Cadmium and Lead Removal from Aqueous Solution Using Magnetite Nanoparticles Biofabricated from Portulaca oleracea Leaf Extract

Magnetic nanoparticles of iron oxide (Fe 3 O 4 NPs) were prepared using a biosynthetic method to investigate their potential use as an adsorbent for adsorption of Pb(II) and Cd(II) from the aqueous solution. The present study for the ﬁ rst time used the magnetite nanoparticles from leaf extract of Portulaca oleracea for the removal of Pb(II) and Cd(II) metal ions. Characterizations for the prepared Fe 3 O 4 NPs (PO-Fe 3 O 4 MNPs) were achieved by using X-ray di ﬀ raction (XRD), ﬁ eld emission scanning electron microscope (FESEM), energy-dispersive X-ray spectroscopy (EDX), transmittance electron microscopy (TEM), and Fourier transform infrared (FTIR) spectroscopy. The batch adsorption process has been performed to study the e ﬀ ect of various parameters, such as contact time, pH, temperature, initial metal concentration, and adsorbent dose. The optimum pH for Cd(II) and Pb(II) adsorption was 6. The removal of heavy metals was found to increase with adsorbent dosage and contact time and reduced with increasing initial concentration. Langmuir, Freundlich, Khan, and Toth isotherms were used as adsorption isotherm models. The adsorption data ﬁ tted well with the Freundlich isotherm model with correlation coe ﬃ cient ( R 2 > 0 : 94 ). The maximum adsorption capacities ( Q max ) at equilibrium were 177.48mg/g and 108.2267 mg/g for Cd(II) and Pb(II), respectively. The kinetic analysis showed that the overall adsorption process was successfully ﬁ tted with the pseudo-second-order kinetic model. The calculated thermodynamic parameters ( Δ G ° , Δ H ° , and Δ S ° ) showed that the adsorption of Cd(II) and Pb(II) ions onto PO-Fe 3 O 4 MNPs was exothermic and spontaneous. These results demonstrate that biogenic synthesized PO-Fe 3 O 4 MNPs are highly e ﬃ cient adsorbents for the removal of Pb(II) and Cd(II) ions from contaminated water.


Introduction
Water is the most important molecule on the earth and is a source of sustainable life. However, millions of people face water scarcity daily [1]. Rapid population growth demands a rapid expansion in the agricultural and industrial sectors, resulting in increased demand for water, which is necessary for the survival of all living forms on this blue planet [2]. Due to the release of untreated organic/inorganic harmful effluents into freshwater bodies, rapid growth in industrialization, population, and urbanization has resulted in a severe exponential increase in environmental pollution [3][4][5].
When water is contaminated, removing the pollutants is costly, difficult, and often impossible. Water pollution is not only harming the organisms but also destroying entire ecosystems [6,7]. Heavy metals are well recognized among the various pollutants that contribute to environmental damage, owing to their persistence in the environment, toxicity, and bioaccumulative nature, all of which lead to negative consequences for human health and the ecosystem [8,9]. Lead, chromium, nickel, cadmium, and arsenic in the environment pose a serious threat to plants, animals, and even humans due to their bioaccumulation, nonbiodegradability, and toxicity even at trace concentrations [10].
Human exposure to even trace concentrations may result in conditions such as cardiovascular problems, depression, gastrointestinal and renal failure, neurological damage, osteoporosis, tubular and glomerular dysfunction, and various cancers [11,12]. Cadmium and lead are two of the most toxic metals for plants, animals, and humans. They are also harmful at low concentrations because they disrupt enzyme functioning, replace essential metals in pigments, and produce reactive oxygen species [3,13]. As a result of these serious issues, many effective methods to remove heavy metals have been developed, including ion exchange, membrane filtration, adsorption, photodegradation, coagulation-flocculation, electrodeposition, and electrooxidations [14][15][16][17][18]. Until now, adsorption is the most preferred method for water purification due to its efficiency, low operational cost, and application in both small-and large-scale operations [19]. Various kinds of adsorption materials have been used for water remediation, including carbon-based materials, clays, biological materials, bentonite, zeolites, metal oxide, magnetic nanoparticles, agricultural residues, and mesoporous substances such as MCM-41, MCM-48, and SBA-15 [20,21].
Magnetite nanoparticles (NPs) are strong adsorbents for removing pollutants from wastewater. Due to their magnetic properties, they may be easily isolated from the reaction media by applying an external magnetic field. Furthermore, the application of magnetic separation on the nanoadsorbents provides the crucial benefit of the rapid removal of toxic metals from wastewater [22].
Different methods including coprecipitation, thermal decomposition, microemulsion, and solvothermal techniques can be used to fabricate magnetite Fe 3 O 4 NPs [23]. Hazardous chemicals, organometallic precursors, and hard reaction conditions, such as high pressure or high temperature, are used in these procedures. However, these methods have several disadvantages, including high toxicity, low nanoparticle stability, exhibiting low dispersion rates, and undesirable to work within scaled-up applications [24,25]. Therefore, the fabrication of magnetite NPs by both economically and environmentally sustainable processes is necessary. The application of leaf extracts for nanoparticle synthesis has attracted a lot of attention in recent years, due to their low cost, nontoxicity, wide availability, strong metal capping affinity, biodegradability, and nonmutagenicity [26,27]. Alcohols, aldehydes, amines, carboxyl, ketones, hydroxyl, and sulfhydryl are the intervening functional groups in the synthesis of NPs; therefore, nearly any biological substance containing these groups can be used to convert metal ions into NPs. Some molecules, such as terpenoids, flavonoids, different heterocyclic, polyphenols, reducing sugars, and ascorbate, are directly involved in the synthesis of NPs, while others, such as proteins, serve as stabilizing agents [28]. Examples of plant extracts that have been used in the biosynthesis of NPs include Camellia sinensis, Quercus virginiana, Punica granatum, and Eucalyptus globulus [24], Moringa oleifera [29], and Calliandra haematocephala [30] in the remediation of various pollutants in water.
In this study, Portulaca oleracea (family: Portulacaceae; common name, purslane) leaf extract was employed to synthesize magnetite Fe 3 O 4 NPs. Due to the presence of various active phytochemicals such as alkaloids, phenols, flavonoids, coumarins, and terpenoids, Portulaca oleracea is commonly used in medical fields, such as drugs and medicine [31]. Only one study has investigated the preparation of Fe 3 O 4 NPs using Portulaca oleracea leaf extract [32].
In this work, we have reported for the first time the use of magnetite Fe 3 O 4 NPs from Portulaca oleracea leaf extract as efficient adsorbents to adsorb cadmium and lead from aqueous solutions. The Fe 3 O 4 NPs were prepared successfully and characterized by X-ray diffraction (XRD), field emission scanning electron microscope (FESEM), energydispersive X-ray spectroscopy (EDX), transmittance electron microscopy (TEM), and Fourier transform infrared (FTIR) spectroscopy. The effect of different parameters has been studied such as pH, temperature, initial metal concentrations, adsorbent dose, and contact time. Furthermore, isotherm, kinetics, and thermodynamic studies were carried out to understand the mechanism of the adsorption of metal ions by the biofabricated Fe 3 O 4 NPs.

Experimental Section
2.1. Materials. The leaves of Portulaca oleracea were obtained from the local market in Sulaymaniyah, Iraq. The chemicals: iron sulfate heptahydrate (FeSO 4· 7H 2 O) (Himedia, India), sodium hydroxide (NaOH) pellets (Merck, Germany), nitric acid (HNO 3 ) (Sigma Aldrich, Germany), lead nitrate (Pb(NO 3 ) 2 ) (Fluka), and cadmium nitrate (Cd(NO 3 ) 2 ) (BDH/England) were used as received without further purification. Stock solutions of lead and cadmium ions with concentrations of (1000 mg/L) were prepared by dissolving 1.598 g of lead nitrate and 2.744 g of cadmium nitrate in 200 mL of deionized water. A 10 mL concentrated HNO 3 was added to the metal ion solutions and then diluted to 1000 mL with distilled water. Solutions of HCl and NaOH (0.1-1 M) were used for pH adjustment.

Preparation of Portulaca oleracea Leaf Extract. Fresh
Portulaca oleracea leaves were washed with tap water to remove the dirt and surface-adherent materials and then with double-distilled water. The thoroughly washed leaves were air-dried for about an hour. The dried leaves were made into small parts and heated in 500 mL of deionized water for the release of phenolic biomolecules, which rendered the solution yellow. The clear yellow filtrate which was named Portulaca oleracea leaf (POL) extract after cooling was preserved at 4°C for further use [33].

Synthesis of Magnetic Fe 3 O 4 Nanoparticles.
A simple and eco-friendly method was used to prepare magnetite Fe 3 O 4 nanoparticles. In a glass beaker, a freshly prepared 0.1 M FeSO 4 solution (100 mL) was added to the POL extract at a volume ratio of 1 : 1 at room temperature. The pH of this mixture was increased to 11 by adding NaOH. The solution was then placed in a water bath for 60 min at 90°C. The formed black precipitate indicated the formation of magnetic Fe 3 O 4 nanoparticles (PO-Fe 3 O 4 MNPs). The PO-Fe 3 O 4 MNPs were isolated using a magnet and then washed several times with deionized water and ethanol. After that, 2 Journal of Nanomaterials the particles were dried overnight at 80°C in an air oven [30,34]. Figure 1 illustrates a green synthesis scheme for PO-Fe 3 O 4 MNPs.

2.4.
Characterization. An FTIR spectrometer (Thermo Scientific Nicolet iS10) was used to investigate the surface functional groups and capping agents of PO-Fe 3 O 4 MNPs. The crystalline structure of PO-Fe 3 O 4 MNPs was examined using an X-ray diffractometer (XRD) (PAN Analytical Xpert Pro, Netherlands). XRD was performed using Cu-Kα radiation (λ = 1:54 Å); the diffracted intensities of all samples were recorded in the 2θ range of 10°-80°with a step size of 0.1°a nd a scanning speed of 1 step/second. Field emission scanning electron microscopy (FE-SEM) (Quanta 4500, FEI) and transmission electron microscopy (TEM) (JEM-2100, JEOL, Japan) were used to examine the morphological characteristics and size of powdered PO-Fe 3 O 4 MNPs. The purity and the constituent elements of the prepared nanoparticles were confirmed by energy-dispersive X-ray spectroscopy (EDX) combined with FE-SEM.  [22]. After that, the magnetic nanoadsorbent was then isolated from the solution using magnets. The residual metal ion concentrations were measured using ICPOES.

Equilibrium Isothermal Investigation.
The equilibrium adsorption isotherm is important for understanding the interaction between adsorbate and adsorbent, which provides significant information about the surface characteristics, activity of the adsorbent, and mechanism of adsorption [36]. Different amounts of PO-Fe 3 O 4 MNPs (0.05, 0.1, 0.2, 0.4, 0.6, 0.8, 1, 1.2, and 1.4 g) were put into a number of conical flasks. Single metal solutions at concentrations of 50 mg/L were prepared for single systems of lead and cadmium ions, respectively, and then 100 mL from each solution was added to each flask. The pH of the metal solutions was adjusted to the optimum pH value. Thermoshaker was used to agitate the solutions continuously for an hour with a speed of 200 rpm and a temperature of 20 ± 2°C. The PO-Fe 3 O 4 MNPs were removed from the solutions with a magnet, and the samples were filtered using Whatman filter paper (no. 1). The Pb(II) and Cd(II) concentrations in the filtrate were determined using ICPOES. The removal efficiency and adsorption capacity of PO-Fe 3 O 4 MNPs were calculated from experimental data using [37].
Portulaca oleracea  3 Journal of Nanomaterials where C o (mg/L) is the initial concentrations of metal ions Pb(II) and Cd(II); C e (mg/L) is the equilibrium concentrations; V1 (L) is the volume of the metal solution, and W (g) is the dosage of PO-Fe 3 O 4 MNPs.
The experimental laboratory data obtained from isothermal adsorption experiments was interrelated to the common nonlinear adsorption model equations (Freundlich, Langmuir, Toth, and Khan) through the use of statistical software version 12 to compute fundamental parameters of each model. The Freundlich isotherm for heterogeneous surface energy systems is given as follows: where K corresponds to the maximum binding capacity and n characterizes the affinity between the sorbent and sorbate [38].
The Langmuir adsorption isotherm which describes the adsorbate-adsorbent system equilibrium shows that all adsorbed species interact only with one site and not with each other, and adsorption is confined to a monolayer    5 Journal of Nanomaterials [21]. The Langmuir model can be represented as where q m (mg/g) is the Langmuir maximum adsorption capacity and b (L/mg) is the Langmuir constant [39].
The Khan isotherm model is given in where b k and a k are Khan constants and q max is the maximum uptake [40].
The Toth isotherm is expressed as follows: where b T and n T are constants [41].
2.5.5. Kinetics. Adsorption kinetics describes the rate at which an adsorbate is retained or released from an aqueous environment to a solid-phase interface under various conditions [42]. The kinetic study was carried out using 0.5 g of PO-Fe 3 O 4 MNPs in 100 mL of single metal ion solutions with the concentration of 50 mg/L for each Pb(II) and Cd(II) at pH 6. The flasks with their contents were shaken for different adsorption times (10-70 min). The rate of sorption is analyzed by two kinetic models, namely, pseudo-first-order and pseudo-second-order.
The pseudo-first-order model explains that the rate of occupation of sorption sites is proportional to the number of unoccupied sites. The equation is represented as where k 1 (min −1 ) is the pseudo-first-order rate constant of adsorption and q t (mg/g) and q e (mg/g) are the amount of metal ions adsorbed at any particular time and equilibrium, respectively.
The pseudo-second-order kinetic model is based on the assumption that chemisorption is the rate-controlling step and is expressed as follows: where k 2 (g/mg·min) is the pseudo-second-order rate constant and q e (mg/g) and q t (mg/g) are the amount of the metal ions adsorbed at equilibrium and at time t, respectively [21,43].
2.5.6. Thermodynamic Parameters of Adsorption. The influence of temperature on Pb(II) and Cd(II) ion adsorption on PO-Fe 3 O 4 MNPs was studied at 20, 35, 45, and 55°C. About 100 mL of each solution with a concentration of 50 mg/L was mixed with 0.5 g of PO-Fe 3 O 4 MNPs, and then, the mixtures were maintained at a different temperature ranging from 20 to 55°C, for an hour and agitated at the speed of 200 rpm [4]. The nanoparticles were separated, and the Pb(II) and Cd(II) concentrations were measured using ICPOES.   The presence of agglomeration could be attributed to van der Waals forces that bind particles together and also shear forces that can be applied on the nanoscale [46]. The mean particle size is 26.0196 nm with a 9.05132 nm standard deviation.

Results and Discussion
The FESEM images of the PO-Fe 3 O 4 MNPs are shown in Figures 4(a) and 4(b). From FESEM images, it was clearly observed that the nanoparticles are bead-like, spherical in shape, with slight aggregation. Three of such nanoparticles, 34.52, 34.46, and, 46.71 nm, are mentioned in Figure 4(b). Similar spherical shapes were also reported when biosynthesis of Fe 3 O 4 was conducted using leaf extract of Mussaenda erythrophylla [47]. X-ray elemental mapping and energydispersive spectroscopy (EDX) were performed to reveal the presence of elemental constituents in the PO- The surface functional groups and capping agents of PO-Fe 3 O 4 MNPs which are responsible for the reduction and stabilization were studied by FTIR spectroscopy. Figure 5 illustrates the FTIR spectrum of PO-Fe 3 O 4 MNPs. The peaks were observed at 582 cm -1 and 790 cm -1 due to Fe-O vibrations of Fe 3 O 4 [48]. The band at 3394 cm -1 is attributed to the O-H group of polyphenolic compounds [49]. The band at 1662 cm -1 is assigned to -C=Cstretching vibration of alkenes [30]. The band at 1400 cm -1 belongs to C-C groups derived from aromatic rings found in the POL extract [50]. The bands between 1000 cm -1 and 1300 cm -1 were attributed to the C-O functional group in alcohols, ethers, ester,  7 Journal of Nanomaterials carboxylic acids, and amides in the extract [46]. These bands confirm the formation of PO-Fe 3 O 4 MNPs and showed that they were covered with polyphenols and other organic compounds which improved their stability.

Adsorption Process
3.2.1. Effect of pH. pH is the main factor that affects the efficacy of the adsorption process. In the present study, the impact of pH on Pb(II) and Cd(II) removal efficiency using biosynthesized PO-Fe 3 O 4 MNPs was verified at pH values ranging from 3 to 8. Pb(II) and Cd(II) adsorption was low at pH values around 3, which was attributed to electrostatic repulsion between the adsorbent and metal ions in the solution. When the concentration of hydrogen ions in the solu-tion increases, the adsorbent sites are occupied by the hydrogen ions instead of metal ions. The protonation of active sites thus tends to decrease the metal adsorption [37]. As presented in Figure 6, the removal efficiency for Pb(II) and Cd(II) at pH 3 is found to be 15.42% and 4.8%, respectively. Maximum adsorption was recorded at higher pH 6, i.e., maximum adsorptions for Pb(II) and Cd(II) were 100% and 95.32%, respectively.
Beyond the value of pH 6, solute ions will precipitate due to the formation of insoluble metal hydroxides, which then start precipitating from the solutions at higher pH values and make the true sorption studies impossible. This should be avoided during sorption tests because it makes distinguishing between sorption and metal precipitation difficult [51]. As a result, the pH value of 6 was chosen as the optimum and  [22]. The removal of Pb(II) was rapid during the first 30 min. However, no significant increase in the adsorption rate was found after 30 min. The concentration of Cd(II) decreased within 50 min and remained almost constant after an hour, implying that adsorption is rapid and reaches saturation within an hour. This is a promising result because equilibrium time is critical in wastewater treatment plants that are economically viable [53].

Effect of Initial Metal Concentration.
The effect of the initial metal concentration on the removal efficiency by 0.5 g PO-Fe 3 O 4 MNPs at optimal pH was investigated using solutions with varying initial metal concentrations (10, 50, 100, and 150 mg/L). Figure 8 shows that there is a lowering in adsorption of lead and cadmium ions with increasing in initial metal ion concentration in solution. The initial metal concentration plays an important role in the removal efficiency since there is a constant active binding site for a given mass of adsorbent where the fixed amount of metals can be adsorbed. Thus, increasing the metal concentration in solution against the same quantity of adsorbent decreases the adsorption capacity. These results agreed with the results obtained by Ebrahim et al. [35] and Das and Rebecca [54].

Effect of PO-Fe 3 O 4 MNP Dose.
The concentration of the adsorbent is one of the most important factors influencing the efficiency of the process and adsorption capacity. In this study, the impact of the various amounts of the biosynthesized PO-Fe 3 O 4 MNPs varying from 0.02 to 1.4 g was studied on the removal efficiency of the Pb(II) and Cd(II) ions. Figure 9 shows that, with increasing nanoadsorbent mass, the percentage of nanoadsorbents and the adsorption percent of both Pb(II) and Cd(II) ions increase.  This is due to the fact that at increasing dosages, there are more available sites on the surface of nanoadsorbents [55].

Adsorption
Isotherms. The adsorption isotherms provide important information concerning adsorption capacity, the adsorption mechanism between the contaminant and the adsorbent, and the contaminant distribution between the adsorbent and the solution [4]. Adsorption isotherms were determined by fitting the experimental data obtained at equilibrium time, with the isotherm models including Freundlich, Langmuir, Toth, and Khan. The Langmuir adsorption isotherm is based on monolayer adsorption on the surface and assumes a homogenous sorbent surface [39]. The Toth isotherm is an empirical modification of the Langmuir equation that is aimed at reducing the error between experimental and predicted equilibrium data. This method is especially useful for explaining systems with heterogeneous adsorption [40]. The Freundlich isotherm can be applied to adsorption processes on heterogonous surfaces; it gives the concept of multilayer adsorption and the exponential distribution of active sites on the surface of the sorbent [56]. Finally, the Khan isotherm represents both the Langmuir and Freundlich models, suggested for adsorbate adsorption from pure solutions [40].       O 4 MNPs is higher than that of most of the adsorbents listed in Table 1.
As illustrated in Figure 9, advanced adsorption removal for the lead was achieved at a low dose of PO-Fe 3 O 4 MNPs and it has a more rapid affinity towards the nanoparticles as compared to cadmium ions, which reveals the presence of various electrical attractions between cation lead metal and negative adsorption functional sites. Additionally, the lead ion possesses the smallest hydration radius; this agrees with the conception that ions with a small hydration radius are desirably selected and gathered at the interface [51,57].
3.2.6. Kinetics. The kinetics of Cd(II) and Pb(II) adsorption on PO-Fe 3 O 4 MNPs were studied using pseudo-first-order and pseudo-second-order kinetic models, as demonstrated in Figures 11 and 12. The kinetic parameters and correlation coefficients R 2 are documented in Table 3. Cd(II) and Pb(II) adsorption data were well fitted to pseudo-second-order equation (R 2 > 0:99 PbðIIÞ; 0.95 Cd(II)). Thus, chemisorption is  3.2.7. Thermodynamic Analysis. Temperature is another important factor that influences the remediation efficiency of the adsorption process. Figure 13(a) shows the variation of percentage removal efficiency with temperature. It is obvious from the results that changing the temperature from 20 to 35°C has no significant effect on the sorption of adsorbents so the adsorption experiments can be carried out at room temperature without any adjustment. Similar results were reported by Rasheed and Ebrahim [51]. However, removal efficiency decreases beyond 35°C due to a reduction in the number of active surface sites available for adsorption on the adsorbent [66]. Furthermore, at high temperatures, the attractive forces between the adsorbent and adsorbate become weaker, and therefore, sorption decreases [22].

13
Journal of Nanomaterials including Gibb's free energy (ΔG°), enthalpy (ΔH°), and entropy (ΔS°) are obtained using the following equation: ΔG°= ΔH°− TΔS°: In these equations, R is the ideal gas constant, T is the absolute temperature (K), K c is the equilibrium constant, C ad is the amount of Pb(II) and Cd(II) adsorbed on PO-Fe 3 O 4 MNPs per liter of the solution (mg/L), and C e is the equilibrium concentration of Pb(II) and Cd(II) in the solution (mg/L). The enthalpy and entropy change values were calculated from the slope and intercept of the plot of ln K c versus 1/T as shown in Figures 13(b) and 13(c). The calculated ΔG°, ΔH°, and ΔS°are arranged in Table 4. The negative values of ΔG°illustrate the spontaneity and feasibility of the adsorption reaction at a given temperature, and the increasing value of ΔG°with an increased temperature indicates a decrease in the degree of feasibility for Pb(II) and Cd(II) adsorption. To be thermodynamically acceptable, Δ G°must always be negative [21]. The negative values of Δ H°, -176.323312 for Pb(II) ions and -34.228738 kJ/mol for Cd(II) ions, show that the adsorption is exothermic. Moreover, the ΔS°values for Pb(II) and Cd(II) ions at the men-tioned temperatures are obtained as -0.51621626 and -0.09403134 kJ/mol/K, respectively. These negative values indicate reducing the irregularity or randomness in the adsorbate-adsorbent interface during Pb(II) and Cd(II) adsorption. and Cd(II) solution at optimal conditions (temperature: 20 ± 2°C, pH: 6, agitation speed: 200 rpm; equilibrium time: 60 min). The suspension was filtered using Whatman filter paper (no. 1), and the residue was dried in an oven at 50°C overnight.
The XRD patterns of Pb(II)-and Cd(II)-loaded PO-Fe 3 O 4 MNPs are shown in Figure 14. It was noted that after adsorption of Cd(II) by PO-Fe 3 O 4 MNPs, three peaks, which are centered at 32, 48, and 55°, were observed, attributed to the presence of the Cd(II) ions. In case of Pb(II) adsorption, two peaks were observed, which are centered at 31 and 48°. In addition, XRD spectra showed that there were no changes in the peaks of PO-Fe 3      The EDX analysis of PO-Fe 3 O 4 MNPs after adsorption of Cd(II) and Pb(II) is presented graphically in Figures 16(a) and 16(b). The EDX patterns show the existence of magnesium, oxygen, sulfur, iron, calcium, and cadmium on the surface of cadmium-loaded PO-Fe 3 O 4 MNPs, and the distribution of oxygen, magnesium, calcium, sulfur, iron, and lead on the surface of lead-loaded PO-Fe 3 O 4 MNPs clearly confirms successful adsorption of Pb(II) and Cd(II) on PO-Fe 3 O 4 MNP surfaces. The results show a good agreement with those obtained by Bagbi et al. [67]. The elemental mapping also confirmed the adsorption of Pb(II) (in green) and Cd(II) (in green) as shown in Figures 16(c) and 16(d). It is clear that Pb(II) and Cd(II) ions are uniformly distributed on the surface of PO-Fe 3 O 4 MNPs.

Conclusion
In this study, Portulaca oleracea leaf extract was successfully used as a reductant in PO-Fe 3 O 4 MNP synthesizing process. The biosynthesized PO-Fe 3 O 4 MNPs were characterized and used as adsorbents for the removal of Pb(II) and Cd(II) metal ions from the aqueous solution in batch adsorption system. The batch experiments showed that the removal efficiency of Pb(II) and Cd(II) by PO-Fe 3 O 4 MNPs increased with increasing pH (up to 6), contact time, and PO-Fe 3 O 4 MNP dosage. On the other hand, an increase in metal concentration and temperature resulted in reduced Pb(II) and Cd(II) removal efficiency of PO-Fe 3 O 4 MNPs. Isotherm studies revealed that the Freundlich model can properly predict adsorption equilibrium data, which indicates multilayer adsorption. The kinetic studies suggested pseudo-secondorder reactions for the adsorption, while thermodynamic studies demonstrated the adsorption as exothermic and spontaneous. This study shows that PO-Fe 3 O 4 MNPs can be considered fast, efficient, and biocompatible nanoadsorbent which have promising applications in environmental remediation processes and nanobiotechnology in the future.

Data Availability
The data sets used and analyzed during the current study are available within the article only.

Conflicts of Interest
The authors have no conflict of interest.