Surface decoration of bis-aminosilane cross-linked multiwall carbon nanotube ultrafiltration membrane for fast and efficient heavy metal removal

Heavy metals (HMs) are highly toxic water pollutants abundant in industrial wastewater. Herein, a bis[3-(trimethoxysilyl)propyl]amine (BTMSPA) cross-linked multiwalled carbon nanotube (MWCNT) nanomaterial (CQACNT) was synthesized by silanization of MWCNT-OH followed by grafting of positively charged quaternary ammonium groups (glycidyl trimethyl ammonium chloride (GTMAC)) by an epoxide ring-opening reaction. The composite membranes were prepared by the incorporation of CQACNT into the poly(ether sulfone) (PES) polymer matrix. The CQACNT-6 composite membrane exhibited a 3.5-fold increase in pure water permeability (PWP; 312.8 L m−2 h−1 bar−1) as compared to the pristine PES (CQACNT-0) membrane (89.6 L m−2 h−1 bar−1). Moreover, the CQACNT-6 composite membrane showed high HM removal rates (Pb: 89.53%; Ni: 90.42%; Cu: 91.43%; Zn: 91.86%) as compared to the CQACNT-0 membrane (Pb: 39.73%; Ni: 40.32%; Cu: 42.52%; and Zn: 43.91%). After 9 treatment cycles, the CQACNT-6 membrane retained up to 87%, and 94% of its initial PWP and initial Cu2+ rejection, respectively, compared to only 58%, and 54%, respectively for pristine CQACNT-0. The positively charged quaternary ammonium groups enhanced the surface features of PES and MWCNTS, resulting in competitive HM removal rates due to the electrostatic repulsion between the HM and the porous membranes, as well as high PWP.


INTRODUCTION
The global boom in industrialization has increased the level of toxic pollutants in various water bodies more than ever before 1,2 . Heavy metals (HMs) are persistent water pollutants with a toxic, non-biodegradable nature and a great tendency to accumulate in living organisms 3 . HMs are present as soluble salts in industrial wastewater, creating a threat to terrestrial fauna and aquatic life cycles 4 . HMs can decrease the oxygen intake of marine organisms, which causes severe injury to basic cellular processes, brain functions, kidneys, and liver 3 . Removing HMs from industrial wastewater is challenging due to their small size, diversity, and toxicity 5 . The most common HMs found in wastewater are Pb, Ni, Cu, and Zn 6,7 . Water remediation technologies such as ion exchange 8,9 , adsorption 10 , electrochemical treatment 3 , chemical precipitation 7 , coagulation and flocculation 1 , and membrane filtration 11 have been applied for the removal of HM. The major drawbacks of ion exchange, adsorption, electrochemical treatment, chemical precipitation, coagulation and flocculation include operational and sludge disposal cost, partial removal of certain ions, and high energy consumption. Among all, membrane-based removal technologies have gained specific attention because they are considered environmentally friendly, cost-effective, and have a low-energy consumption [12][13][14] . Membrane composites applied in pressure-driven filtration processes can be divided into three categories based on their surficial charge (positively, negatively, and neutrally charged) 4,15 . Among all, positively charged membranes (PCMs) are highly effective in HM removal due to the electrostatic repulsion between the PCM surface and positively charged HMs, leading to enhanced separation efficiencies 4,7,12,14 .
Recently, various studies have been conducted to prepare new PCMs for the removal of HMs 4,7,14,[16][17][18][19][20] . Li et al. developed a type of PCM by surface grafting of polyamide with poly(amidoamine) dendrimer 4 . The prepared PCM exhibited more than 90% removal rates. A PCM prepared by self-assembly of ethylenediamine grafted multiwalled carbon nanotube (MWCNT) on the surface of polyethersulfone (PES) membrane showed a pure water flux (PWF) of 80.5 L m −2 h −1 at 10 bar pressure with a rejection rate of at least 90% for various HMs 14 . Zhou et al. developed a PCM by surface quaternization of poly (vinyl chloride co dimethylaminoethyl methacrylate), which exhibited 95% rejection of HMs and a pure water permeability (PWP) of 84 L m −2 h −1 bar −1 7 . Wu et al. modified polyamide by surface-initiated atom transfer radical polymerization of methacryloxyethyltrimethyl ammonium chloride grafted to 2-bromoisobutyryl bromide 16 . The modified membrane exhibited a stable long-term operation for 168 h with more than 90% rejection of HMs and a PWF of 82.5 L m −2 h −1 at 6 bar applied pressure. Hyperbranched polyethyleneimine (PEI) cross-linked PCMs showed excellent performance for the removal of HMs 17,18 . Gong et al. synthesized a PCM by incorporating metalorganic frameworks into PEI and trimesic acid, showing a PWP of 12.2 L m −2 h −1 bar −1 and 90.9% rejection of NiCl 2 19 . A PCM prepared by interfacial polymerization of 1,2,3,4-cyclobutane tetracarboxylic acid chloride with PEI on a PES membrane exhibited a PWP of 156.85 L m −2 h −1 and a rejection of more than 90% for HMs 20 . These PCMs exhibited an excellent rejection rate for the HMs. However, the low PWP and poor long-term stability due to fouling are still major concerns 16,19,20 . Therefore, the development of PCMs with enhanced PWP and long-term stability can be driven by the incorporation of novel designed nanomaterials, such as MWCNTs, to attain boosted separation performances for the removal of HMs.
In this paper, a series of PCMs were fabricated by the surface silanization of hydroxyl MWCNT (MWCNT-OH) with bis [3-(trimethoxysilyl)propyl]amine (BTMSPA) followed by quaternization. To further enhance the positive charge, a glycidyltrimethylammonium chloride (GTMAC) was grafted on the surface of silanized MWCNT-OH by an epoxide ring-opening reaction. The performance of the developed PCMs was assessed in terms of PWP, HM rejection, antifouling behavior, as well as physicochemical properties. Moreover, a comparative analysis of the separation performance of the optimal PCM fabricated with reported PCMs in literature was carried out.

RESULTS AND DISCUSSION
Synthesis and characterization of CQACNT The CQACNT was synthesized by a two-step reaction: (i) surface silanization process of MWCNT-OH by BTMSPA and (ii) epoxide ring-opening reaction of GTMAC to form CQACNT ( Fig. 1(a)). The structural and surface morphology of the MWCNT-OH and CQACNT nanomaterials was assessed using the SEM images shown in Fig. 1 . The MWCNT-OH shows a 1D tubular structure with a smooth surface ( Fig. 1(c)). On the other hand, SEM analysis of CQACNT showed similarly a 1D tubular structure with linkages between tubes and rugged appearance ascribed to the crosslinking of MWCNT-OH by silanization ( Fig. 1(e)). Further, TEM images ( Fig. 1(f and g)) confirmed the 1D tubular structure of MWCNT-OH and CQACNT. The surface modification of MWCNT-OH by silanization followed by quaternization was confirmed by FT-IR spectra ( Fig. 1(h)). The FT-IR spectrum of MWCNT-OH displays the bands at~1705,~1377 and~1102 cm −1 , that are ascribed to the characteristic peaks for C=O, C-OH (bending) and C-O stretching, respectively. The MWCNT-OH mixture was crosslinked with BTMSPA to introduce silane and amine moieties on the surface. As compared to the FT-IR spectrum of MWCNT-OH, that of CQACNT showed two new peaks at 1180 cm −1 , and 1022 cm −1 corresponding to the absorption band for C-N and Si-O-C. This confirmed the successful grafting of the silane and amine moiety onto the surface of MWCNT-OH. Furthermore, a new peak at 1484 cm −1 corresponding to C-N + confirmed the grafting of the quaternary ammonium groups. These observations confirm that silanization followed by quaternization of MWCNT-OH have been successfully carried out. MWCNT-OH is a graphitized nanomaterial that has equivalent elemental domains of the parallel stacking of hexagonal carbon structure. The XRD pattern was used to recognize structural modification after reaction with BTMSPA. Figure 1(i) shows the XRD patterns of the MWCNT-OH and CQACNT nanomaterials. XRD patterns of MWCNT-OH showed characteristic peaks at 2θ of 26.18°(002), 43.4°(100), 53.1°(004), and 78.8°(110) 21 . After modification, the XRD patterns of CQACNT showed that the peak positions remained unchanged with a decrease in the intensity, demonstrating the silanization and functionalization occurring on the surface of MWCNT-OH.
XPS analysis was used to determine the surface atomic contents of the MWCNT-OH and CQACNT. The XPS survey spectrum of MWCNT-OH confirmed the presence of C 1 s, and O 1 s at binding energies (B.E.) of 283.7 eV, and 532.6 eV, respectively, while CQACNT shows Si 2p, Si 2 s, C 1 s, N 1 s, and O 1 s at the B.E. of 102 eV, 152 eV, 283.7 eV, 401 eV, and 532.6 eV, respectively (Supplementary Fig. 1). It can be seen that the survey spectrum of CQACNT showed two new peaks of N 1 s, and Si 2p, and confirmed the successful silanization and functionalization of the MWCNT-OH. The deconvolution of the bands in the C 1 s, O1s, Si 2p, and N 1 s high-resolution XPS (HR-XPS) spectra of MWCNT-OH and CQACNT is shown in Fig. 2(a)-(d). The C 1s HR-XPS spectra of MWCNT-OH and CQACNT could be deconvoluted into three major bands at B.E. of 284.5 eV, 285.6 eV, and 286.5 eV, assigned to the graphitic structure (C=C), C-C (Sp 3 ) defect bonds on the MWCNT-OH structure, and C-O bonds in alcohols, phenols, and ethers, respectively 22 . It can be seen that the band at B.E. of 286.5 eV in CQACNT became intense and broad, which could be attributed to the overlaps of B.E. of the C-N bond with the C-O 23 . The deconvoluted O1s HR-XPS spectrum of MWCNT-OH shows three peaks at B.E. of 531.8 eV, 533.1 eV, and 535.2 eV, attributed to the O=C from quinone, O-C from alcohol and phenol, and O-H from water, respectively 22 . As compared to the deconvoluted O 1 s HR-XPS spectrum of CQACNT with MWCNT-OH, two new broad bands in CQACNT were observed at B.E. of 532.5 eV, and 534 eV, assigned to -O x Si overlapped with parental O=C and O-C bands and Si-OH or Si-O-Si band, respectively ( Fig. 2(b)) 24 . The deconvoluted Si 2p HR-XPS spectrum of CQACNT, showed broad bands at B.E. of 102.8 eV, and 104 eV, assigned to Si-O bonded to MWCNT-OH and Si-O-Si and confirmed the successful grafting of BTMSPA. Furthermore, the HR-XPS spectrum of N 1 s of CQACNT showed two peaks at the B.E. of 400.7 eV, and 402 eV, assigned to N-C to amine, and N + -C to positively charged quaternary ammonium groups, respectively ( Fig. 2(d)).

Membrane preparation and characterization
The CQACNT composite membranes were prepared by NIPS using a dope solution of CQACNT (0-8 wt%) with PES. The detailed membrane fabrication process, the chemical structure of the membrane, the possible interactions between PES and the CQACNT, and optical images are given in Fig. 3(a). It is expected that the CQACNT is stabilized in the PES matrix by forming a strong H-bond between the oxygen-containing groups. The optical images of the pristine CQACNT-0 and modified membrane CQACNT-6 display white and dark colors, respectively. Figure 3(b) shows the FT-IR spectra of the CQACNT-0 membrane and the CQACNT-6 composite membrane. The absorption bands at 1574 cm −1 , 1395 cm −1 , 1236 cm −1 , and 1147 cm −1 are attributed to the stretching vibrations of aromatic C=C, C-H, symmetric S=O and asymmetric S=O, respectively, from PES moieties 25 . The presence of silica moieties (silanization) in the CQACNT-6 membrane was confirmed by an absorption band at 1072 cm −1 attributed to the stretching vibration of Si-O-C group. Furthermore, the functionalization of the CQACNT-6 membrane with quaternary ammonium groups was confirmed by the presence of absorption bands at~1485 cm −1 , and 1180 cm −1 levels attributed to the C-N + and C-N stretching, respectively. Due to the very low concentration of the CQACNT nanomaterial (6 wt%) in PES polymer matrix, the intensities of a few peaks are either weak or merged with other peaks. XRD was used to recognize the possible structural changes within the membrane matrix. Figure 3(c) shows the XRD patterns of CQACNT-0, and the CQACNT-6 membrane. The CQACNT-0 membrane showed a characteristic diffractogram of an amorphous membrane that has a maximum intensity peak at about 2θ value of 17.87°and a minor peak at about 2θ value of 43.33°. Interestingly, the XRD pattern of the CQACNT-6 membrane exhibited an amorphous nature where the characteristic PES 2θ peaks were still detected but wider with a higher peak intensity and shifted from 17.87°to 18.90°. The broadening and shifting of the peak at 18.90°can be attributed to the incorporation of the CQACNT nanomaterial into PES.
The structural morphology (top, bottom, and cross-sectional surfaces) of the CQACNT-(0-6), MWCNT-OH-6, and CASCNT-6 membranes were studied using SEM (Fig. 4). SEM images of the top surfaces of all membranes revealed a smooth, dense structure, free from any defects. However, the SEM image of the bottom surface of membranes displayed a visible distribution of the pores. The density and size of the pores on the bottom surface increase with the incorporation of CQACNT. Cross-sectional SEM images of  the prepared membranes showed a sponge-like structure with asymmetric fingers and a dense top layer. Incorporation of the CQACNT into the PES membrane matrix caused an increase in the porous structure with irregular fingers, attributed to the silanization and functionalization with quaternary ammonium groups.
The roughness of a membrane surface plays a crucial role in determining the separation performance and the fouling tendency of a membrane. A membrane with a rougher surface has a higher tendency to foul, thus declining the separation performance with time 26 . Figure 5(a)-(g) shows the AFM analysis of the CQACNT-0 and CQACNT-6 composite membrane. The AFM images confirmed the decrease in the surface roughness after the addition of CQACNT to the PES matrix. The results showed actual surface area roughness (R a ) and root means square roughness (R q ) of 59.7 nm, and 72.2 nm, respectively for CQACNT-0 and 25.1 nm, and 31.1 nm, respectively for CQACNT-6 ( Fig. 5(g)). This could be attributed to the migration of the functionalized CQACNT nanomaterial to the membrane interface during the NIPS phenomenon, creating a more hydrophilic surface area that ultimately results in a smoother surface.
Membrane wettability, surface free energy, and WU are crucial properties that regulate its separation performance in dynamic filtration systems. The measure of the WCA was used to determine the wettability of the membrane 27 . A low value of WCA designates that the membrane surface is highly wetted, leading to enhanced water permeation and anti-fouling capacity 28 . Figure 6(a) and (b) show the static and dynamic WCA of the prepared CQACNT-(0-6), MWCNT-OH-6, and CASCNT-6 composite membranes. The static WCA of the CQACNT composite membranes decreased with the increased incorporation of CQACNT into PES. CQACNT-6 showed the lowest static WCA (46°), which is 1.51-fold, 1.35-fold, and 1.34fold less, as compared to the pristine CQACNT-0, MWCNT-OH-6, and CASCNT-6 membranes, respectively. The dynamic WCA of the prepared membranes showed a decrease with time. The CQACNT-6 membrane showed the highest drop in dynamic WCA (15°; from 46°to 31°, over a period of 160 s), as compared to the pristine CQACNT-0 (6°), MWCNT-OH-6 (9°), and CASCNT-6 (9°) membranes ( Fig. 6(b)), demonstrating enhancement in the overall wettability. The increased wettability of the CQACNT-6 membrane is attributed to the exceptional hydrophilic nature of the CQACNT. Furthermore, the wettability of the prepared membranes was evaluated by calculating the membrane-water interfacial free energy ðÀΔG SL Þ (Fig. 6(c)). A high value of ÀΔG SL , represented a more wetted membrane surface and thus excellent affinity for water 29 . The CQACNT-6 membrane showed the highest ÀΔG SL (131.88 mJ m −2 ), as compared to the pristine CQACNT-0 (108.73 mJ m −2 ), MWCNT-OH-6 (116.14 mJ m −2 ), and CASCNT-6 (117.42 mJ m −2 ) membranes, indicating the high wettability of the CASCNT-6 membrane. The water holding capacity in the membrane matrix provides an indication of the unobstructed pathway for water permeation during the dynamic filtration process. The water holding capacity of each membrane was evaluated in terms of WU ( Fig. 6(d)). The amount of water content present in the membrane matrix depends on the ionic clusters, wettability, and void volumes existing in the membrane matrix 30 . The WU was found to increase upon blending of CQACNT into the PES matrix. The CQACNT-6 membrane exhibited a higher WU (107.53%), as compared to the pristine CQACNT-0 WU (59.42%).
Surface charge, IEC, porosity, and MPS analysis of prepared membranes The surface zeta potential of a membrane is a vital property that expressly affects the rejection capability of charged pollutants. The surface zeta potential of the membranes developed was estimated in water for a wide pH range (4-9) and is presented in Fig. 7(a). The zeta potential of the pristine CQACNT-0 membrane was~−9.38 mV, which was transformed to a positively charged surface after the incorporation of CQACNT. The CQACNT-6 membrane showed a charge of +20.46 mV at pH = 6. It can be seen that the MWCNT-OH and CASCNT incorporated membranes, namely MWCNT-OH-6, and CASCNT-6 exhibited negatively charged surfaces with zeta values of −6.38 mV, and −5.23 mV at pH = 6, respectively. The incorporation of quaternized CQACNT into the PES polymer matrix resulted in a stronger positively charged surface, which indicates that many positively charged quaternary ammonium groups occur on the membrane surface. The positively charged surface will efficiently boost the strong positive-positive electrostatic repulsion between the CQACNT composite membranes and positively charged pollutants. Furthermore, the presence of a positively charged surface of developed CQACNT membranes was confirmed by IEC. The IEC represents the sum of all positively charged active sites or quaternary ammonium groups that are responsible for the exchange of ions in the membrane matrix. It can be seen that the IEC of the pristine CQACNT-0 membrane increased with the incorporation of CQACNT, and the CQACNT-6 composite membrane showed a maximum IEC of 0.71 meq g −1 (Supplementary Fig. 2). Membrane porosity and MPS are crucial properties that significantly influence water permeability and HM rejection capability. These properties are functions of the ionic clustering of quaternary ammonium groups and membrane-water affinity. The porosity and MPS of the membranes developed are given in Fig. 7(b). It can be seen that the porosity and MPS increased upon the incorporation of CQACNT into PES. The CQACNT-6 composite membrane showed high porosity and MPS (porosity = 69.61%; MPS = 44.1 nm) as compared to the pristine CQACNT-0 (porosity = 57.72%; MPS = 27.5 nm), MWCNT-OH-6 (porosity = 64.18%; MPS = 33.9 nm), and CASCNT-6 (porosity = 62.42%; MPS = 32.9 nm) membranes. This trend can be explained by the increase in membrane wettability as a result of CQACNT. This leads to a faster exchange rate between solvent (NMP) and non-solvent (DI water), creating a more porous structure 31 . Furthermore, the quaternary ammonium groups existing in the CQACNT made ionic clusters that provided additional affinity toward water, consequently enhancing the porosity of the membrane.

PWP and heavy metal ion removal efficiency
The PWP of the CQACNT composite membranes increased remarkably by incorporating CQACNT into PES (Fig. 8(a)). The CQACNT-6 composite membrane exhibited a 3.5-fold increase in PWP (312.8 L m −2 h −1 bar −1 ) as compared to the pristine CQACNT-0 membrane (89.6 L m −2 h −1 bar −1 ). It can be seen that as compared to PES membranes incorporated with MWCNT-OH and  surface of the CQACNT composite membrane and metal ions during separation. It is expected that the highly positively charged surface of CQACNT composite membrane repels the positively charged metal ions, thus helping in improving the separation performance. The rejection efficiency of the fabricated membranes was evaluated by ultrafiltration of different heavy metal ions (Fig. 8(c)). The effects of applied pressure and feed concentration on the separation performance of the CQACNT-0 and CQACNT-6 composite membranes were evaluated (Fig. 8(d) & Supplementary Fig. 3). It can be seen that as the applied filtration pressure and concentration of metal ions increase, the rejection efficiency for both membranes decreases. The CQACNT-6 composite membrane showed a smaller drop in Zn 2+ removal efficiency upon increasing the applied pressure from 1 bar to 4 bar (8.22%), as compared to CQACNT-0 (29.2%). A similar trend was observed in the feed concentration, where the Zn 2+ removal efficiency decreased by 7.69% for CQACNT-6 and by 22.3% for CQACNT-0 when the feed concentration from 20 ppm to 100 ppm. The separation performances of the CQACNT-6 composite membrane in terms of PWP and HM removal were as compared to the reported literature on MWCNT porous membranes (

Anti-fouling and long-term durability test
The antifouling behavior of the CQACNT, MWCNT-OH-6, and CASCNT-6 composite membranes against metal ions (Pb 2+ , Ni 2+ , Cu 2+ , and Zn 2+ ) was estimated in terms of HM adsorption. High adsorption leads to higher chances of blocking the membrane pores by forming a concentrated layer, decreasing the antifouling capacity. The amount of metal ions adsorbed on the developed composite membranes is shown in Fig. 9(a). It can be seen that the adsorption capacity decreased with increasing CQACNT content. Among all membranes developed, the CQACNT-6 membrane showed the lowest adsorbed amount for Pb 2+ (4.21 µg cm −2 ), Ni 2+ (5.4 µg cm −2 ), Cu 2+ (6.42 µg cm −2 ), and Zn 2+ (7.61 µg cm −2 ). The CQACNT-6 membrane showed 9-times, 11-times, and 10times lower adsorption capacity of Pb 2+ , as compared to the pristine CQACNT-0, MWCNT-OH-6 and CASCNT-6 membranes, respectively. The decrease in the HM adsorption is attributed to the increased positive charge by incorporating CQACNT. The electrostatic repulsion produced between the positively charged surface of the CQACNT-6 membrane and positively charged HM ions leads to a lower deposition, which increases antifouling capacity.
To evaluate the long-term durability of CQACNT-6, normalized PWP and normalized rejection were compared with that of the pristine CQACNT-0 membrane using 9-cycles of Cu 2+ filtration. Deterioration in PWP and rejection of the CQACNT-6 membrane was significantly reduced as compared to the pristine CQACNT-0 membrane ( Fig. 9(b)). After 9 filtration cycles, the normalized PWP and rejection efficiency of the CQACNT-6 membrane deteriorated by 13%, and 6%, respectively. This is a significant improvement over the pristine CQACNT-0 membrane, which showed 42%, and 46% deterioration of PWP and rejection, respectively.

Stability of CQACNT in the membrane matrix
The stability of the CQACNT nanomaterial in the developed composite membrane can be attributed to the strong H-bonding between the CQACNT and PES polymer matrix. CQACNT interactions with the PES polymer matrix are schematically represented in Fig. 3(a). The -OH groups of CQACNT interact with the oxygencontaining groups in PES through H-bonding. Furthermore, the stability and interaction of CQACNT within the membrane were confirmed via leaching experiments. A CQACNT-6 membrane coupon was immersed in DI water for 10 d with continuous shaking. The IEC, water contact angle, and FT-IR spectra of the CQACNT-6 membrane showed no significant changes after 10 d and confirmed the stability of CQACNT in the composite membrane ( Fig. 10(a)-(c)). The alkaline stability test on the CQACNT-6 composite membrane showed small deterioration in the removal efficiency and PWP after 10 d (Fig. 10(d)). The CQACNT-6 membrane retained 99.1%, 97.27%, and 95.66% of PWP of its initial value after immersion in alkaline solution for 1, 5, and 10 d, respectively. Moreover, the CQACNT-6 membrane retained a removal efficiency of 98.16%, 96.24% and 94.38% of its initial value after immersion in alkaline solution for 1, 5, and 10 d, respectively.

Synthesis of cross-linked quaternary ammonium carbon nanotube (CQACNT)
Cross-linked quaternary ammonium carbon nanotube (CQACNT) was synthesized in a two-step reaction. The first step involves the silanization of MWCNT-OH by BTMSPA. In a typical synthesis procedure, MWCNT-OH (100 mg) was added to a three-neck round bottom flask with ethyl alcohol (100 mL) and dispersed via ultrasonication for 90 min. Then, BTMSPA (200 µL) was added, and the resulting mixture was left to stir under a nitrogen atmosphere at 70-75°C for 12 h. The reaction mixture was cooled to room temperature and ethyl alcohol was removed by filtration using Whatman filter paper (pore size 0.45 µm). Finally, the obtained product was washed with an excess amount of ethyl alcohol and filtered to remove any unreacted BTMSPA molecules. The powder was dried under vacuum for 24 h. The sample was named as crosslinked aminosilane carbon nanotube (CASCNT). The second step involves the epoxide ring-opening reaction of GTMAC. CASCNT (50 mg) and GTMAC (100 µL) were added to a three-neck round bottom flask containing ethyl alcohol (100 mL) and stirred for 3 h at 75°C. Finally, the reaction mixture was cooled to room temperature, washed with an excess amount of ethyl alcohol, and dried under vacuum for 24 h. Thus, CQACNT was obtained as the final product.

Synthesis of CQACNT composite membranes
The CQACNT composite membranes were prepared by the nonsolvent induced phase separation (NIPS) method. 0-8 wt% of MWCNT-OH, CASCNT and CQACNT relative to PES were dispersed in NMP by bath sonication for 1 h. Then, PVP was gradually added to the above mixture under stirring at room temperature. The PES was then gradually added with constant stirring and the final mixture was kept for 2 h at 70°C. The subsequent mixture was stirred continuously for another 24 h at room temperature to obtain a homogeneous dope solution. Finally, the doped solution was degassed under a vacuum oven and cast on a glass plate using a casting knife with a thickness of 250 μm. The casted membrane was finally placed in a coagulation bath containing DI water at 24°C. The prepared membranes were removed from the coagulation bath, washed thoroughly with DI water, and used for characterization. The prepared membranes were named MWCNT-OH-X, CASCNT-X, and CQACNT-X, where X represents the weight percentage of the respective nanomaterial in the composite membrane. The detailed composition of each prepared membrane is given in Supplementary Table 1.

Instrumental characterization of materials and membrane
A series of characterizations were performed for both the material and the membranes. Fourier Transform Infrared Spectroscopy (FT-IR), X-ray Diffraction (XRD), X-ray Photoelectron Spectroscopy (XPS) were applied to study the chemical structure of the synthesized materials and fabricated membranes. Scanning Electron Microscopy (SEM), Transmission electron microscopes (TEM) and Atomic Force Microscope (AFM) were applied to assess the morphology. The measurements of zeta potential, optical images, and water contact angle (WCA; θ) were performed to study the physicochemical properties. The details of all of the above analyses are explained in Supplementary Note 1. The membrane liquid interfacial surface free energy (ÀΔG SL ) was estimated from modified Young-Dupre equation (Eq. (1)) using the WCA of prepared membranes 32 : where γ L is the surface tension of water (72.8 mJ m −2 ) at 25°C, and SAD is the difference in surface roughness area. Roughness refers to the ratio of the actual surface area (R a ) to the projected surface area (R p ).
where N is the milliequivalent amount of the ion exchange group estimated by titration, and M dry is the weight of the dry membrane (g).
Pure water permeability (PWP) and heavy metal ion removal efficiency The separation performance of the prepared membranes was evaluated by measuring their PWP and metal-ion-removal efficiency. All separation performance experiments were evaluated using a dead-end filtration setup (HP4370 Sterlitech, Co, USA) with an effective membrane area of about 1.25 × 10 −3 m 2 . The prepared membranes were first compacted by filtering DI water at a pressure of 1.5 bar for 1 h. PWP was calculated using Eq. (3): where V is the permeate volume of water (L), A is the effective area of the membrane (m 2 ), Δt is the filtration time (h), and ΔP is the applied pressure (bar). HM ion retention of the prepared membranes was evaluated by filtering a solution containing a mixture of inorganic salts (Pb(NO 3 ) 2 , NiCl 2 , CuCl 2 and ZnCl 2 ) dissolved in DI water with concentration of 45 ppm each salt. A solution of 0.1 M HCl was used to adjust the pH of the prepared solution to ensure solubility and avoid precipitation of HM at high pH. The HM rejection coefficient (R; %) of the prepared membranes was calculated using Eq. (4): where C b and C p are the concentrations of heavy metal ions in the feed and permeate, respectively. Inductively Coupled Plasma-Optical Emission Spectrometry (ICP-OES; Model 5100 SVDV, Agilent, USA) was used to measure these concentrations.

Antifouling and long-term durability test
The antifouling capacity of the fabricated membranes was evaluated by immersing square membrane coupons (4 × 4 cm 2 ) in an aqueous metal salt solution (150 ppm; 50 mL) and kept in a shaker for 24 h. After 24 h, all membranes were removed from the solution and the amount of metal ions adsorbed by each membrane (M ad ) was calculated according to Eq. (5) 34 : where C i , and C f are the initial and final concentrations (mg L −1 ) of the metal ion, V is the volume of solution (L), and A is the area of the membrane (cm 2 ). Long-term durability was assessed by calculating the flux recovery ratio and rejection recovery ratio in terms of normalized flux and normalized rejection over 9 cycles (each cycle took 2 h). Each cycle begins with the filtration of DI water for 60 min and then salt solution filtration for 60 min. After completion of each cycle, the used membrane was washed with a 0.1 M HCl solution to dissolve any deposited HMs followed by DI water several times. The applied pressure during all experiments was kept constant at 1 bar. Normalized flux and normalized rejection were calculated using Eq. (6) & (7), respectively: where, J i , J f , R i and R f are initial PWP, PWP after each cycle, the initial rejection, and the rejection after each cycle of the filtration experiment, respectively.

Stability of CQACNT in the membrane matrix
The stability of CQACNT in the polymer membrane matrix was evaluated by FT-IR, IEC, and WCA investigation of the prepared membrane surface before and after being placed in DI water in a closed vessel for 10 d under vigorous shaking. The alkaline stability of the membrane was tested by dipping the membrane samples in 0.01 M NaOH solution at room temperature for 1, 5, and 10 d. After that, the membranes were washed several times with DI water and the separation performance was evaluated in terms of PWP and rejection.

DATA AVAILABILITY
All data generated or analyzed during this study are included in this published paper, and its supplementary information files.