Preparation of Magnetic Surface Ion-Imprinted Polymer Based on Functionalized Fe3O4 for Fast and Selective Adsorption of Cobalt Ions from Water

A novel cobalt ion-imprinted polymer (Co(II)-MIIP) based on magnetic Fe3O4 nanoparticles was prepared by using Co(II) as the template ion, and bis(2-methacryloxyethyl) phosphate and glycylglycine as dual functional monomers. The fabricated material was analyzed by Fourier transform infrared spectroscopy, thermogravimetric analysis, field emission scanning electron microscopy, energy dispersive X-ray spectroscopy, Brunauer–Emmett–Teller, X-ray diffraction, and vibrating sample magnetometer. The adsorption experiments with Co(II)-MIIP, found that the maximum adsorption capacity could reach 33.4 mg·g−1, while that of the non-imprinted polymer (Co(II)-NIP) was found to reach 15.7 mg·g−1. The adsorption equilibriums of Co(II)-MIIP and Co(II)-NIP was established within 20 min and 30 min, respectively. The adsorption process could be suitably described by the Langmuir isotherm model and the pseudo-second-order kinetics model. In binary mixtures of Co(II)/Fe(II), Co(II)/Cu(II), Co(II)/Mg(II), Co(II)/Zn(II), and Co(II)/Ni(II), the relative selectivity coefficients of Co(II)-MIIP toward Co(II)-NIP were 5.25, 4.05, 6.06, 11.81, and 4.48, respectively. The regeneration experiments indicated that through six adsorption–desorption cycles, the adsorption capacity of Co(II)-MIIP remained nearly 90%.


Introduction
Cobalt (Co) has excellent hardness, thermal fatigue resistance, and magnetic property, leading to the wide use of Co and Co compounds in various industrial fields, such as mining, metallurgy, electroplating, paint, and electronics [1]. As a result, the discharge of Co contained wastewater from industrial activities causes severe environmental pollution, as well as health threats to human beings [2,3]. The Co content in an adult's body is generally about 1.1 mg. A small amount of Co can cause anemia, while an excessive amount of Co can cause poisoning [4].
Until now, the treatment of wastewater containing Co has raised substantial concern, and researchers continue to explore ways to efficiently remove Co in industrial wastewater, such as biological treatment [5], chemical precipitation [6], electrochemical methods [7], membrane separation [8], and adsorption. Among these methods, adsorption is thought to be an economical and effective method for removing Co(II) ions from aqueous solutions among used methods. Vivas et al. [9] investigated the performance of dicalcium phosphate dihydrate as an adsorbent in treating Co waste liquid, but the recycling efficiency was found to be low. Tawfik et al. [10] synthesized a new hydrophobic cross-linked polyzwitterionic acid, which displayed a superior capability to adsorb Co(II) ions and assisted with the adsorption of organic pollutants. Mostafa et al. [11] prepared a magnetic chitosan using 8-hydroxyquinoline to remove Co(II) ions from aqueous solutions. Regretfully, these adsorbents have several shortcomings in practical applications, such as insufficient recycling performance, poor selectivity, and long acting time. Thus, synthesizing new adsorbents for quick and selective removal of Co from wastewater is urgently needed.
Ion-imprinted polymers (IIPs) are designed based on molecularly imprinted technique [12]. Metal ions can be imprinted as template ions for complexation to polymerizable ligands [13]. After removing the template ions, the resulting polymers can possess a strong affinity to template ions, and the polymer memory effect of IIPs enables specific ligands to selectively recognize target ions. So far, various metal ion-imprinted polymers have been reported. Angkana et al. [14] used the suspension polymerization to prepare copper-imprinted polymers. Huang et al. [15] studied Cr(VI) ion-imprinted polymer on graphene oxide-mesoporous silica nanosheets. Zhang et al. [16] synthesized Mo(VI)imprinted chitosan/triethanolamine gel beads by using ion-imprinted technology. Lee et al. [17] synthesized a magnetic Co(II)-imprinted polymer based on mesoporous silica for the selective removal of Co(II) ions. To realize the fast adsorption of target ions, surface ion imprinted polymers were prepared using silica, chitosan, and Fe 3 O 4, etc., as carriers to support the ion imprinted layer. In comparison, Fe 3 O 4 nanoparticles (NPs) have shown superior properties to other carriers, such as stable physical properties, higher surface area, and excellent magnetic properties, which can be used as an ideal carrier for IIPs.
In this study, a novel Co(II)-imprinted polymer was prepared using magnetic Fe 3 O 4 NPs modified with tetraethyl orthosilicate and methacryloxy propyl trimethoxyl silane as the support. The easy separability was one of the advantages of magnetic materials for waste water treatment, and the magnetic materials had a unique role of rapid separation and recovering by applying an external magnetic field [18]. Bis(2-methacryloxyethyl) phosphate (B-2MP) and glycylglycine (GG) were used as dual monomers. The joint action of dual monomers endows the resultant ion imprinted adsorbents with higher selectivity and adsorption rate towards target ions, due to the strong affinity between multiple functional groups and target ions [19]. The final product was characterized, and the adsorption properties were investigated as well.

Synthesis of Fe 3 O 4 NPs
Uniform Fe 3 O 4 magnetic NPs were synthesized by a chemical co-precipitation method based on our previous work [20]. First, 2.12 g of FeCl 2 ·4H 2 O and 4.86 g of FeCl 3 ·6H 2 O were dissolved in 110 mL of deionized water saturated with nitrogen gas (N 2 ), then the mixture was heated up to 80 • C under N 2 atmosphere in a four-necked flask. After 10 mL of ammonia aqueous solution (25%, w/w) was added dropwise under vigorous mechanical stirring, the brown solution gradually turned black. The mixed solution was stirred vigorously for 30 min under N 2 atmosphere until black Fe 3 O 4 NPs were obtained. The synthesized Fe 3 O 4 NPs were rinsed with deionized water and dried in vacuum at 45 • C for 8 h.

Surface Silanization of Fe 3 O 4 NPs
Fe 3 O 4 NPs (1.0 g) were dispersed in 120 mL of absolute ethanol, then 20 mL of deionized water and ammonia aqueous solution (25%, w/w) were added [21]. Hereafter, 2 mL of TEOS was added dropwise to the mixed solution and kept stirring for 12 h at room temperature. After the reaction, the silanized Fe 3 O 4 NPs (Fe 3 O 4 @SiO 2 ) were separated under an external magnet, rinsed with deionized water, and dried in vacuum at 40 • C for 8 h.

Functionalization of Fe 3 O 4 @SiO 2
The prepared Fe 3 O 4 @SiO 2 NPs (0.5 g) were dispersed into 80 mL of ethanol aqueous solution (15%, v/v) under sonication to form a suspension. Next, 2 mL of MPS was added dropwise under mechanical stirring [22]. The reaction lasted 12 h at 40 • C. After the reaction, the functionalized Fe 3 O 4 @SiO 2 (Fe 3 O 4 @SiO 2 @MPS) were rinsed with absolute ethanol and deionized water. Finally, the product was dried in vacuum at 60 • C for 8 h. Later, the Co(II)-MIIP containing template ions were rinsed with ethanol and deionized water. Co(II) ions were eluted from ion-imprinted polymers with 0.05 mol·L −1 NaOH for 120 min until Co(II) ions were not discovered in the elution solution. After the elution, the Co(II)-MIIP was rinsed repeatedly with deionized water, and the washed imprinting material was dried in vacuum at 60 • C for 12 h. By contrast, the same synthesis method was used to obtain magnetic non-imprinted polymers (MNIP), except that Co(II) ions were not added in the synthesis process. The preparation process of Co(II)-MIIP is shown in Figure 1.

Characterizations
The functional groups of prepared materials were analyzed by Fourier transform infrared spectroscopy (FT-IR, Nicolet 6700, Thermo Fisher, MA, USA). Scanning electron microscopy (SEM, Thermo Fisher, MA, USA), and energy dispersive spectroscopy (EDS) were used to analyze the surface morphology of the materials and the types of elements. Thermogravimetric analysis (TGA) was used to analyze the thermal stability (Perkin Elmer TGA 400, New Castle, DE, USA). The Brunauer-Emmett-Teller (BET) equation was used to determine the surface area and pore sizes (V-Sorb 2800 Series Analyzer, Gold APP Instrument, Beijing, China). The vibrating sample magnetometer (VSM, VersaLab, CA, USA) was used to analyze the magnetic property. XRD patterns were determined by using the X-ray diffractometer (XRD, SmartLab, TKY, Japan) from 10 • to 90 • .

Adsorption Experiments
The simulated Co(II) ions solution was used in the adsorption experiment. The prepared adsorbents (10 mg) were added into 10 mL of Co(II) ions solution, which was then shaken at 25 • C. Over a certain period, the adsorbent was separated and recovered by the magnet, and the solution was filtered with the filter head (0.45 µm). Then, the residual Co(II) ions were determined by inductively coupled plasma-optical emission spectrometer (ICP-OES, iCAP 6300, Thermo Fisher, USA). The adsorption capacity q e (mg·g −1 ) could be computed using Equation (1): where c i (mg·L −1 ) is the initial concentrations of Co(II) ions, and c e (mg·L −1 ) is the equilibrium concentrations; V (L) is the volume of the liquid; m (g) is the mass of adsorbents.
The influence of solution pH on the adsorption capacity of adsorbents were investigated by using simulated Co(II) ions solution with pH values ranging from 3.0 to 8.5. The adsorption capacity of the adsorbents was calculated based on the variations of Co(II) concentration at intervals, and the resultant adsorption curves were fitted by using pseudofirst-order and pseudo-second-order models, respectively. The equilibrium adsorption isotherms were carried out with the original concentration ranges from 20-500 mg·L −1 , and Langmuir isotherm equation and Freundlich isotherm equation were used to fit the equilibrium adsorption experimental data, respectively.

Adsorption Selectivity
To research the adsorption selectivity, Cu(II), Zn(II), Ni(II), Mg(II), and Fe(II) were also added into the solution of Co(II) ions. Each concentration was 100 mg·L −1 in binary mixtures. In 10 mL of different dual-system solutions, the amount of adsorbent (Co(II)-MIIP or Co(II)-NIP) was 1.0 g·L −1 . After the adsorption experiment, all concentration of Co(II) ions and competing ions were determined by ICP-OES. The distribution coefficient (K d , L·g −1 ) and selectivity coefficient (K) were calculated by using Equations (2) and (3) [23]. The relative selectivity coefficient (K ) was calculated using Equation (4) [24]:

B-2MP and GG Dosage
The effect of the addition amount of B-2MP and GG on the adsorption performance is shown in Figure 2. When monomers were not added in the synthesis process, the adsorption capacity of Co(II)-MIIP was only 2.3 mg·g −1 . When only B-2MP or GG was added in the synthesis process, that of Co(II)-MIIP was 18.1 mg·g −1 and 10.3 mg·g −1 , respectively; this was due to the Schiff base nitrogen and carboxyl oxygen having good complexing ability [25]. It showed that the monomer had a significant effect on the adsorption performance, and the complexation between B-2MP and template ion was stronger than that of GG. The highest adsorption capacity was obtained when B-2MP: GG was 4:1, indicating that the presence of GG could enhance the complexation between B-2MP and the template ion. This may be due to more chelates. Therefore, the best ratio of monomer B-2MP and GG was 4:1.

The Amount of EGDMA
The effect of EGDMA usage on the adsorption performance is illustrated in Figure 3. When the addition amount of EGDMA was in a range of 2-12 mmol, the adsorption capacity of Co(II)-MIIP increased rapidly as the increase of the addition amount of EGDMA. The monomer-ion prepolymerized unit was fully cross-linked due to sufficient EGDMA, resulting in abundant specific imprinting sites on the surface of the imprinting material. However, when EGDMA was over-dosed, there was a decrease in the saturated adsorption capacity. The cross-linking agent made an important impact to the preparation process of IIPs. The excessive cross-linking agent would self-polymerize on the surface of the adsorbent, which not only caused the specific surface area of the imprinted material decrease, but also made it difficult to elute the template ions [26]. Therefore, the optimal addition amount of the crosslinking agent EGDMA was 12 mmol.

FT-IR
The absorption peaks of Fe 3 O 4 NPs, Fe 3 O 4 @SiO 2 , Fe 3 O 4 @SiO 2 @MPS, and Co(II)-MIIP were analyzed by FT-IR in the wavenumber range of 500-4000 cm −1 , as shown in Figure 4. In curve (a), the peak at 596 cm −1 was due to the asymmetric vibration of Fe-O, and the peak at 3438.5 cm −1 was due to the hydroxyl groups of Fe 3 O 4 NPs or the residual water in the sample [3,27]. The existence of these characteristic peaks proves the successful preparation of Fe 3 O 4 NPs [28]. In curve (b), the peaks at 796 cm −1 and 942 cm −1 were attributed to Si-O stretching vibration, and the stretching vibration of Si-O-Si caused the peak at 1013 cm −1 . The absorption peak indicated that Fe 3 O 4 NPs were successfully modified by TEOS [29]. In curve (c), the peak located at 1434 cm −1 was the characteristic peak of C=C, and the peak at 1621 cm −1 was ascribed to the C=O bond. The peaks at 2951 cm −1 and 3055 cm −1 were the characteristic peaks of -CH 2 and -CH 3 , respectively. These absorption peaks were all derived from the silane coupling agent MPS [30]. In curve (d), the N-H tensile vibration from the monomer GG caused the absorption peak at 764 cm −1 , and the C=N stretching vibration caused the peak located at 1728 cm −1 . Moreover, the -NH 2 asymmetric vibration caused the absorption peak at 3421 cm −1 [25]. Furthermore, the absorption peaks at 1158 cm −1 and 1260 cm −1 were attributed to the P=O of monomer B-2MP [31]. The existence of the above characteristic peaks proved the successful preparation of Co(II)-MIIP.

TGA
The thermal stability of Fe 3 O 4 NPs, Fe 3 O 4 @SiO 2 @MPS, and Co(II)-MIIP was judged by the thermogravimetric analyzer, and the outcomes are shown in Figure 5.

SEM and EDS
The surface morphology and microstructure of Fe 3 O 4 @SiO 2 @MPS and CO(II)-MIIP were analyzed by SEM. The specific analysis are exhibited in Figure 6. The SEM image of Fe 3 O 4 @SiO 2 @MPS (Figure 6a) shows that the particles were spherical with uniform particle size. According to the SEM image of Co(II)-MIIP (Figure 6b), the organic imprinted layer caused the surface of Co(II)-MIIP to be porous and rough. Furthermore, the Co(II)-MIIP particles were interconnected owing to agglomeration. Figure 6c,d shows the EDS characterization diagrams of Fe 3 O 4 @SiO 2 @MPS and Co(II)-MIIP, respectively. Figure 6c mainly contains elements such as C, O, Fe, and Si. The presence of Fe indicated that the preparation of Fe 3 O 4 NPs was successful, while the presence of Si and C was attributed to the modification and functionalization process of Fe 3 O 4 NPs. Compared with the EDS of Fe 3 O 4 @SiO 2 @MPS, the N and P elements are shown in the diagram of Co(II)-MIIP, indicating that GG and B-2MP were involved in the polymerization process. The above elements proved that the polymer was successfully prepared.

BET
The N 2 adsorption-desorption isotherms and pore size distribution curves of Fe 3 O 4 @SiO 2 @MPS and Co(II)-MIIP are exhibited in Figure 7. The N 2 adsorption capacity of Fe 3 O 4 @SiO 2 @MPS and Co(II)-MIIP increased slowly in the low pressure region (P/P 0 < 0.5), and sharply increased in the high pressure region (0.8 < P/P 0 < 1.0), indicating that the N 2 isotherm of two materials belonged to category IV isotherm. There were abundant mesoporous structures on the surface of the materials [32]. In addition, it could be found from the figure that the N 2 adsorption capacity of Fe 3 O 4 @SiO 2 @MPS was significantly greater than that of Co(II)-MIIP. The Barrett-Joyner-Halenda method was used to determine the pore size, pore volume, and specific surface area of Fe 3 O 4 @SiO 2 @MPS and Co(II)-MIIP [33]. The relevant results were shown in Table 1. The pore volume decreased from 0.4028 cm 3 ·g −1 for Fe 3 O 4 @SiO 2 @MPS to 0.2375 cm 3 ·g −1 for Co(II)-MIIP, and the specific surface area also decreased from 126.82 m 2 ·g −1 to 74.94 m 2 ·g −1 , which was attributed to the formed organic imprinting area [34]. However, the average pore diameter of Co(II)-MIIP (9.31 nm) was still in the mesoporous range (2 nm < d < 50 nm), indicating that it was a mesoporous material and suitable for ion adsorption [35]. Its pore structure increased the surface area and provided more adsorption sites. The rough and easily modifiable surface of nanoparticles was conducive to capturing Co(II) ions [36].

VSM
The magnetic properties of Fe 3 O 4 @SiO 2 @MPS and Co(II)-MIIP are illustrated in Figure 8. The hysteresis loops indicated that Fe 3 O 4 @SiO 2 @MPS and Co(II)-MIIP were both superparamagnetic [37]. In addition, the results showed that the magnetic saturation intensity of Fe 3 O 4 @SiO 2 @MPS was 36.1 emu/g, while that of Co(II)-MIIP was only 9.5 emu/g. Since the imprinted polymer layer loaded on the surface, the magnetic saturation intensity of Co(II)-MIIP was weakened. However, it is shown that Co(II)-MIIP in the solution could still be separated quickly under the action of an external magnetic field from the insert images in Figure 8.

XRD
The XRD patterns of Fe 3 O 4 , Fe 3 O 4 @SiO 2 @MPS and Co(II)-MIIP were shown in Figure 9. For Fe 3 O 4 NPs, the diffraction peaks matched well with that reported in the JCPDS-International Centre, which proved that the prepared Fe 3 O 4 NPs had a good crystal structure [20]. After surface silanization, Fe 3 O 4 @SiO 2 @MPS showed no significant difference with Fe 3 O 4 NPs regarding both diffraction peaks and peak intensities. The characteristic diffraction peaks of Co(II)-MIIP were nearly unchanged, but the peak intensities obviously decreased. This can be explained by Fe 3 O 4 NPs being encapsulated in Co(II)-MIIP, and the functional ion imprinted layer resulted in the attenuation of diffraction peaks [38]. However, the crystal structure of nanoparticles remained intact after surface functionalization [20].

Effect of Solution pH
Solution pH has a decisive effect on the existence of ions and the degree of protonation of the adsorbent and has an important position in the process of ion enrichment by the adsorbent. As shown in Figure 10a [25], Co(II) has four existing forms, namely Co 2+ , Co(OH) + , Co(OH) 2 , and Co(OH) 3 -, in the pH range of 4.0 to 13.0. When pH < 8.0, the main existing form of Co(II) is Co 2+ . Figure 10b showed the adsorption capacity of Co(II)-MIIP and Co(II)-NIP in the pH range of 3.0 to 8.5. Under acidic or neutral conditions (pH ≤ 7.0), Co(II)-MIIP and Co(II)-NIP both exhibited poor adsorption capacity to Co(II) ions. Because the electrostatic repulsion between the protonated functional groups and the positivelycharged Co(II) ions weakened the coordination interaction between the imprinted sites and Co(II) ions, resulting in the lower adsorption capacity [11]. When the pH of the solution was between 7.0 and 8.0, the adsorption capacity of both adsorbents increased with the increase of solution pH. At this time, the protonation of the functional groups on Co(II)-MIIP decreased, and the unprotonated functional groups could coordinate with Co(II) ions. Meanwhile, the electrostatic attraction between functional groups and Co(II) ions also contributed to the increase of adsorption capacity [39]. In addition, due to the imprinting effect of template ions, the adsorption capacity of Co(II)-MIIP for Co(II) ions was much higher than that of Co(II)-NIP. When the solution pH exceeded 8.0, high concentrations of Co(II) ions were easily precipitated [39]. Therefore, pH = 8 was the optimum pH value for subsequent adsorption experiments, which is consistent with previous studies [9,25].

Adsorption Kinetics
The kinetics of the adsorption process can provide relevant information about solute adsorption rate and adsorption model. The adsorption capacity of Co(II)-MIIP and Co (II)-NIP to Co(II) ions varied with adsorption duration, as shown in Figure 11a. Within the first five minutes, the adsorption capacity of Co(II)-MIIP increased rapidly, and nearly 85% of the total adsorption capacity occurred in this stage. After 20 min, adsorption equilibrium was achieved. For comparison, the adsorption rate of Co(II)-NIP was relatively uniform and slow. The adsorption equilibrium was reached after 30 min, which was longer than that of Co(II)-MIIP. Due to the lack of Co(II) ions template effect in Co(II)-NIP, the surface adsorption sites were less than that of Co(II)-MIIP, and the specific recognition between adsorbent and Co(II) ions was lacking. By comprehensive comparison, it could be seen that Co(II)-MIIP had the advantage of faster adsorption than Co(II)-NIP.
where k 1 (min −1 ) and k 2 (g·mg −1 ·min −1 ) are the pseudo-first-order and pseudo-secondorder kinetic rate constants, respectively; q t (mg·g −1 ) and q e (mg·g −1 ) are the adsorption amount of Co(II) ions at time t and equilibrium, respectively. The kinetics models for the adsorption of Co(II) ions onto Co(II)-MIIP and Co(II)-NIP are shown in Figure 11b, and the relevant kinetics fitting parameters are listed in Table 2. Comparing R 2 of the pseudo-first-order and the pseudo-second-order fittings, it can be seen that the pseudo-second-order kinetics is more suitable to describe the adsorption process of Co(II) ions, which indicated that adsorption proceeded via chemical adsorption [42]. At the same time, it could be seen that the fitting degree of Co(II)-MIIP was closer to the experiment, which proved that Co(II)-MIIP had better performance than Co(II)-NIP.

Adsorption Isotherm
The equilibrium adsorption isotherms were carried out with the original concentration ranges from 20-500 mg·L −1 , as shown in Figure 12. Adsorption capacity of Co(II)-MIIP and Co(II)-NIP increased rapidly with initial concentration of Co(II) ions increased from 20 to 100 mg·L −1 . The adsorption capacity increased gradually from 100 to 300 mg·L −1 and reached saturation when the concentration increased to 300 mg·L −1 . At this time, the active imprinted sites that can bind to Co(II) ions on the imprinted materials were all occupied [43], and the saturated adsorption capacities were 33.4 mg·g −1 and 15.7 mg·g −1 , respectively. The adsorption capacity of Co(II)-MIIP was far greater than that of Co(II)-NIP because several imprinted sites were emerged in the surface ion imprinting process.
ln q e = ln K F + 1 n ln C e (8) where C e (mg·L −1 ) is the Co(II) ion concentration in solution at adsorption equilibrium; q e (mg·g −1 ) is the adsorption capacity of Co(II) ions by adsorbents at adsorption equilibrium; q m (mg·g −1 ) is the theoretical maximum adsorption capacity; K L (L·mg −1 ) is the Langmuir isotherm model constant; K F (mg·g −1 ) is the Freundlich isotherm model constant; and n represents the Freundlich isotherm model binding constant. The fitting curves are shown in Figure 13a,b, and the relevant fitting parameters are listed in Table 3. According to the data, the correlation coefficients (R 2 ) of the Langmuir model for Co(II)-MIIP and Co(II)-NIP were 0.995 and 0.997, respectively, while the R 2 of the Freundlich isotherm model were 0.839 and 0.865, respectively. It can be concluded that Langmuir isotherm model is more suitable to describe the adsorption process of Co(II)-MIIP and Co(II)-NIP, demonstrating that the adsorption of Co(II) ions by Co(II)-MIIP and Co(II)-NIP is a monolayer chemical adsorption, which is consistent with the conclusion of adsorption kinetics [46]. In addition, the theoretical maximum adsorption capacity of Co(II)-MIIP and Co(II)-NIP calculated by the Langmuir isotherm equation were 37.81 mg·g −1 and 17.54 mg·g −1 , respectively, which were closer to the experimental maximum adsorption capacities (33.43 mg·g −1 and 15.71 mg·g −1 ). It also suggested that that Langmuir isotherm model was more suitable to describe the adsorption process of Co(II)-MIIP and Co(II)-NIP.

Adsorption Selectivity
Binary competitive system In this experiment, Cu(II), Zn(II), Ni(II), Mg(II), and Fe(II) ions, which possessed the same valence state and similar ion radius as Co(II) ions, were selected as competitive ions to explore the adsorption selectivity of Co(II)-MIIP and Co(II)-NIP. The adsorption capacities of Co(II)-MIIP and Co(II)-NIP for Co(II) ions and various competitive ions are illustrated in Table 4. The distribution coefficient (K d , L·g −1 ), selection coefficient (K), and relative selectivity coefficient (K ) calculated by Equations (2)-(4) are listed in Table 4. Co(II)-MIIP had adsorption effect on all ions in the solution, indicating that Co(II)-MIIP had an enrichment effect on template ions and ions with similar structure, but the adsorption capacity of competitive ions was significantly lower than that of Co(II) ions, indicating that Co(II)-MIIP had strong selective recognition on template ions [27]. In contrast, the adsorption capacity of Co(II)-NIP for competitive ions was not significantly different from that of Co(II) ions, because the lack of template ions led to fewer adsorption sites and irregular three-dimensional structure in the preparation of Co(II)-NIP. In addition, in the presence of different competitive ions, the K parameter was greater than 1, which also showed that the selective recognition of Co(II)-MIIP was better than Co(II)-NIP [27,40].

Multicomponent competitive system
There are many kinds of ions in industrial wastewater, so it is necessary to investigate the adsorption selectivity of Co(II)-MIIP and Co(II)-NIP for Co(II) in a multicomponent competitive system, which may contain Co(II), Cu(II), Zn(II), Ni(II), Mg(II), and Fe(II) ions in the solution. The competitive ions used in binary competitive system were also selected to simulate a multicomponent competitive system and investigate the adsorption selectivity of prepared adsorbents, with concentration of 100 mg·L −1 each. As shown in Figure 14, compared with the binary competitive system, both the adsorption capacity of Co(II)-MIIP and Co(II)-NIP for Co(II) ions reduced. However, the adsorption capacity of Co(II)-MIIP for Co(II) ions was still at least three times that of competitive ions, and there was still no significant difference in the adsorption capacity of Co(II)-NIP for Co(II) ions and competitive ions because of the poor selectivity of Co(II)-NIP. The results showed that Co(II)-MIIP exhibited good adsorption selectivity for template ions even in the presence of various competitive ions.

Reusability
Reusability of adsorbents is one of the important means to save treatment costs. In addition to excellent selectivity, better recycling performance is another advantage of imprinted materials. Six adsorption-desorption cycles were performed to study the reusability of magnetic Co(II)-MIIP, and 0.05 mol·L −1 NaOH solution was used as the eluent. As given in Figure 15, the adsorption capacity of Co(II)-MIIP decreased from 26.30 mg·g −1 to 23.40 mg·g −1 after six adsorption-desorption cycles, retaining 89% of its initial adsorption capability. Experimental results demonstrate that there was no serious damage to the imprinting recognition sites of the adsorbent after repeated adsorption and elution [47]. Therefore, the prepared Co(II)-MIIP has excellent stability and reusability. The comparison of Co(II)-MIIP with other adsorbents reported was listed in Table 5.  We have compared the adsorbent with previously reported adsorbents regarding adsorption capacity, time, reusability, and adsorption selectivity, and the results are listed in Table 5. It can be concluded from the table that the equilibrium time and the reused cycles of the prepared Co(II)-MIIP were better or comparable in respect to other reports. Meanwhile, it showed excellent selectivity.

Conclusions
A novel ion-imprinted polymer Co(II)-MIIP with magnetic property was synthesized for the rapidly and efficiently selective separation of Co(II) from aqueous solution. Through the analysis of various characterizations about its morphology and structure, Co(II)-MIIP was a kind of mesoporous adsorbent with high stability that can be used for ion adsorption. It achieved better filtration and recovery by applying an external magnetic field. The combination of dual monomers (B-2MP and GG with molar ratio of 4:1) and surface ion imprinting technology then gives it a better selectivity. In the binary competition system and the multiple competition system, it showed that Co(II)-MIIP had good adsorption selectivity and strong anti-interference ability. At the same time, it also had a stable reusability; the adsorption capacity dropped only 11% after six consecutive adsorptionelution cycles so as to realize the fast and efficient adsorption of Co(II) from the aqueous solution containing various ions.

Conflicts of Interest:
The authors declare no conflict of interest.