrium adsorption capacity, qt (mg/g) is the adsorption capacity at time t (min), k1 (1/min) is the pseudo-first-order rate adsorption constant, and k2 (g/mg/min) is the rate constant of the pseudo-second-order rate adsorption constant. The kinetic rate constants k1 and k2, and the correlation coefficients are listed in Table 2. Figure 10 shows that adsorption increased quickly over 60 min, then reached a saturation point. As temperature increases, adsorption quantity reduced, indicating that low temperature is advantageous to the MSA-AC2 adsorption of MB. According to the correlation coefficient, the experimental data was fit better to the pseudo-second-order model (R 2 ≥ 0.997) than the pseudo-first-order model (R 2 ≥ 0.992). Moreover, the qe values were obtained for the pseudo-first-order and pseudo-second-order models, and in the case of the pseudo-second-order model, the theoretical value (qe,cal = 229.89 mg/g, 224.22 mg/g, 211.86 mg/g) was very close to the experimental data (qe = 222.3 mg/g, 212.3 mg/g, 198.8 mg/g). Therefore, the pseudo-second-order model was used to describe the adsorption of MB on MSA-AC2 [12,39]. In previous studies [31,40], adsorption capacity can be associated with the surface chemical property of MSA-AC.

Adsorption Kinetics Studies
To evaluate the adsorption behavior of MB onto MSA-AC2, a pseudo-first-order (Equation (3)) and pseudo-second-order model (Equation (4)) have been applied to analyze the experimental data [39].
Here, q e (mg/g) is the equilibrium adsorption capacity, q t (mg/g) is the adsorption capacity at time t (min), k 1 (1/min) is the pseudo-first-order rate adsorption constant, and k 2 (g/mg/min) is the rate constant of the pseudo-second-order rate adsorption constant. The kinetic rate constants k 1 and k 2 , and the correlation coefficients are listed in Table 2. Figure 10 shows that adsorption increased quickly over 60 min, then reached a saturation point. As temperature increases, adsorption quantity reduced, indicating that low temperature is advantageous to the MSA-AC2 adsorption of MB. According to the correlation coefficient, the experimental data was fit better to the pseudo-second-order model (R 2 ≥ 0.997) than the pseudo-first-order model (R 2 ≥ 0.992). Moreover, the q e values were obtained for the pseudo-first-order and pseudo-second-order models, and in the case of the pseudo-second-order model, the theoretical value (q e,cal = 229.89 mg/g, 224.22 mg/g, 211.86 mg/g) was very close to the experimental data (q e = 222.3 mg/g, 212.3 mg/g, 198.8 mg/g). Therefore, the pseudo-second-order model was used to describe the adsorption of MB on MSA-AC2 [12,39]. In previous studies [31,40], adsorption capacity can be associated with the surface chemical property of MSA-AC.

Adsorption Isothermal Model
Adsorption isotherms are critical for optimizing the use of adsorbents, as they describe how dye molecules interact with adsorbent particles. Therefore, finding the best fitting isotherm is of great importance. The parameters, obtained by fitting the experimental data to Langmuir (Equation (5)) and Freundlich (Equation (6)) isotherms [31] are listed in Table 3 Here, qe (mg/g) is the amount of MB adsorbed at equilibrium, Ce (mg/L) is the equilibrium concentration of MB solution, and qm (mg/g) is the monolayer adsorption capacity of the adsorbent. KL is the Langmuir adsorption constant, which is related to the free energy of adsorption. KF and n (dimensionless) are the Freundlich adsorption isotherm constants, representing the adsorption extent and the degree of non-linearity between solution concentration and adsorption, respectively.
The regression parameters calculated from the Langmuir and Freundlich models at three different temperatures ( Figure 11) are listed in Table 3. In Figure 12, under the different temperature, the equilibrium adsorption quantity is increased with the increase of the MB solution equilibrium concentration, showing a trend of increasing gradually. The relatively higher R 2 values of Langmuir isotherms, compared with that of Freundlich isotherms, confirm that the Langmuir model (R 2 ≥ 0.996) is a better-fitting isotherm for the experimental data of MSA-AC2. The Langmuir adsorption isotherm equation can better describe the MSA-AC2 adsorption behavior of MB, implying that MB in MSA-AC2 adsorption was monolayer adsorption [31,41].

Adsorption Isothermal Model
Adsorption isotherms are critical for optimizing the use of adsorbents, as they describe how dye molecules interact with adsorbent particles. Therefore, finding the best fitting isotherm is of great importance. The parameters, obtained by fitting the experimental data to Langmuir (Equation (5)) and Freundlich (Equation (6)) isotherms [31] are listed in Table 3.
ln q e = 1 n ln C e + ln K F Here, q e (mg/g) is the amount of MB adsorbed at equilibrium, C e (mg/L) is the equilibrium concentration of MB solution, and q m (mg/g) is the monolayer adsorption capacity of the adsorbent. K L is the Langmuir adsorption constant, which is related to the free energy of adsorption. K F and n (dimensionless) are the Freundlich adsorption isotherm constants, representing the adsorption extent and the degree of non-linearity between solution concentration and adsorption, respectively.
The regression parameters calculated from the Langmuir and Freundlich models at three different temperatures ( Figure 11) are listed in Table 3. In Figure 12, under the different temperature, the equilibrium adsorption quantity is increased with the increase of the MB solution equilibrium concentration, showing a trend of increasing gradually. The relatively higher R 2 values of Langmuir isotherms, compared with that of Freundlich isotherms, confirm that the Langmuir model (R 2 ≥ 0.996) is a better-fitting isotherm for the experimental data of MSA-AC2. The Langmuir adsorption isotherm equation can better describe the MSA-AC2 adsorption behavior of MB, implying that MB in MSA-AC2 adsorption was monolayer adsorption [31,41].

Comparison with Other Methods
When compared with most reported procedures for the determination of MB adsorption, the method described herein is effective for the removal of MB. These results are summarized in Table 4.

Conclusions
In conclusion, magnetic microspheres were synthesized by a simple and environmentally conscious method. The microspheres effectively adsorbed MB dye and were characterized by FT-IR, SEM, VSM, TGA. These characterization techniques have proved that the Fe3O4 of MSA-AC2 did not change through the composite process. Although the saturation magnetization of MSA-AC2 was lower than the MNPs, the magnetization of MSA-AC2 was adequate for fast separation. The results

Comparison with Other Methods
When compared with most reported procedures for the determination of MB adsorption, the method described herein is effective for the removal of MB. These results are summarized in Table 4.

Conclusions
In conclusion, magnetic microspheres were synthesized by a simple and environmentally conscious method. The microspheres effectively adsorbed MB dye and were characterized by FT-IR, SEM, VSM, TGA. These characterization techniques have proved that the Fe3O4 of MSA-AC2 did not change through the composite process. Although the saturation magnetization of MSA-AC2 was

Comparison with Other Methods
When compared with most reported procedures for the determination of MB adsorption, the method described herein is effective for the removal of MB. These results are summarized in Table 4.

Conclusions
In conclusion, magnetic microspheres were synthesized by a simple and environmentally conscious method. The microspheres effectively adsorbed MB dye and were characterized by FT-IR, SEM, VSM, TGA. These characterization techniques have proved that the Fe 3 O 4 of MSA-AC2 did not change through the composite process. Although the saturation magnetization of MSA-AC2 was lower than the MNPs, the magnetization of MSA-AC2 was adequate for fast separation. The results demonstrated that MSA-AC2 has high adsorption efficiency, with a maximum adsorption capacity of 222.3 mg/g for MB. The adsorption efficiency for MB was studied under the following conditions: 150 min, 298 K and optimal pH of 7. The as-prepared MSA-AC2 composite exhibited a high BET-specific surface area, reaching 183.63 m 2 /g. The adsorption isotherm fitted well with the Langmuir model. Kinetic data was described appropriately by the pseudo-second-order model (R 2 ≥ 0.999) and the experimental data was very close to the theoretical value of the pseudo-second-order model. These results reveal that the MSA-AC2 has a potential application in wastewater treatment and in the development of a Fe 3 O 4 -SA-AC composite absorbent that is simple and fast to prepare, cost-effective, and environmentally friendly.