Facile Synthesis of MOFs-Templated Carbon Aerogels with Enhanced Tetracycline Adsorption Performance

: Three-dimensional aerogels have great potential for antibiotic removal from aqueous solution due to their excellent solution mass transfer channels and special morphology. Herein, the metal ions were bound with alginate to form alginate-Fe, alginate-Cu, and alginate-Fe-Cu hydrogels, then they were used as nucleation sites for metal organic framework (MOF) growth to obtain MAlgs gels, respectively. Considering the aqueous environmental stability of MOFs particles, the alginate and MOF particles in MAlgs aerogels were pyrolyzed as templates to obtain the derived carbon aerogel CMAlgs. The results showed that the adsorption capacity of MAlgs-Fe-Cu aerogel was higher than that of MAlg-Cu and MAlg-Fe aerogels, up to ~130 mg · g − 1 . The adsorption performance of carbon aerogel CMAlg-Cu decreased obviously because of the decrease of pore size and oxygen-containing functional groups. The adsorption process is a combination of physical adsorption and chemical adsorption. In addition, CMAlgs aerogels exhibit better recyclability than MAlgs aerogels. This work provides a new strategy for fabricating MOFs-templated in-situ grown carbon aerogels for water puriﬁcation. pores. The speciﬁc surface areas of MAlg-Fe, MAlg-Cu, MAlg-Fe-Cu, CAlg-Fe-Cu are 375.37, 258.33, 685.56, and 329.51 m 2 g − 1 , respectively. It is found that the speciﬁc surface area decreased after carbonization, which may be caused by the decomposition of three-dimensional network skeleton and the condensation of metal-organic ligands. The degree of defects of carbon materials is measured according to the intensity ratio of peak D to peak G ( I D / I G ). The results show that the I D / I G of CMAlg-Fe, CMAlg-Cu, and CMAlg-Fe-Cu aerogels are 0.84, 0.82, and 0.83, respectively. This indicates that iron is more likely to make carbon materials highly disordered and can produce more defects, which is conducive to the exposure of adsorption sites, thereby improving the adsorption performance of aerogels.


Introduction
As a broad-spectrum antibiotic, tetracycline is widely used in human health care and animal feed additives because of its low cost and good inhibition and killing effect on many pathogens [1,2]. Antibiotics enter wastewater treatment plants in various forms as persistent substances due to their low metabolic rate and low biodegradation [3,4]. The presence and concentration enrichment of tetracycline in the aquatic environment can cause the enhancement and spread of tetracycline-resistant bacteria and resistance genes, even posing a potential risk to the ecosystem and human health [5][6][7]. The advanced treatment techniques include adsorption, flocculation, advanced oxidation technology, chemical degradation, and biological treatment [8][9][10][11]. Among them, the adsorption separation method is widely used to remove antibiotic contaminants because of its low cost and easy operation [12,13]. Therefore, developing efficient and inexpensive adsorption materials is the key to practical applications. The antibiotics adsorption materials mainly include carbon materials, clay minerals, resins, metal oxides, and metal-organic frameworks [14][15][16]. However, there are some problems such as low adsorption capacity, difficulty recycling and reusing powder materials, and possible secondary pollution. Research and development of new efficient and inexpensive adsorbent materials is the key to practical applications.
Three-dimensional polymer aerogels have attracted extensive attention in the field of water treatment because of their excellent biodegradability, non-toxicity, easy functionalization and solid-liquid separation properties [17,18]. Sodium alginate is an anionic polysaccharide extracted from seaweed, and it has abundant oxygen-containing functional groups [19][20][21][22][23]. Alginic acid has good gel properties and chelates metal ions (Fe 3+ ,

Preparation of MAlgs and CMAlgs Aerogels
Synthetic routine of aerogels is shown in Scheme 1. Two g of sodium alginate was dissolved in 100 mL of deionized water and mechanically stirred to obtain a homogeneous solution. The uniform solution was dropped into 0.10 mol·L −1 CuCl 2 ·2H 2 O and 0.10 mol·L −1 FeCl 3 ·6H 2 O solution and cross-linked for 10 h to obtain Alg-Cu and Alg-Fe hydrogels, respectively [39,40]. Similarly, the Alg-Fe-Cu hydrogel can be obtained by replacing the crosslinking solution with a mixture of 0.05 mol·L −1 CuCl 2 ·2H 2 O and 0.05 mol·L −1 FeCl 3 ·6H 2 O. The hydrogels were washed three times with deionized water to remove uncrosslinked metal ions. Then, the hydrogels were transferred to ethanol solution of 30 mg mL −1 1,3,5-benzenetricarboxylic acid for 18 h to obtain MAlg-Fe, MAlg-Cu and MAlg -Fe-Cu hydrogels, respectively. All the prepared hydrogels were washed three times with ethanol and deionized water, and then freeze-dried for 24 h to obtain MAlg-Fe, MAlg-Cu and MAlg-Fe-Cu aerogels [41]. The MAlg-Fe, MAlg-Cu and MAlg-Fe-Cu aerogels were pyrolyzed at 500 • C in N 2 atmosphere for 1 h with a heating rate of 5 • min −1 , respectively, to obtain CMAlg-Fe, CMAlg-Cu, and CMAlg-Fe-Cu aerogels.

Batch Adsorption Experiments
Batch experiments were conducted to evaluate the performance of MAlgs CMAlgs aerogels for the adsorption of TC. The isotherm experiments were conducte a thermostatic shaker at 298 K and 150 rpm for 480 min with a solid to liquid ratio of g·L −1 and under varying the initial tetracycline concentrations (20-150 mg·L −1 ). The ki ics experiments were studied in 150 mg·L −1 TC solution with a solid to liquid ratio of mg·mL −1 under varying reaction time (5,15,30,60,90,120,180,240,360, and 480 m The effects of pH were studied in 30 mg·L −1 TC solution with a solid to liquid ratio of mg·mL −1 in a pH range varying from 3 to 11. The effects of solid to liquid ratio were car out varying the MAlgs and CMAlgs aerogels dosage from 0.1 to 2 mg·mL −1 . The rege ation performance of the aerogel for the adsorption of TC was studied in 30 mg·L −1 solution with a solid to liquid ratio of 0.8 mg·mL −1 and using DMF and methanol solu as the resolving solution. The MAlgs and CMAlgs aerogels were separated from the s tion after adsorption and the concentrations of TC were measured at 360 nm using a vis spectrophotometer (UV-6100, Mapada, Shanghai, China). All the experiments w performed in triplicate and the result selected the numerical average of three results.
Langmuir and Freundlich isotherms were used to evaluate the adsorption equ rium. The Langmuir and Freundlich isotherm equation is as follows: where Ce (mg·L −1 ) is the equilibrium TC concentration in the solution, qm (mg g −1 ) is monolayer adsorption capacity and KL (L·mg −1 ) is the Langmuir constant. KF and n Freundlich constants.
Pseudo-first-order and pseudo-second-order to evaluate the adsorption proc which is based on solid phase adsorption. These two models can be expressed by eq tions (3) and (4)

Batch Adsorption Experiments
Batch experiments were conducted to evaluate the performance of MAlgs and CMAlgs aerogels for the adsorption of TC. The isotherm experiments were conducted in a thermostatic shaker at 298 K and 150 rpm for 480 min with a solid to liquid ratio of 0.8 g·L −1 and under varying the initial tetracycline concentrations (20-150 mg·L −1 ). The kinetics experiments were studied in 150 mg·L −1 TC solution with a solid to liquid ratio of 0.8 mg·mL −1 under varying reaction time (5,15,30,60,90,120,180,240,360, and 480 min). The effects of pH were studied in 30 mg·L −1 TC solution with a solid to liquid ratio of 0.8 mg·mL −1 in a pH range varying from 3 to 11. The effects of solid to liquid ratio were carried out varying the MAlgs and CMAlgs aerogels dosage from 0.1 to 2 mg·mL −1 . The regeneration performance of the aerogel for the adsorption of TC was studied in 30 mg·L −1 TC solution with a solid to liquid ratio of 0.8 mg·mL −1 and using DMF and methanol solution as the resolving solution. The MAlgs and CMAlgs aerogels were separated from the solution after adsorption and the concentrations of TC were measured at 360 nm using a UV-vis spectrophotometer (UV-6100, Mapada, Shanghai, China). All the experiments were performed in triplicate and the result selected the numerical average of three results.
Langmuir and Freundlich isotherms were used to evaluate the adsorption equilibrium. The Langmuir and Freundlich isotherm equation is as follows: where C e (mg·L −1 ) is the equilibrium TC concentration in the solution, q m (mg g −1 ) is the monolayer adsorption capacity and K L (L·mg −1 ) is the Langmuir constant. K F and n are Freundlich constants. Pseudo-first-order and pseudo-second-order to evaluate the adsorption process, which is based on solid phase adsorption. These two models can be expressed by Equations (3) and (4), respectively.
where q t (mg·g −1 ) and q e (mg·g −1 ) are the amounts of TC adsorbed at any time and equilibrium, respectively. k 1 (min −1 ) and k 2 (min −1 ) are the rate constants of pseudo first-order and pseudo second-order, respectively.

Morphological Characterization
Sodium alginate is a natural linear polysaccharide obtained from brown algae, which has unique gel properties. The Fe 3+ , Cu 2+ metal ions can independently ion-exchange Na + in sodium alginate and chelate with alginate chain to produce Alg-Fe and Alg-Cu hydrogel with a "egg-box" structure. Alginate chains can also simultaneously chelate Fe 3+ and Cu 2+ alginate chains to produce AlG-Fe-Cu hydrogel. Subsequently, the hydrogel spheres as mentioned above are dispersed in an ethanol solution of organic ligand trimellitic acid to obtain MAlgs (MAlg-Fe, MAlg-Cu, and MAlg-Fe-Cu) hydrogel spheres with uniformly dispersed internal MOFs crystal particles. This is mainly because the metal ions are anchored in the three-dimensional network through the coordination of COO-related to guluronic acid on the alginate chain, which facilitates the further coordination of the anchored metal ions with the organic ligands to form crystal in situ. CMAlgs (CMAlg-Fe, CMAlg-Cu, and CMAlg-Fe-Cu) aerogel with multilayer pore structure was obtained by thermal decomposition based on MAlgs aerogel of in-situ grown MOFs materials as templates.
The microstructure images of MAlgs aerogel and CMAlgs aerogel were obtained by SEM. As shown in Figure 1, MAlg aerogel presents an interconnected three-dimensional network structure and the MOFs particles contained therein exhibit good dispersibility, which further proves that the three-dimensional network structure can effectively limit the growth and aggregation of MOF particles. Different central metal ions in MAlgs gel lead to different morphologies and structures of MAlg-Fe and MAlg-Cu, MAlg-Fe-Cu aerogels. The MAlg-Fe aerogel shows a honeycomb-like 3D network structure with MOFs particles grown in its grid. The MAlg-Cu aerogel is covered with MOFs particles on its flat gel matrix. The MAlg-Fe-Cu aerogel has an uneven surface due to the growth of MOFs particles. The three-dimensional network structure is still maintained after pyrolysis. The polycondensation of the metal-organic framework leads to the formation of micropores between metal particles and the alginate framework. However, it was obviously observed that the porosity of CMAlg-Cu aerogel was lower than that of CMAlg-Cu and CMAlg-Fe-Cu aerogels. The decomposition and collapse of the alginate gel framework and the etching of the metal particles are favorable for the formation of mesoporous structures. The multilayer pore structure is beneficial to the adsorption of pollutants.

FTIR and XRD Analysis
The crystal phase and structure of the sample were analyzed by XRD pattern shown in Figure 2a. The XRD peaks of the synthesized MAlg-Fe aerogel have diffract peaks of certain intensity at 2θ = 10.3° and 20.1°, which are similar to the characteri peaks in the XRD spectrum of MIL-100 (Fe) reported in the literature [42,43]. The bro

FTIR and XRD Analysis
The crystal phase and structure of the sample were analyzed by XRD pattern, as shown in Figure 2a. The XRD peaks of the synthesized MAlg-Fe aerogel have diffraction peaks of certain intensity at 2θ = 10.3 • and 20.1 • , which are similar to the characteristic peaks in the XRD spectrum of MIL-100 (Fe) reported in the literature [42,43]. The broadening of the main diffraction peaks is mainly due to the three-dimensional pores of the gel network restricting crystal growth, resulting in high dispersion and small particle size of MIL-100 (Fe) crystals. The diffraction peaks of MAlg-Cu aerogel are in good agreement with the standard spectrum of HKUST-1, which confirms that HKUST-1 crystals are successfully deposited in situ in MAlg-Cu aerogel [44][45][46]. For the MAlg-Fe-Cu aerogel, the diffraction peaks are broadened, and the degree of crystallinity is poor. CMAlg-Fe aerogel has a diffraction peak of nano-zero-valent iron at 43.1 • , which confirms that metal particles can be reduced to Fe 0 after carbonization with alginate and MOF as template materials.

The BET Surface Areas and Pore Volumes Analysis
The pore structure of MAlg aerogel before and after carbonization was analyzed nitrogen adsorption-desorption test, as shown in the Figure 3a. Obvious hysteresis loo can be observed on the adsorption-desorption curves of MAlgs aerogel and CMAlgs a ogel, which belong to type IV curve, proving that the aerogel contains abundant mesop rous pores. The specific surface areas of MAlg-Fe, MAlg-Cu, MAlg-Fe-Cu, CAlg-Fe-C are 375.37, 258.33, 685.56, and 329.51 m 2 g −1 , respectively. It is found that the specific su face area decreased after carbonization, which may be caused by the decomposition three-dimensional network skeleton and the condensation of metal-organic ligands.
As shown in Figure 3b, the sample single metal MAlgs shows mesoporous size d tribution, and the center is in the range of 4-11 nm with an obvious peak. The pore stru ture of bimetal MAlG-Fe-Cu is concentrated in the range of 10-100 nm. The pore structu of CMAlg-Fe-Cu after carbonization becomes larger, which is consistent with the resu of SEM. The prepared aerogel's mesoporous and three-dimensional macroporous stru ture is conducive to exposing more adsorption sites and the unobstructed pore structu is conducive to reducing the mass transfer resistance of pollutants. The FTIR spectra of the MAlgs aerogel before and after carbonization are shown in Figure 2b. The peaks at 1629, 1451, and 1364 cm −1 in MAlgs aerogel are attributed to the stretching vibration peak of C=O, the flexural vibration peak of the hydroxyl group, and the stretching vibration peak C-O, respectively. For MAlgs aerogels, the peak at 711 cm −1 is the fingerprint peak of MIL-100 (Fe), which is attributed to the Fe 3 O structure, and 742 cm −1 is attributed to the stretching vibration peak of the Cu-O bond coordinated by Cu and BTC. For the increased aromatic structure of CMAlgs aerogel after carbonization, the peak at 2951 cm −1 is attributed to the stretching vibration of C-H, and at 930 cm −1 is attributed to the C-O-C stretching vibration. It is found that carbonization still retains a large number of oxygen-containing functional groups (-CO, -COO, C=O), which can improve the hydrophilicity between the adsorbent surface and the adsorption interface, making the adsorption process smoother.

The BET Surface Areas and Pore Volumes Analysis
The pore structure of MAlg aerogel before and after carbonization was analyzed by nitrogen adsorption-desorption test, as shown in the Figure 3a. Obvious hysteresis loops can be observed on the adsorption-desorption curves of MAlgs aerogel and CMAlgs aerogel, which belong to type IV curve, proving that the aerogel contains abundant mesoporous pores. The specific surface areas of MAlg-Fe, MAlg-Cu, MAlg-Fe-Cu, CAlg-Fe-Cu are 375.37, 258.33, 685.56, and 329.51 m 2 g −1 , respectively. It is found that the specific surface area decreased after carbonization, which may be caused by the decomposition of threedimensional network skeleton and the condensation of metal-organic ligands.
face area decreased after carbonization, which may be caused by the decomposition three-dimensional network skeleton and the condensation of metal-organic ligands.
As shown in Figure 3b, the sample single metal MAlgs shows mesoporous size d tribution, and the center is in the range of 4-11 nm with an obvious peak. The pore stru ture of bimetal MAlG-Fe-Cu is concentrated in the range of 10-100 nm. The pore structu of CMAlg-Fe-Cu after carbonization becomes larger, which is consistent with the resu of SEM. The prepared aerogel's mesoporous and three-dimensional macroporous stru ture is conducive to exposing more adsorption sites and the unobstructed pore structu is conducive to reducing the mass transfer resistance of pollutants.

The Raman and Pore VSM Analysis
The Raman test was performed on the aerogel CMAlg aerogel obtained by pyrolys as shown in Figure 4a. Two resonance peaks were observed at 1350 cm −1 (peak D) a 1580 cm −1 (peak G), which were attributed to graphitized sp 2 carbon and disordered carbon, respectively. The degree of defects of carbon materials is measured according the intensity ratio of peak D to peak G (ID/IG). The results show that the ID/IG of CMA Fe, CMAlg-Cu, and CMAlg-Fe-Cu aerogels are 0.84, 0.82, and 0.83, respectively. This As shown in Figure 3b, the sample single metal MAlgs shows mesoporous size distribution, and the center is in the range of 4-11 nm with an obvious peak. The pore structure of bimetal MAlG-Fe-Cu is concentrated in the range of 10-100 nm. The pore structure of CMAlg-Fe-Cu after carbonization becomes larger, which is consistent with the results of SEM. The prepared aerogel's mesoporous and three-dimensional macroporous structure is conducive to exposing more adsorption sites and the unobstructed pore structure is conducive to reducing the mass transfer resistance of pollutants.

The Raman and Pore VSM Analysis
The Raman test was performed on the aerogel CMAlg aerogel obtained by pyrolysis, as shown in Figure 4a. Two resonance peaks were observed at 1350 cm −1 (peak D) and 1580 cm −1 (peak G), which were attributed to graphitized sp 2 carbon and disordered sp 3 carbon, respectively. The degree of defects of carbon materials is measured according to the intensity ratio of peak D to peak G (I D /I G ). The results show that the I D /I G of CMAlg-Fe, CMAlg-Cu, and CMAlg-Fe-Cu aerogels are 0.84, 0.82, and 0.83, respectively. This indicates that iron is more likely to make carbon materials highly disordered and can produce more defects, which is conducive to the exposure of adsorption sites, thereby improving the adsorption performance of aerogels.
Water 2022, 14, x FOR PEER REVIEW 7 of dicates that iron is more likely to make carbon materials highly disordered and can p duce more defects, which is conducive to the exposure of adsorption sites, thereby i proving the adsorption performance of aerogels. CMAlg aerogel has certain magnetic properties due to the inclusion of Fe 0 and C The saturation magnetic field intensity was tested. As shown in Figure 1, the saturati magnetization of CMALG-Fe and CMALG-Fe-Cu aerogels were 0.02 and 0.04 emu g −1 spectively, showing weak magnetic properties on the CMAlgs aerogel surface.

Adsorption Isotherm Models
The adsorption processes of MAlgs and CMAlgs aerogels were fitted with Langm and Freundlich models, respectively. Both the Langmuir and Freundlich models can CMAlg aerogel has certain magnetic properties due to the inclusion of Fe 0 and Cu 0 . The saturation magnetic field intensity was tested. As shown in Figure 1, the saturation

Adsorption Isotherm Models
The adsorption processes of MAlgs and CMAlgs aerogels were fitted with Langmuir and Freundlich models, respectively. Both the Langmuir and Freundlich models can fit the experimental data well, and the Freundlich model has a better fit (R 2 > 0.99).
The results showed that the uneven surface of aerogel could form adsorption active sites with different energy. The adsorption process of MAlgs and CMAlgs aerogels consists mainly of multilayer physical interaction and monolayer chemical complexation. Figure 5 and Table 1 show that the maximum adsorption capacity of MAlg-Fe, MAlg-Cu, and MAlg-Fe-Cu aerogels are 128.37, 108.23 and 130.72 mg·g −1 , respectively, among which MAlg-Cu-Fe has the highest adsorption capacity. After carbonization of the prepared aerogels, the maximum adsorption amounts of CMAlg-Fe, CMAlg-Cu, and CMAlg-Fe-Cu aerogels are 106.16, 56.66 and 131.06 mg·g −1 , respectively. The adsorption capacity of CMAlg-Fe and CMAlg-Cu decreased significantly, especially for CMAlg-Cu aerogel. The hydroxyl and carboxyl functional groups of alginate in MAlgs aerogels can interact with water through hydrogen bonding and have hydrophilic properties, which facilitate the transport of tetracycline solution and adequate contact with gel adsorption sites in the pore channels of 3D network macropores and mesopores. In addition, the MOF-functionalized MAlgs have a large specific surface area as well as the protonated amino, carboxyl, and hydroxyl groups in the molecular structure of tetracycline can form hydrogen bonds with organic oxygen-containing functional groups on the MAlgs aerogels. CMAlgs aerogel surface has strong aromaticity and few oxygen-containing functional groups. The large specific surface area is still maintained, especially for CMAlg-Fe-Cu. The aromatic structure of CMAlgs can form π-π stacking interactions with the benzene structure of tetracycline. It can also experience a cation-π mechanism with the protonated amino group of tetracycline, which is the main reason for the adsorption of CMAlgs gel. The pores of CMAlg-Cu show inhomogeneity due to carbonization as well as the formation of metal particles leading to the blockage of pore channels and occupying the corresponding active sites. The poor hydrophilicity is not conducive to the mass transfer of tetracycline solution. This means that some internal pores may be ineffective for the adsorption of large tetracyclines. Iron oxides and graphitized carbon mainly dominate CMAlg-Fe-Cu and CMAlg-Fe aerogel aerogels. The literature reports that iron oxides have a potent complexation tetracycline. Hence, their surface adsorption processes include chemical coordination and multilayer physical adsorption processes.
Water 2022, 14, x FOR PEER REVIEW 8 of tetracycline. Hence, their surface adsorption processes include chemical coordination a multilayer physical adsorption processes.

Adsorption Kinetics
A kinetic model was used to fit the data to understand the reaction pathway and the adsorption rate of the aerogels. The adsorption of tetracycline by MAlgs and CMAlgs aerogels increased sharply during the first 30 min of the adsorption process, and then the adsorption process slowed down until it leveled off (Figure 6). At the beginning of the reaction, tetracycline molecules rapidly occupied the abundant active sites on the aerogel surface, and the adsorption amount decreased with time due to the saturation of the active sites as the reaction proceeded. The fitted parameters of the kinetics of tetracycline adsorption by MAlgs and CMAlgs aerogels are shown in Table 2. Both the fitted primary kinetic model and the fitted secondary kinetic model can fit the experimental data well, in which the fitted secondary kinetic model fits better (R 2 > 0.99). Meanwhile, the amount of tetracycline adsorption by aerogels obtained from the fitted secondary kinetic equation is closer to the actual adsorption amount. Among the adsorption processes that control the adsorption rate are chemisorption processes accompanied by physical adsorption. Studies have shown that the faster adsorption rate of CMAlg-Fe-Cu aerogel is due to its ability to provide more mesopore volumes and more adsorption sites.

Effect of Solid-Liquid Ratio
The effect of solid-liquid ratio on the removal of tetracycline by MAlgs and CMAlgs aerogels is shown in Figure 7. The solid-liquid ratio was set to increase from 0.1 g·L −1 to 2 g·L −1 . The removal efficiency of MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels had reached 90% when the addition amount was 0.5 g·L −1 , and then gradually increased and leveled off. However, the adsorption capacity of the MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels showed a decreasing trend. It is attributed to the fact that tetracycline molecules quickly occupied the adsorption site at the MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels surface. Then the adsorption site was gradually saturated, and the system tended to be in equilibrium. The higher removal efficiency is caused by the increase of total surface functional groups and effective contact area. Excessive addition of aerogel leads to the decrease of adsorption capacity because the overlap of active sites reduces the effective contact area of tetracycline and causes waste of adsorbent. 0.8 g·L −1 was selected as the most suitable solid-liquid ratio in consideration of removal efficiency and economy. Table 2. Kinetic parameters of the pseudo-first-order and pseudo-second-order adsorption kinetic models.

Pseudo-First-Order
Pseudo-Second-Order g·L . The removal efficiency of MAlg-Fe-Cu and ~90% when the addition amount was 0.5 g·L −1 , and off. However, the adsorption capacity of the MAl showed a decreasing trend. It is attributed to the fa occupied the adsorption site at the MAlg-Fe-Cu and the adsorption site was gradually saturated, and th The higher removal efficiency is caused by the incre and effective contact area. Excessive addition of ae tion capacity because the overlap of active sites redu cycline and causes waste of adsorbent. 0.8 g·L −1 wa liquid ratio in consideration of removal efficiency a

Effect of pH
It was found that the amount of tetracycline adsorbed by MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels was significantly pH-dependent. Both MAlg-Fe-Cu and CMAlg-Fe-Cu aerogel adsorption were effective in the range of solution initial pH from 3 to 11, indicating that the aerogel could remove tetracycline by adsorption over a wide range of pH. When the initial solution pH = 3, the removal rate of tetracycline by MAlg-Fe-Cu and CMAlg-Fe-Cu reaches 85.8% and 89.3%, and the removal effect decreases slightly when the pH is 11. The existing form of antibiotics in solution will change with the change of pH. There are three equilibrium constants of tetracycline in aqueous solution: pKa1 = 3.30, pK a 2 = 7.68, pK a 3 = 9.68. Therefore, it can be dissociated into four different forms at different pH: cationic form (TC + ), amphoteric form (TC 0 ), anionic form (TC − ), and the double anion form (TC 2− ). The zeta potentials of MAlg-Fe-Cu and CMAlg-Fe-Cu were further tested under different pH conditions (Figure 8b). TC completely loses electrons and assumes a cationic form (TC + ) at lower pH, at this time, the MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels showed electronegativity, which was favorable for electrostatic adsorption. The adsorption effect of MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels on tetracycline gradually increases with the increase of pH, which was attributed to the enhanced electronegativity of MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels. When pH value increases to neutral, TC molecules gradually exist in amphoteric TC 0 and the adsorption process lacks electrostatic adsorption. As the pH continues to increase, the presence of negatively charged forms such as TC − molecule TC 2− , however, the negative charge of MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels reached a maximum electrostatic repulsion, leading to the lowest adsorption. At this time, the adsorption process of aerogels mainly relies on pore filling and π-π interaction between aromatic structures. ent pH: cationic form (TC ), amphoteric form (TC ), anionic form (TC ), and the dou anion form (TC 2− ). The zeta potentials of MAlg-Fe-Cu and CMAlg-Fe-Cu were furth tested under different pH conditions (Figure 8b). TC completely loses electrons and sumes a cationic form (TC + ) at lower pH, at this time, the MAlg-Fe-Cu and CMAlg-Feaerogels showed electronegativity, which was favorable for electrostatic adsorption. T adsorption effect of MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels on tetracycline gradually creases with the increase of pH, which was attributed to the enhanced electronegativ of MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels. When pH value increases to neutral, TC m ecules gradually exist in amphoteric TC 0 and the adsorption process lacks electrosta adsorption. As the pH continues to increase, the presence of negatively charged for such as TC − molecule TC 2− , however, the negative charge of MAlg-Fe-Cu and CMAlg-Cu aerogels reached a maximum electrostatic repulsion, leading to the lowest adsorpti At this time, the adsorption process of aerogels mainly relies on pore filling and π-π teraction between aromatic structures.

Regenerability
Reusability is one of the essential criteria to evaluate the performance of adsorb materials. The regeneration performance of the aerogel for the adsorption of tetracycl was studied using DMF and methanol solution as the resolving solution. The expe mental results are shown in Figure 9. The equilibrium adsorption amounts of tetracycl adsorbed by MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels are lost about 22% and 8% after regeneration cycles by resolution, respectively. The main reason is that the adsorption pacity of the MAlg-Fe-Cu aerogel is reduced because the binding sites of the MOF ba bone in the MAlg-Fe-Cu aerogel are destroyed during the desorption and recycling p cess. However, CMAlg-Fe-Cu aerogel has excellent stability and good regeneration p formance, which is a selective adsorption material with good application prospects.

Regenerability
Reusability is one of the essential criteria to evaluate the performance of adsorbent materials. The regeneration performance of the aerogel for the adsorption of tetracycline was studied using DMF and methanol solution as the resolving solution. The experimental results are shown in Figure 9. The equilibrium adsorption amounts of tetracycline adsorbed by MAlg-Fe-Cu and CMAlg-Fe-Cu aerogels are lost about 22% and 8% after six regeneration cycles by resolution, respectively. The main reason is that the adsorption capacity of the MAlg-Fe-Cu aerogel is reduced because the binding sites of the MOF backbone in the MAlg-Fe-Cu aerogel are destroyed during the desorption and recycling process. However, CMAlg-Fe-Cu aerogel has excellent stability and good regeneration performance, which is a selective adsorption material with good application prospects.

Conclusions
In summary, a series of functionalized MAlgs and CMAlgs aerogels were

Conclusions
In summary, a series of functionalized MAlgs and CMAlgs aerogels were synthesized by simple in-situ growth and pyrolysis to solve environmental problems. The threedimensional network of MAlgs aerogel can grow MOFs particles well and effectively prevent aggregation, presenting a mesoporous structure. CMAlg-Cu aerogels have ineffective tetracycline adsorption due to the smaller shrinkage pore size after carbonization. In addition, CMAlgs aerogels exhibit weak magnetic properties. The maximum adsorption capacity of MAlgs and CMAlgs aerogels for tetracycline is~130 mg·g −1 , respectively. The results of adsorption kinetics and adsorption isotherms indicate that adsorption process can be combined with physical adsorption and chemical adsorption and that the surface of the adsorbent is uneven. The adsorption mechanism shows that the adsorption process is dominated by π-π interaction and pore filling effect. The electrostatic adsorption enhances the adsorption process of aerogel because aerogel is negatively charged under acidic pH. In addition, CMAlgs aerogel exhibits better recyclability than MAlgs aerogel. This study is expected to provide a feasible strategy for removing tetracycline antibiotics and broaden the application range of carbon aerogels as adsorbents.
Author Contributions: Conceptualization, methodology, validation, formal analysis, investigation, data curation, writing-original draft preparation, Y.K. and Y.Z.; writing-review and editing, visualization, K.H.; supervision, project administration, funding acquisition, B.S. All authors have read and agreed to the published version of the manuscript.
Funding: This research was funded by the National Natural Science Foundation of China, grant number 51808538.