Introduction

Water treatment processes confront significant challenges in terms of optimizing technology to avoid human health concerns and to ensure environmental sustainability, as population grows, water sources become scarcer and water quality deteriorates due to land use and climate change1. These water-related issues are better understood and handled as a result of enhanced detection and awareness of the toxicological, environmental, and biological effects of an ever-growing list of substances dubbed Emerging Pollutants (EPs). EPs are a group of man-made chemicals, such as pharmaceuticals, pesticides, flame retardants, detergents, and cosmetics, that are essential to contemporary living and whose manufacture and use have risen dramatically in the previous decades1,2,3. The uncontrolled and continuous release of these new compounds into the environment may have an impact on aquatic biota, human health4,5 and also the performance and costs of drinking water treatment technologies6,7.

Antibiotics are classified as a type of persistent pollutant that lead to fast spread of different types of resistant bacteria. Cefotaxime is important type of cephalosporin antibiotics for the treatment of gram negative and positive bacterial infections with a lengthy half-life owing to its aromatic-ring structure. It is usually detected in wastewater and drinking water and is very difficult to totally remove8. Nowadays, there are different techniques have been applied to eliminate antibiotics from aquatic system, such as oxidation9, adsorption and degradation10,11. Between these techniques, adsorption is cheap, simple, promising method for antibiotics, organic and inorganic contaminants removal from water12,13,14,15. The polymeric beads as adsorbent have been more favorable than the nanoparticles, film or fiber forms because of its easy fabrication, excellent dispersion, controllable size dimension and quick recovery process.

Carrageenan is a sulfated polysaccharide made up of anhydrogalactose and galactose units found in red seaweed extracts16. Iota carrageenan is the most often utilized, which comprise two sulfated groups per disaccharide unit. Because of its chemical functionality and natural abundance, it is widely used for water treatment, namely in the removal of pharmaceutical contaminants and pesticides17.

Poly vinyl alcohol (PVA) is an eco-friendly, biodegradable and cost-effective polymer with outstanding chemical stability and hydrophilicity properties; therefore, it is widely used to eliminate various pollutant from water. This type of polymer contains abundant hydroxyl groups and can be easily coagulated and cross-linked, however, by mixing PVA with IC lead to create porous network rich with hydroxyl and sulfate groups, which can be effective for the adsorption capacity enhancement18.

The presence of metal oxide nanostructures in the surface and structure of polymeric matrix leads to the production of nanocomposite polymeric-based matrix, which has been proposed as one of the most potent tools for preventing membrane fouling in various water treatment processes19,20,21,22,23. Among metal oxide nanoparticles, ZrO2 has received a lot of interest in recent years due to its unique properties such as good chemical and mechanical stability with high hydrophilic properties, in addition to their availability, low cost and simple synthesis method21. However, sulfated zirconia as the adsorbent consider as a cation exchanger that promotes more elimination of the cationic counterpart such as wide sector of antibiotics which contain amine groups.

This work aimed to synthesis eco-friendly and effective green adsorbent nanocomposite beads prepared by using water as a solvent to process biodegradable and low-cost polymers to remove Cefotaxime antibiotic contaminant from water. PVA was chosen as the key polymer in the beads due to its good interaction with IC polymer to form compatible composite rich with functional groups, in addition to supporting SZrO2 nanoparticles. To our knowledge, this is the first time to SZrO2 nanoparticles have been incorporated into PVA/IC blending polymers matrix in different concentrations to create nanocomposite beads named as SPVA/IC/SZrO2 and use it as adsorbent for antibiotics in water treatment.

Experimental

Iota carrageenan (type V), PVA (99% hydrolysis and medium MW), Cefotaxime sodium salt and 4-sulphophthalic acid (SPA) (99.9 wt.% in H2O) were purchased from (Sigma-Aldrich, USA) and Glutaraldehyde (GA) (50 wt.% in H2O) was purchased from Alfa Aesar.

Synthesize

Synthesize of nano-sulfated zirconia (SZrO2)

Nano SZrO2 was prepared using a simple calcination method in the absence of any solvent between zirconium oxychloride octahydrate ZrOCl2.8H2O and ammonium sulfate (NH4)2SO4 with 1:5 molar ratio were mixed and ground in a mortar then placement for 12 h at room temperature, after that calcined for 5 h at 600 °C. Finally, the powder was ground in ball mill at 1500 rpm for 30 min to obtain nano size.

Preparation of SPVA/IC/SZrO 2 beads

First, PVA and IC were dissolved separately in 100 mL deionized H2O at 90 °C for 2 h then blending with percentage PVA: IC (95:5) wt.%. After that, crosslinking the polymers blend by certain amount of GA as covalent crosslinker and SPA as ionic crosslinker and sulfonating agent for PVA, to convert to sulfonated polyvinyl alcohol (SPVA)22. Then the prepared nanocomposite was incorporated with different concentrations of SZrO2 (1wt.% and 2.5wt.%) in polymeric blend. The two solution samples were named SPVA/IC/SZrO2-1, SPVA/IC/SZrO2-2.5. The composite solution was put in syringe, dropped in saturated solution of boric acid to form beads, and left for overnight then washing.

As illustrated in Fig. S1 in supplementary information which shows the possible structure of SPVA/ IC/ SZrO2 beads, esterification reactions between carboxylic groups of SPA and hydroxyl groups of two polymers were used to ionically crosslink IC and PVA. Furthermore, acetal interactions between GA's aldehyde groups and the hydroxyl groups of the two polymers covalently crosslinked the two polymers. While SZrO2 was bonded to polymeric matrix by hydrogen bond interactions between its oxygenated groups and the -OH groups of two polymers.

Characterization

The characteristic groups of SZrO2 powder and the nanocomposite beads were monitored by Fourier transform infrared spectrophotometer (Schimadzu FTIR-8400 S-Japan), while the structures were evaluated by X-ray diffractometer (Schimadzu7000-Japan). Thermal changes of SPVA/IC/SZrO2 beads were traced by using thermo-gravimetric analyzer (Shimadzu TGA-50, Japan) the range of the temperature was 25–800 °C, under nitrogen atmosphere and the heating rate at 10 °C min−1. Morphological structure of the SPVA/IC/SZrO2-2.5 beads was shown by scanning electron microscope (SEM) combined with energy-dispersive analysis X-ray (EDX) (Joel Jsm 6360LA-Japan). Visualization of the nano SZrO2 was done by using transmission electron microscopy (TEM, JEM 2100 electron microscope).

To investigate the beads stability, pieces with diameter of 1 mm were immersed in 100 mL of deionized water at 35℃ for 24 h. The swelling coefficient S was calculated as follows:

$$\mathrm{S}\left(\mathrm{\%}\right)=\frac{{\mathrm{W}}_{w}-{\mathrm{W}}_{d}}{{\mathrm{W}}_{d}} \times 100$$
(1)

where Ww and Wd were the masses of the swollen and dry PVA/IC/SZrO2 nanocomposite bead, respectively.

To determine the point of zero charge (pHpzc) of PVA/IC/SZrO2 nanocomposite bead, 5 mg of beads were added up to 10 mL of solutions containing the pH values ranging from 3 to 9. The suspensions were then shaken gently for 24 h, then final pH values of every solution were recorded and the pHPZC values was calculated.

Batch adsorption tests

Adsorption tests were carried out by using a batch equilibration technique. One gram per liter stock solutions of Cefotaxime antibiotic were diluted to different degrees by adding deionized water. However, 50 mL of Cefotaxime antibiotic solutions with different concentrations (25, 50,100 and150 mg L-1) at 25 ˚C were added with a specific amount of prepared nanocomposite beads, with the help of a thermostated shaker running at 150 rpm. After reaching equilibrium, the adsorbent beads were separated and the remaining antibiotic concentration in the aqueous phase was measured using a UV spectrophotometer at 235 nm.

The amounts of adsorbed antibiotic were calculated according to the following formulas:

$${q}_{t}=\frac{{C}_{0}-{C}_{t}}{m} V$$
(2)
$${q}_{e}=\frac{{C}_{o}- {C}_{e}}{m} V$$
(3)

where qt and qe (mg g−1) were the amounts of antibiotic adsorbed per unit weight of adsorbent at time t and equilibrium; C0, Ct and Ce mg L−1 were the antibiotic concentrations at initial time, time t and the equilibrium time, respectively; V (L) was the volume of antibiotic solution; and m (g) was the amount of adsorbent. The removal efficiency R was determined as follows:

$$R\left(\%\right)=\frac{{C}_{0}- {C}_{t}}{{C}_{0}}\times 100$$
(4)

To optimize the Cefotaxime antibiotic removal conditions, we tried to establish a relationship between factors and responses, according to a response surface methodology (RSM) model. The selected matrix for the response surface methodology followed the Box-Behnken design24, with 17 trials. To evaluate the adsorption process performance, three factors were used: A (time, min); B (initial antibiotic concentration, mg L−1); and C (beads adsorbent dose, mg), at three levels illustrated in Table S1 in supplementary information. Design-Expert, 13.0.9.0 programme from STAT-EASE, INC was used for experimental design, model construction and data analysis. After proper optimization of the adsorption, the kinetic and isotherm parameters of the process were characterized.

Static kinetics and isotherms models of adsorption

The rate and mechanism of the adsorption process could be elucidated based on kinetic studies with different initial concentrations of Cefotaxime antibiotic varied from 25 to 150 mg L−1. The pH was fixed at 5 and dose of adsorbent was 2 mg mL−1, while the adsorption time was varied from 0 to 24 h. In order to elucidate the adsorption kinetics, the pseudo-first-order, pseudo second-order and intraparticle diffusion models were applied, as illustrated in Table 1. Additionally, to describe how the adsorbate interacts with adsorbents and give a thorough understanding of the nature of interaction, the adsorption isotherm models were tested to validate the antibiotic uptake behavior of PVA/IC/SZrO2 composite bead using Langmuir and Freundlich isotherms.

Table 1 Kinetics and isotherms models of adsorption process.
Full size table

Reusability test

To investigate the reusability of PVA/IC/SZrO2 composite bead, 10 mg of beads was mixed with 50 mL of 20 mg L−1 antibiotic. The mixture was shaken for 15 min. after adsorption, the beads was separated. Then 0.01 M NaOH was added and the solution was shaken again for 15 min. Finally, the beads was repeatedly washed by 70% (v/v) ethanol aqueous solution, until antibiotic was no longer detected in the solution. The cyclic adsorption–desorption processes were conducted up to 10th cycle successfully to study the reusability of the nanocomposite.

Results and discussion

Morphological, physical and thermal characteristics of SZrO2 and nanocomposite beads

Figure 1a illustrate FTIR spectra of SZrO2 and PVA/IC/SZrO2 composite beads. SZrO2 spectrum shows a board peak at 3250 cm−1 and sharp peak at 1630 cm−1, that may be referred to the adsorbed moisture and hydrogen bonds formed, however, the peak around 500 cm−1 return to Zr–O bond, while, peaks at 1217, 1128 and 1016 cm−1 are characteristic for S–O. On the other hand, the FTIR spectra for PVA/IC/ SZrO2 nanocomposite beads, the bands around 3250 cm−1 are attributable to the O–H bonds from water molecules that become more adsorbed as the concentration of sulfated zirconia increases due to its hydrophilic properties, and the bands at 1600 cm−1 are indicative of –OH groups of PVA and IC. The sulphate groups of iota carrageenan have a distinctive peak at 830 cm−1. The C–H bonds in the polymers structure can be attributed to bands at 2840 and 2300 cm−125, while the weak bands at 1700 and 1750 cm−1 correspond to C=O bonds and C–H bending, respectively in the aromatic structure of sulfophithalic acid (SPA), which demonstrate that the crosslinking process has been completed. Sulfate groups of SZrO2 are responsible for the bands at 950 and 1100 cm−1.

Figure 1
figure 1

(a) FTIR spectra of SZrO2 and SPVA/IC/SO4ZrO2 composite beads, (b) XRD patterns of SZrO2 and SPVA/IC/ SZrO2 composite beads.

Full size image

In Fig. 1b it can be observed the amorphous structure for the prepared composite beads increased with increasing SZrO2 concentration, while the sulfated zirconia powder curve shows characteristic peaks intensity of SZrO2 at a 2θ angle 54, 28, 3826,27.

Figure 2a shows a semi-spherical shape for SPVA/IC/SO4ZrO2 composite beads and porous future for inside surface Fig. 2b. While the TEM image of sulfated zirconia in Fig. 2c demonstrated that, the material developed in nanoscale particles. EDX spectra as shown in Fig. 2d confirmed the presence of sulphur groups on the surface of SZrO2, proving the synthesize of sulfated zirconia.

Figure 2
figure 2

SEM images for (a) SPVA/IC/ SZrO2-2.5 beads surface, (b) SPVA/IC/ SZrO2-2.5 inside, (c) TEM image for SZrO2 nanoparticles with the inset frequency distribution plot of SZrO2 nanoparticles size from TEM image, (d) EDX analysis for SZrO2.

Full size image

As shown in Fig. 3, the TGA curves of beads without and with SZrO2shows about 8% loss in weight at ~ 150 ºC and that returns to the moisture evaporation21. The second loss stage of composite beads occurred in the range of 150—270 ℃ and is related to the degradation of functional groups, while the third loss stage is characterized by a remarkable decomposition from 270 to 360 ℃ and is related to the decomposition of polymeric chains, which began at 230 ℃ for the undoped beads and at 270 ℃ with a lower weight percentage for the doped beads. This behaviour demonstrates that the addition of SZrO2 improves the composite's temperature stability by boosting covalent, ionic, and hydrogen bonding in the nanocomposite.

Figure 3
figure 3

(a) TGA curves and (b) time dependent swelling response of SPVA/IC and SPVA/IC/SZrO2 nanocomposite beads.

Full size image

As shown in Fig. 3b, response of swelling behavior of SPVA/IC, SPVA/IC/SZrO2-1 and SPVA/IC/SZrO2-2.5 in water with respect to time was studied at room temperature. After a set amount of time had passed, the degree of swelling was assessed, and the immersion experiment lasted 24 h. SPVA/IC beads showed maximum degree of among other beads with SZrO2 and that can be explained by adding SZrO2 to the polymeric mixture of SPVA and IC may result in an increase in the amount of hydrogen bonds formed between polymer chains and SZrO2, resulting in increased chemical stability in polymer chains.

Adsorption process evaluation

Effect of solution pH and adsorption surface chemistry

It is crucial to investigate the beads' main surface charge at a certain pH. The calculation of the point of zero charge (pHPZC) is used for that purpose in addition, it can be used to comprehending the electrostatic interactions of the beads with Cefotaxime molecules. The point of zero charge of SPVA/IC nanocomposite beads was found around pH 6.5 while for SPVA/IC/SZrO2-1 and SPVA/IC/SZrO2-2.5 nanocomposite beads was found around pHs 6.1 and 5.3 respectively as shown in Fig. S3 in supplementary information. However, below these values of PZC the surface become positively charged on the other hand, above these values the surface acquired negative charge for the removal of positive molecules. The SZrO2 affects the PZC of SPVA/IC polymeric matrix and due to the greater percent of oxygenated groups content in SZrO2 lowers the value of PZC to 6.1 and 5.3 for SPVA/IC/SZrO2-1 and SPVA/IC/SZrO2-2.5 nanocomposite beads respectively. Two processes are involved in the absorption of Cefotaxime from aqueous medium by nanocomposite beads. The first is the diffusion of Cefotaxime into nanocomposite beads with water molecule penetration, and the second is associated with electrostatic attractive forces. The pH has a significant and observable impact on the absorption process. The influence of the pH of the solution on Cefotaxime adsorption process was studied in the range of 3 to 9 to find the optimal pH value, as shown in Fig. 4a. The results indicate the maximum adsorption has occurred at pH6. The significant decrease of the adsorption capacity at pH ranged between7and 9 may be due to the degradation of Cefotaxime followed by hydrolysis of the β-lactam ring and the acetoxy ester. In addition, increasing pH elevate the deprotonation of Cefotaxime, accordingly that will increase the repulsion between Cefotaxime molecules and negatively charged beads above its PZC values. On the other hand, at very low pH values less than 4, the protonation rate of Cefotaxime amine groups will increased, which increases its solubility and decreases its adsorption rate, besides the surfaces of SPVA/IC/SZrO2 would be surrounded by many hydronium ions that compete with Cefotaxime for active sites. While, the high adsorption capacity at solution pH ranged between 4 and 6 can be referred to maximum stability of Cefotaxime at pH ranged between 4 and 6 (pKa for Cefotaxime is 3.1)28 and that increase the possibility to form hydrogen bond and electrostatic attraction between nanocomposite beads and Cefotaxime molecules as shown in Fig. S4 in supplementary information. Thus, pH6 was selected for further adsorption studies of Cefotaxime.

Figure 4
figure 4

(a) Effect of solution's pH (0.01 g adsorbent beads, 50 mL of 100 mg L−1 Cefotaxime solution at 3 h adsorption time, and 25 °C temperature), (b) effect of SZrO2 concentration on Cefotaxime adsorption process.

Full size image

A batch adsorption process was used to investigate the effect of adding SZrO2 with different concentrations on Cefotaxime adsorption process onto polymeric beads. As shown in Fig. 4b it can be noted that the adsorption capacity of the beads was increased with increasing SZrO2 content and that may be referred to forming hydrogen bond and electrostatic attraction force between oxygenated groups of the composite and amino groups in Cefotaxime.

Effect of contact time

As shown in Fig. 5, for all beads samples, the adsorption capacity grew significantly at first, then gradually increased and eventually became constant over time. This could be due to the fact that there are free surface sites available for adsorption during the initial adsorption stage, but due to repulsive forces between Cefotaxime molecules adsorbed on beads and those in the solution, the remaining unoccupied surface sites are difficult to utilize as time passes. However, the adsorption process reached equilibrium after approximately 3 h. Furthermore, it can be also noticed the removal efficiency of Cefotaxime onto SPVA/IC/SZrO2-2.5 is higher than SPVA/IC and SPVA/IC/SZrO2-1 and that may referred to SPVA/IC/SZrO2-2.5 contain more active side than the other types of beads.

Figure 5
figure 5

Adsorption kinetics of Cefotaxime onto composite beads at C0; 100 mg L−1, dose of adsorbent beads 0.2 mg mL−1, at 25 °C and pH  6.

Full size image

The RSM is a model based on statistics and it is often used to clarify the interaction between reaction parameters for optimization since it is faster, practical and all of the components' effects and potential interactions may be evaluated. The adsorption of Cefotaxime onto SPVA/IC/SZrO2-2.5 nanocomposite beads was evaluated according to matrix design illustrated in Table S2 in supplementary information using independent variables including (A) time in hours, (B) Cefotaxime concentration in mg L−1 and (C) beads dosage in mg on dependent response, which is removal efficiency (%). To explain Cefotaxime elimination using SPVA/IC/SZrO2-2.5 beads, the following regression equation for the link between response and variables (A, B and C) was utilized:

$$ Removal \, \left( \% \right) \, = 95 \, + 6.21A \, - 11.25B \, + 17.46C \, + 5AB - 2.08AC + 10BC - 9.04A^{2} + 0.5375B^{2} - 13.04C^{2} $$

Moreover, according to the perturbation plot for Cefotaxime removal efficiency with SPVA/IC/SZrO2-2.5 nanocomposite beads as shown in Fig. 6, it was observed that as Cefotaxime concentrations increases the removal efficiency decreases, while factors time and beads dose have significant effect on removal efficiency whereas they increase, the removal efficiency increased and then decreased.

Figure 6
figure 6

The perturbation plot.

Full size image

ANOVA analysis of variance is well-known for determining the statistical significance of the quadratic response surface model. As shown in Table S3, the quadratic model is very suitable for high coefficient of determination R2 (0.9566). The p value of the quadratic model was less than 0.05, therefore, this quadratic model was found to be significant in addition this model is confirmed due to the F-value is found to be 17.16.

According to RSM analysis results as shown in Fig. 7, the following are the optimum conditions: initial Cefotaxime concentration is 88.97 mg L−1 at time: 3.58 h and adsorbent dosage: 11.68 mg to achieve full removal. The efficiency of Cefotaxime elimination was discovered to be impacted by all variable parameters.

Figure 7
figure 7

Response surface plots for removal efficiency (%) of Cefotaxime onto SPVA/IC/SZrO2-2.5 nanocomposite beads (a,c,e) 3D surface plots and (b,d,f) 2D surface plots.

Full size image

Kinetics and isotherms of adsorption process

Three kinetic models were used to study the adsorption of Cefotaxime onto SPVA/IC/SZrO2-2.5 nanocomposite beads: pseudo-first-order, pseudo-second-order, and intraparticle diffusion models. For the three kinetic models at varying concentrations, the calculated sorption capacities, reaction rate constants, and R2 values of the linear correlation coefficients were shown in Table 2. The sorption capacities estimated using the pseudo-first-order equation were found to be significantly different from the experimental results. While, for the pseudo-second-order kinetic model, the resulting R2 values are generally greater than those obtained from pseudo-first-order kinetics, implying that the sorption process followed pseudo-second-order kinetics and that chemisorption was the rate-controlling phase. This appears to include valence forces as a result of chemical reactions or electron exchange between oxygenated groups on Cefotaxime molecules and hydroxyl groups on nanocomposite beads and that were responsible for the hydrogen bonds. Despite the fact that the pseudo-second-order-kinetics model had the best fit order, the findings produced from this model were insufficient to evaluate Cefotaxime molecules' diffusion mechanism onto SPVA/IC/SZrO2-2.5 nanocomposite beads. As shown in Fig. S5 in supplementary information, the adsorption process linear fitting findings were consistent with the intraparticle diffusion model, whereas the diffusion mechanism was split into three stages that could be explained by the following. At the beginning Cefotaxime molecules transport through the solution to the bead surface and form film diffusion at the boundary layer, or charged molecules diffuse from a bulk solution to the beads' exterior surface after that the Cefotaxime charged molecules transferred into the pores and intraparticular active sites of beads. Finally, the Cefotaxime molecules were chemically bound via small pores in the beads, followed by the final equilibrium adsorption.

Table 2 Kinetic models’ parameters and determination coefficients for Cefotaxime adsorption onto SPVA/IC/SZrO2-2.5 nanocomposite beads.
Full size table

Langmuir and Freundlich models as shown in Fig. S6 were explored at different beginning concentrations and three different temperatures (25, 35 and 45 ºC), as illustrated in Table 3. The high adsorption capacity showed a strong electrostatic contact between Cefotaxime molecules and the bending sites of the beads, and the R2 values of the Langmuir model were extremely near to one. Furthermore, at low temperatures, RL values were higher than at high temperatures, and its values were found to be between zero and one, indicating that the adsorption process is chemical rather than physical22. However, the results showed that the adsorption process onto beads was best fitted by Freundlich isotherm model, with values of "n" ranging from 2 to 10, which indicate good adsorption and implying higher efficiency for Cefotaxime adsorption by nanocomposite beads as the values get increase.

Table 3 Adsorption isotherm parameters for Cefotaxime adsorption onto SPVA/IC/SZrO2-2.5 nanocomposite beads at adsorbent dosage 0.2 mg mL−1.
Full size table

Desorption–adsorption test

After 10 cycles, the adsorbent's ability to regenerate was tested, and it was observed that the removal efficiency was still high, and that the fluctuations in the removal % after each desorption cycle were quite minor, as shown in Fig. 8, indicating that SPVA/IC/SZrO2-2.5 nanocomposite beads had potential in wastewater application.

Figure 8
figure 8

Adsorption–desorption cycles.

Full size image

The efficiency of prepared SPVA/IC/SZrO2-2.5 nanocompoaite beads for drug removal was compared with other adsorbent materials as illustrated in Table 4.

Table 4 A review of the performance of some nanocomposite adsorbent materials used to remove drug from water.
Full size table

Conclusions

Novel and low expensive nanocomposite beads was produced using a simple blending, eco-environmentally approach and available polymers as PVA and IC. It was appeared that the incorporation of different weight ratio of SO4ZrO2 as doping agent into the polymeric PVA/IC blend improves the nanocomposite beads adsorption capacity towards Cefotaxime antibiotic. It was discovered that when the ultimate concentration of 100 mg L−1 Cefotaxime solution was compared at varied contact times and pH 6 conditions, the outcomes were better in the case of SPVA/IC/SZrO2-2.5 nanocomposite beads. The increasing of SO4ZrO2 content in the PVA/IC matrix increases porosity and active functional groups such as oxygen containing groups, so that the adsorption efficiency improves. At various experimental conditions, the time-dependent adsorption capacity was assessed. According to the experimental optimization, it was observed that as Cefotaxime concentrations increases the removal efficiency decreases, while factors time and beads dose have significant effect on removal efficiency whereas they increase, the removal efficiency increased and then decreased. The adsorption kinetic of Cefotaxime was better fitted to pseudo-second-order model, and the adsorption isotherm was better fitted to the Langmuir and Freundlich models. The ability of SPVA/IC/SZrO2-2.5 nanocomposite beads to regenerate ten times further demonstrated its suitability for long-term use. The current study reveals that SPVA/IC/SZrO2-2.5 nanocomposite beads have a lot of potential in water treatment for removing antibiotic pollutants because of their fast separation, ease of operation, high capture capacity, and good cycle performance.