Isothermal andKinetic Investigation of Exploring the Potential of Citric Acid-Treated Trapa natans andCitrullus lanatus Peels for Biosorptive Removal of Brilliant Green Dye from Water

Trapa natans peels (TNPs) and Citrullus lanatus peels (CLPs) were utilized for the biosorptive removal of brilliant green dye (BGD), after modifying with citric acid. Characterization and surface morphology were studied by Fourier transform infrared spectroscopy and scanning electronmicroscopy. For the removal of BGD by citric acid-treated Trapa natans peels (CA-TNPs), the optimum conditions were obtained with adsorbent dose 0.8 g, contact time 25 minutes, initial pH 5, temperature 30°C, and agitation speed 100 rpm, while for the citric acid-treated Citrullus lanatus peels (CA-CLPs), adsorbent dose 0.8 g, contact time 20 minutes, pH 5, temperature 30°C, and agitation speed 100 rpm gave optimum results. )e qmax values obtained were 108.6, 128, 144.9, and 188.68mg/g for R-TNP, CA-TNP, R-CLP, and CA-CLP, respectively, while the correlation coefficient (R) values obtained were 0.985, 0.986, 0.985, and 0.998 for R-TNP, CA-TNP, R-CLP, and CA-CLP, respectively. )ese favor the Langmuir isotherm and pseudo-second-order kinetics, with negative (ΔG) values of all adsorbents, determining that the adsorption phenomenon is exothermic and spontaneous in nature. Both citric acid-treated peels of Trapa natans and Citrullus lanatus were found suitable for bulk-scale eradication of hazardous, toxic, and carcinogenic basic cationic dyes.


Introduction
ere are many natural resources in our environment, but water is a very essential constituent and has a number of conflicting demands. Highly skilled management is needed to secure our water resources and to save aquatic life and mankind. e spread of waterborne diseases through water pollution is the major cause of the worldwide death of living organisms [1]. It is reported in the literature that low-cost and efficient adsorbents such as Eugenia jambolana seeds and Citrullus lanatus peels were used for the detoxification of basic blue 9 dye from aqueous media [2]. During the dyeing and processing of fabrics, colored water is discharged into the water resources through wastewaters. It is highly problematic since even a minute amount of dye can remain highly visible [3]. In recent studies, the low-cost chemically modified Citrullus lanatus peels were used for the sorption of lead (II) and cadmium (II) ions in batch studies from wastewater. It was concluded that base-modified adsorbents were more efficient [4]. Synthetic dyes are chemical substances which are frequently used in many industrial fields such as textile, leather, printing, cosmetic, pharmaceutical, food, paper, and wool industries. From the structural point of view, dyes may be acidic, basic, azo, diazo, reactive, disperse, and complexes of metals. From the literature, it is evaluated that more than 10 5 dyes are available commercially, and according to an estimate, 9 × 10 5 of dyes are synthesized every year [5]. erefore, discharging of dyes containing wastewater into the water reservoirs causes serious water pollution which has adverse effects on mankind and aquatic life. In the modern world, water pollution is highly alarming due to the development of the abovementioned industries which generate a huge amount of dye pollutants during processing [6]. It has been observed that in the whole world that the total dye consumption is about 10 4 tons/year and approximately 10 to 15% of these dyes are discharged as effluents during dyeing processes [7]. Mostly, dyes such as brilliant green dye are aromatic in nature and easily biodegraded and release poisonous and carcinogenic products, which are harmful to humans and aquatic lives [8]. Dye effluents in wastewater affect the photosynthesis process of aquatic plants by depleting the dissolved oxygen and hindering the passage of sunlight into water bodies [9]. Based on industrial usage, generally, dyes are classified as anionic dyes (reactive dyes, acid dyes, and direct dyes) and cationic dyes (disperse dyes, nonionic dyes, and basic dyes). A toxic and carcinogenic brilliant green basic dye is extensively used in textile and printing industries. In this study, it is selected as a model dye for its adsorptive removal from wastewater [10]. Synthetic dyes such as vat dyes and disperse dyes are insoluble, while the remaining dyes are soluble in water [11]. Various conventional techniques for the removal of dye effluents from wastewater have been used, which may be biological, physical, or chemical [12]. Typical methods to treat colored water containing dye effluents have high operational and maintenance costs, so a low-profit industry cannot maintain it within its resources [13]. Hence, the treatment of industrial wastewaters containing dyes by adsorption on low-cost adsorbents is an emerging area of research and technology. Adsorption of dyes involves four major steps; first, dye particles diffuse through the solution, following further diffusion through an inner boundary layer and then into the interior of the adsorbents. Finally, molecular interactions (Van der Waals forces) bind the dye molecules on the surface of the adsorbents [14]. Trapa natans and Citrullus lanatus peels are the biosorbents selected in this research project for the detoxification of dye effluents released from industries into water bodies. e adsorption capacity for the removal of textile dyes has not been explored by chemical citric acid-modified adsorbents, which makes this a novel approach. e objectives of the present study are the utilization of Trapa natans and Citrullus lanatus peels as potential adsorbents for the removal of dyes from an aqueous solution and optimization of parameters such as temperature, pH, adsorbent dose, initial dye concentrations, and contact time. e adsorption models Langmuir, Freundlich, Temkin, pseudo-first order, and pseudo-second order will be used to check and explore the efficiency of novel chemically citric acid-modified adsorbents [15]. Trapa natans (water chestnut; water caltrop) belongs to family Trapaceae or Lythraceae [16], and Citrullus lanatus (watermelon) belongs to family Cucurbitaceae [17]. From the literature, the effect of operating parameters such as carbonization temperature and carbonization time on the adsorption phenomenon is studied [18]. It was also noted that Citrullus lanatus peels are composed of pectin, proteins, citruline, and carotenoids [19]. is study is significant for the adsorptive removal of brilliant green dye (BGD) from wastewater. It is a highly toxic cationic dye recently used in the fabric dyeing process and in printing industries [20]. Drinking water containing BGD has serious adverse effects on human health such as dermatitis and malfunctions of gastrointestinal and respiratory organs such as shortness of breath [21,22]. e structure of brilliant green dye is shown in Figure 1. e surface of both adsorbents, Trapa natans peels (TNPs) and Citrullus lanatus peels (CLPs), is composed of numerous functional groups, such as -COOH and -OH, which on deprotonation make their surfaces negatively charged. In this way, numerous negative adsorption sites on their surfaces are produced, which interact with BGD cationic molecules during adsorption in an aqueous solution. Citric acid, being a tricarboxylic acid chelating agent, enhanced the acidity of TNP and CLP, by providing additional carboxyl and hydroxyl groups. erefore, citric acid-treated Trapa natans peels (CA-TNPs) and citric acid-modified Citrullus lanatus peels (CA-CLPs) have more adsorption capacity due to the deprotonation of these additional functional groups [24]. In this study, ecofriendly and inexpensive adsorbents are used for the eradication of brilliant green dye (BGD) from water.

Preparation and Characterization of Adsorbents.
Trapa natans peels (TNPs) and Citrullus lanatus peels (CLPs) were collected from different sites of the market in Lahore, Kasur, and Multan. ese were washed subsequently with tap and distilled water and dried in sunlight.
en, these were placed in an oven at about 80°C for three days,  [23]. and afterward, the adsorbents were crushed and sieved through a 60-mesh sieve. e adsorbents were stored in plastic jars and labeled as TNP and CLP for further use during the experimental work [25]. ese were characterized by physiochemical methods [26].

Selection of Chemicals for Chemical Processing of
Adsorbents. Citric acid-treated peels of Trapa natans and Citrullus lanatus were used for the detoxification and removal of brilliant green dye (BGD) from aqueous solutions. Citric acid chemical-processed adsorbents showed better results of adsorption as compared to their raw forms during experimental work. eir efficiency was also compared with the previously reported adsorbents, elaborated in Table 1. Different chemicals (modifying agents) mentioned in Section 2.1 were also used for the chemical processing of adsorbents, but better results were obtained with citric acidmodified adsorbents (CA-TNP and CA-CLP). e chemical modification decreases the moisture content and increases the porosity and surface area of adsorbents [27]. e net charge on the surface of adsorbents was determined by the point of zero charge (pzc-pH) by acid-base titrations. If (pH > pzc-pH), then the adsorbent surface would be more negatively charged, and cations of basic dyes are readily attracted toward negatively charged adsorbent surfaces and vice versa [28,29]. In this study, brilliant green dye (BGD) was selected due to its highly toxic nature and carcinogenic effects on humans and animals. It is a basic dye, and on dissolution in an aqueous solution, it provides cations (BGD + ). ese adsorbents were also treated with different chemicals separately, such as ethanol, methanol, isopropanol, 0.1 M HCl, and 0.1 M NaOH, and some chelating agents such as urea [30], thiourea [31], EDTA [32], tartaric acid [33,34], citric acid [35][36][37], lactic acid [38], and acetone [39]. Both adsorbents were chemically processed with organic solvents (ethanol, methanol, and isopropanol) for their modifications in glass beakers covered with aluminum sheets for a period of 3 to 4 hours. Excessive soaking of each adsorbent in these organic solvents was avoided to prevent their decline and deterioration, followed by the lumping of lignocellulosic materials. en, these were filtered to get modified biosorbents. ese were dried and added to 25 mL, 25 ppm solutions of BGD separately for 15 minutes at 100 rpm to determine the final concentration of the dye after the adsorption process [40]. For solid-phase chemical modification, selected modifying chelating agents and each biosorbent were taken in a ratio of 1 : 9 by mass in a china dish. ese were mixed and irradiated with microwaves for an interval of nine (9) minutes each in a microwave oven. e scheme is elaborated in Figures 2(a) and 2(b). e resulting chemically modified products were washed with distilled water and dried at 80°C. ese were stored in plastic air-tight jars for further use in the research work. Figure 2(a) represents a schematic chemical treatment of both agrowastes with different modifying chemical agents, while a schematic proposed structure of citric acid-modified adsorbents is shown in Figure 2(b).

Optimization of Parameters.
e adsorption of BGD on R-TNP, CA-TNP, R-CLP, and CA-CLP depends on the chemical composition and available binding sites on the surface of adsorbents. To optimize the factors such as contact time, adsorbent dose, agitation speed, effect of the pH of the dye solution, temperature, and adsorption isothermal, kinetic studies were performed. e % age adsorption of BGD on each adsorbent was calculated by using the following equation: where C 0 (ppm) is the initial concentration of BGD (dye) and C e (ppm) is the adsorption at equilibrium. e quantity of dye (BGD) (mg·g −1 ) can be calculated from the following equation: where q (mg·g −1 ) is the amount of dye adsorbed by the adsorbent, V (L) is the volume of the BGD solution, and m (g) is the mass of the adsorbent [40,57].

Biosorption Experiments.
To optimize the adsorbent dose, raw adsorbents (R-TNP and R-CLP) and citric acid-

Chemical Treatment of Adsorbents.
From the comparative study, elaborated in Figure 3, it was noticed that the adsorption capacity of adsorbents (TNP and CLP) was significantly enhanced by using citric acid as a modifying agent, as discussed in Section 2.3. e novelty of this work is the chemical treatment of TNPs and CLPs with citric acid for better adsorptive removal of basic dyes (BGD) due to its chelating effect and deprotonation in aqueous media. Being a tricarboxylic acid, citric acid is an excellent chelating agent and creates more interactions due to esterification with adsorbents than other acids such as tartaric acid, lactic acid, and HCl [58]. It is interesting to note that rapid adsorption equilibrium was established by chemically modified adsorbents during the experimental work [59]. erefore, it favors the removal of BGD cations by esterification from an aqueous solution. Figure 3 revealed that citric acid chemicaltreated biosorbents showed more efficient adsorption results than other modifying agents. e solid-phase chemical    modification of adsorbents (TNP and CLP) with chemicals such as urea, thiourea, tartaric acid, citric acid, and lactic acid was carried out under microwave radiation [24]. e previously reported literature also revealed that these chemically modified biosorbents gave better results of adsorption mechanism [60,61]. e novel citric acidmodified Trapa natans and Citrullus lanatus peels were labeled as CA-TNP and CA-CLP, respectively.

Physicochemical Interpretation of Biosorbents.
e physicochemical examination of the TNP and CLP is summarized in Table 2. Adsorbents were characterized by different techniques such as Boehm titration to determine the nature of sites which may be acidic or basic, iodine titration, calculation of porosity/bulk density, moisture content, ash content, volatile matters, and pH, and elemental analysis [26].

FTIR Analysis of Adsorbents.
e FTIR spectra of both adsorbents before and after chemical treatment with citric acid are shown in Figure 4 and for the adsorption of BGD on raw adsorbents (R-TNP and R-CLP) and chemically modified adsorbents (CA-TNP and CA-CLP) are shown in Figure 5. For spectroscopic analysis, 0.6 g of each adsorbent (R-TNP, CA-TNP, R-CLP, and CA-CLP) was added to a 25 mL solution of brilliant green dye (BGD) having concentration 25 ppm. ese were agitated at 100 rpm for 25 minutes at 25°C in Erlenmeyer flasks. After filtration, the residues were washed with distilled water and evaporated to perform FTIR [62]. e FTIR spectra before and after the adsorption of BGD on unmodified (R-TNP and R-CLP) and chemically modified (CA-TNP and CA-CLP) adsorbents are shown in Figures 4 and 5, respectively.
In Figure 4(a), the spectrum of unmodified TNP is shown, where the strong band at 3250 cm −1 represents the O-H (stretching) for carboxylic acids and at 2870 cm −1 indicates the C-H (stretching) for alkanes. e peaks at 2367 cm −1 represent the adsorbed atmospheric carbon dioxide molecules. e frequency at 1430 cm −1 is a sign of O-H (bending) for carboxylic acid functional groups. e medium peak at 1339 cm −1 shows the O-H (bending) for phenol. Figure 4(b) shows the citric acid-treated TNP spectrum, which represents the new sharp peaks between wavenumbers 3850 and3600 cm −1 , for the esterification reaction between COOH groups of tricarboxylic citric acid and free O-H groups of the lignocellulosic surface of TNP. A modified peak at 2930 cm −1 indicates the C-H (stretching) for alkanes, while the region between 2200 and 2100 cm −1 represents the stretching groups of alkynes. A comparison of both spectra indicates the variations in citric acid-treated TNP compared to its raw form (R-TNP). Figure 4(c) represents the FTIR spectrum of R-CLP, in which medium peaks at 3770 to 3414 cm −1 are signs of free O-H (stretching) groups for alcohols while two strong peaks at 2960 and 2860 cm −1 represent the N-H (stretching) for amine groups. A weak band at 2100 cm −1 shows the presence of stretching groups for alkynes and at 1638 cm −1 for (stretching) alkenes. e frequency of the strong peak at 1330 cm −1 indicates the presence of C-N (stretching) for aromatic amines. Figure 4(d) represents the spectrum of citric acid-modified CLP, which is obviously different from the spectrum of R-CLP shown in Figure 4(c). A number of new peaks obtained between regions 3870 and 3730 cm −1 evidenced the esterification reaction between COOH groups of citric acid and free OH groups on the surface of the raw CLP adsorbent. e medium peaks at 2940 and 2870 cm −1 are signs of the C-H (stretching) of alkanes. e peak at 2330 cm −1 represents the atmospheric CO 2 , while the 2120 cm −1 frequency shows the monosubstituted alkynes. From the abovementioned study, it was concluded that citric acid-treated adsorbents CA-TNP and CA-CLP are different in surface morphology from their raw and untreated forms due to the reaction between acid and lignocellulosic materials of biosorbents.
FTIR spectra for adsorption of BGD on untreated and chemically citric acid-treated adsorbents are shown in Figure 5. In Figure 5(a), a few peaks ranging from 3860 to 3600 and at 3270 cm −1 indicate the interactions between BGD and free O-H groups on the surface of R-TNP. e strong broad bands at 2950 and 2822 cm −1 represent the N-H (stretching) for amines. A medium peak at 1617 cm −1 indicates the C�C (stretching) for conjugated alkene and at 1437 cm −1 indicates O-H (bending) for carboxylic acid. A strong broad peak at 1022 cm −1 shows the C-N (stretching) group for primary amines. In Figure 5(b), the additional peaks ranging from 3925 to 3600 cm −1 are associated with intermolecular hydrogen bonding between additional esterified carboxylic acid moieties on the surface of CA-TNP. e decrease in wavenumber from 2950 to 2917 cm −1 is associated with the efficient adsorption of BGD on CA-TNP compared with R-TNP. Weak peaks at 2200 cm −1 represent the presence of stretching disubstituted alkynes, and regions between 1680 and 1636 cm −1 represent the associations of C�O secondary amide with BGD molecules, while a strong, unchanged, broad peak at 1022 cm −1 was observed for the C-N (stretching) group of primary amines. In Figure 5(c), wave number ranging from 3900 to 3722 cm −1 is evidenced for free O-H association with BGD molecules on the surface of lignocellulosic materials of CLP, while strong and broad peaks at 2915 and 2848 cm −1 , as compared to R-CLP in A strong, broad peak at 1022 cm −1 shows the C-N (stretching) group for primary amines. It is evidenced from the abovementioned comparative study of FTIR spectra that citric acid-treated novel adsorbents, CA-TNP and CA-CLP, have better adsorption capacity than their untreated raw forms, R-TNP and R-CLP.
In Figure 6(a), R-TNP showed the compact arrangement of cylindrical structures having crevices, voids, and interstices, but in its citric acid chemically modified form (CA-TNP), represented in Figure 6(b), the body structures are converted into flaky with cages and wavy fibers, resulting in increased binding sites, surface area, and also, space for the adsorption of BGD. Figure 6(c) elaborates the structural chemistry of R-CLP and shows the voids and interstices between the numerous round bodies and compact spherical structures, but its chemical modification with citric acid, shown in Figure 6(d), converted it into fluffy, flakey, and wavy bodies with a number of potential binding sites for BGD adsorption. A cluster of citric acid moieties seen well on the surface of the chemically modified novel adsorbent CA-CLP evidenced numerous active binding sites for good and enhanced adsorption. Citric acid breaks and decreases the cellulose crystallinity of lignocellulosic biomass, resulting in increased porosity and surface area of TNP and CLP [66]. Total emplacement sites on the biosorbent surface can be increased by providing additional functional groups during the chemical treatment with suitable modifying agents [67,68]. us, the surface of adsorbents favors more electrostatic and hydrogen bonding interactions with the cationic molecules of BGD due to the presence of a lot of negatively active binding sites.

Optimization of Parameters.
Optimum conditions for the adsorption of BGD on R-TNP, R-CLP, CA-TNP, and CA-CLP were determined by studying the various factors and parameters such as temperature, pH, adsorption dose, contact time, and agitation speed [69].

Effect of Adsorbent Dose on Adsorption.
For the adsorption mechanism, the amount of adsorbent dose has a significant role. e high concentration of dye readily establishes the equilibrium with adsorbents and leaves many vacant adsorption sites, resulting in less removal of BGD from aqueous media. Citric acid acts as a chelating agent in CA-TNP and CA-CLP, increasing the active binding sites for more adsorption processes [59]. Hence, it was noted that BGD adsorption efficiency increases with a lower dose of adsorbent. At 30°C and 100 rpm, the optimum adsorption percentage of BGD was 73.6% on 1.4 g of R-TNP, 82% on 1.2 g of R-CLP, 96.8% on 0.8 g of CA-TNP, and 98.9% on 0.8 g of CA-CLP recorded as shown in Figure 7.

Effect of Contact Time Intervals.
Contact time duration is the major factor necessary to determine the rate of adsorption of dye on the biosorbent. Active binding sites on the biosorbent, dyestuff (cationic or anionic), and interactions between adsorbate and adsorbents determine the efficiency and rate of adsorption. With the increase in time, Journal of Chemistry the saturation of the adsorbate (BGD) on the biosorbent increases. As a result, equilibrium is established and the adsorption decreases [70]. Citric acid-modified biosorbents (CA-TNP and CA-CLP) have more active binding sites; hence, adsorption occurs more readily than unmodified biosorbents (R-TNP and R-CLP). However, with the passage of time, the dyestuffs accumulate on the biosorbents and decrease the rate of adsorption [71].

Effect of Agitation Speed on Adsorption.
It is another important factor that impacts the dye removal from aqueous solutions during the adsorption mechanism. It was observed that high rotating speed was directly related to the adsorption phenomenon due to the formation of a thin film of dye molecules from the bulk of solute (BGD). is unique external boundary of dye molecules ultimately enhanced the adsorption phenomenon. In this study, the maximum detoxification of BGD was achieved at 95.7% at 100 rpm using 0.8 g of CA-CLP and 85% at 125 rpm for R-CLP, while the adsorption of BGD was 93.6% at 100 rpm for CA-TNP and 85% at 125 rpm for R-TNP. is factor was studied using  Figure 9. At higher speed, the adsorption decreases due to the generation of overabundance centripetal power of free BGD molecules in the aqueous media. With further increase in centripetal force due to high speed, an effect of repulsion force is created on the adsorbed dye molecules on the binding sites of adsorbents, resulting in the desorption of the dye [72], as shown in Figure 9.

Effect of Temperature on Adsorption.
Temperature affects the adsorption mechanism in an exothermic or endothermic way. Change in temperature is associated with change in the kinetic energy of molecules of BGD as well as the thermodynamics of the adsorption mechanism [73]. It was observed from the literature that the adsorption phenomenon is usually exothermic and, thus, a rise in temperature decreases the rate of adsorption [74]. In Figure 10, the results of the change in temperature from 10 to 80°C are reflected. e unmodified R-TNP removed 73.6% of BGD at 50°C, whereas the citric acid-modified adsorbent CA-TNP detoxified 90.5% of BGD at 30°C. e R-CLP removed 81% of BGD at 40°C, whereas the citric acid-modified adsorbent CA-CLP showed high efficiency of removal at 94.7% BGD at 30°C. It was noted that high temperature damages the structure of the adsorbent, resulting in swelling up and allowing more penetration of dye molecules inside of it [75]. erefore, in this study, due to this reason, the adsorption in some cases increases in high temperature ranges; e.g., in R-TNP, the adsorption increases from 60 to 70°C (61% to 65%), while in R-CLP, the adsorption increases from 50 to 60°C (77.9% to 80%), as expressed in Figure 10. On the other hand, heating above 50°C adversely affects the inhibitory properties of BGD, such as its loss of antimicrobial activity, associated with decolorization at high temperature [76]. A rise in temperature during the adsorption mechanism affects    the concentration of the solution due to evaporation of water from it. During the experimental studies, the flasks were covered with aluminum foil; thus, this effect was negligible.

Effect of pH on Adsorption.
e impact of pH in the range from 1 to 10 was monitored as shown in Figure 11. e R-TNP removed 71.5% of BGD (before adsorption at pH � 7 and after adsorption at pH � 6), while the CA-TNP detoxified 92.6% of BGD (before adsorption at pH � 5 and after adsorption at pH � 4). Similarly, the second native adsorbent, R-CLP, removed 84% of BGD (before adsorption at pH � 6 and after adsorption at pH � 5), and its modified form, CA-CLP, showed high efficiency by removing 98% of BGD (before adsorption at pH � 5 and after adsorption at pH � 4.5). Both CA-TNP and CA-CLP at pH 5 showed better adsorption due to chelation between [BGD + ] and (COO − ) moieties of esterified tricarboxylic citric acid with the surface of TNP and CLP [77]. Raw adsorbents (R-TNP and R-CLP) showed the maximum adsorption at pH 7 and 6, respectively, due to the deprotonation of COOH groups, resulting in more negative adsorption sites on native adsorbents being produced for the adsorbate-adsorbent electrostatic associations. At high pH, during the equilibrium state, the excess [OH − ] ions were held with the remaining [BGD + ] ions in the solution through electrostatic forces and appear in the form of pairs. is action decreases the adsorption of adsorbate cations, at high pH values [78,79]. It was also observed during the experimental study that, at low pH, the surface of biosorbents becomes more positively charged due to the protonation of adsorption sites. e resulting excessive (H + ) ions at the interface of adsorbate-adsorbent repel the [BGD + ] ions to access the adsorption binding moieties (COOH) [80]. is phenomenon decreased the removal of BGD from the aqueous solution, as expressed in Figure 11. On the other hand, an increase in pH decreases the concentration of (H + ) ions in the solution. is process favors the more adsorption of [BGD + ] ions on negative adsorption sites (COO → ) of adsorbents with strong electrostatic interactions [9]. us, pH is an important factor. It was adjusted by adding 0.1 M NaOH or 0.1 M HCl solution for better adsorption during the experimental approach [81]. e point of zero charge (pH-PZC) of R-TNP and R-CLP is the point of isoelectronic, where the positive and negative charges of the adsorbent surface become equal [82,83]. e pH-PZC value for native Trapa natans peels was 5.8 [84], while for native Citrullus lanatus peels, it was 5.6 [85]. If pH < pH-PZC, then the adsorbent surface is positively charged and repels the cationic dye molecules, whereas if pH > pH-PZC, then the surface of adsorbents is likely to be negatively charged due to deprotonation of functional groups such as -OH and -COOH and repels the anionic dye adsorption [84,86].

Equilibrium Isothermal Studies.
From isothermal studies, the data were correlated and studied under three mathematical models: Langmuir, Freundlich, and Temkin models. ese are expressed in equations (3), (6), and (7), respectively. e optimized conditions for further study are mentioned below.
(i) Langmuir Isotherm: e linear form of the Langmuir isothermal model is represented in equation (3), while graphically effective parameters are shown in Figure 12.
where q e is the amount of dye adsorbed, C e is the remaining amount of dye in ppm after adsorption, and q m is in mg·g −1 while "b" is in L·g −1 [87]. Gibbs free energy change (ΔG 0 ) was calculated from the following equation: where "R" is the universal constant (8.3145 J·mol −1 k −1 ) and "K" is the inverse of Langmuir constant b. Figure 12 shows the comparative study of the Langmuir isothermal model for the adsorption of BGD on unmodified adsorbents (R-TNP and R-CLP) and chemically modified with citric acid adsorbents (CA-TNP and CA-CLP), whereas the effective parameters for the Langmuir isothermal model are elaborated in Table 3. e correlation coefficient (R 2 ) for the adsorption of BGD on R-TNP, CA-TNP, R-CLP, and CA-CLP is 0.9858, 0.9863, 0.9853, and 0.9982, respectively. e q max (mg·g −1 ) values for R-TNP, CA-TNP, R-CLP, and CA-CLP are 108.69, 128, 144.9, and 188.68, respectively, indicating that this model explains the adsorption of BGD in a better way for citric acidmodified adsorbents (CA-TNP and CA-CLP) than native adsorbents (R-TNP and R-CLP), as given in Table 3. By applying the relationship shown in equation (2), the separation factor (R L ) was calculated using a C value equal to 30 ppm. e values of R L < 1 also favor the adsorption phenomenon according to the Langmuir isothermal model [88]. Comparison of q m values showed better adsorption by the citric acid-modified adsorbents (CA-TNP and CA-CLP) than unmodified adsorbents (R-TNP and R-CLP). is leads to the novelty of this study.
Furthermore, q m values of all modified and unmodified adsorbents indicate a homogeneous monolayer adsorption mechanism on the fixed number of equivalent binding sites distributed on the surface of adsorbents [89].

Journal of Chemistry
(ii) Freundlich Isotherm: e linear form of this isothermal model is represented in the following equation: where "K F "(mg 1−1/n ·L 1/n ·g −1 ) is the binding constant related to the adsorption capacity and "n" is the adsorption intensity [90]. e surface heterogeneity or the adsorption capacity can be measured from 1/ n which ranges from 0 to 1. e lowest value of 1/n indicates the presence of more heterogeneity and multilayer adsorption [91]. is can also be analyzed from Figure 13. A comparison study of both of these isothermal models in Table 3 shows that the Langmuir isothermal model fits better than the Freundlich isotherm model. From FTIR analysis, citric acid-    modified adsorbents, CA-TNP and CA-CLP, have more active binding sites for the adsorption of BGD than their native adsorbents, R-TNP and R-CLP. (iii) Temkin Isotherm: e basic assumption of this isothermal model is that the heat of adsorption of adsorbate (BGD molecules) on the surface of adsorbents (R-TNP, CA-TNP, R-CLP, and CA-CLP) linearly decreases with the increase in coverage of their surfaces by dye molecules [92]. e linear form of the Temkin isothermal model is represented in equation (7) and graphically in Figure 14.
where B T � (RT/b T ) (kj·mol −1 ) is the Temkin isotherm constant which indicates the heat of adsorption during the adsorption phenomenon, while "A T " (L·g −1 ) represents the equilibrium binding constant which gives information about the maximum binding energy [93].
e abovementioned constants in this study were obtained by the comparative study of the regression analysis of linear plots of the unmodified (R-TNP and R-CLP) and citric acid-modified (CA-TNP and CA-CLP) adsorbents between "q e " and lnC e , elaborated in Figure 14. e Temkin equilibrium model of isotherm anticipated an equivalent distribution of binding energies on the surface of adsorbents due to the number of dynamic binding sites [94,95]. e heat of adsorption (B T ) is used to determine the interactions between the adsorbate and adsorbent. B T < 8 kj·mol −1 indicates weak and physical binding forces, while B T > 8 kj·mol −1 reveals strong and chemical interactions between the adsorbate and adsorbent [96,97]. From Table 3, it can be seen that the heat of adsorption (B T ) for the adsorption of BGD on unmodified adsorbents, R-TNP and R-CLP, is 2.3076 and 2.2981, respectively, whereas for novel citric acid-modified adsorbents, CA-TNP and CA-CLP, it is 2.3448 and 2.3146, respectively, which when less than 8 depict the weak binding forces, which are physical in nature. e temkin isotherm constant (B T ) reflects that citric acidmodified novel adsorbents offer more binding forces for BGD molecules than unmodified ones. e correlation coefficients (R 2 ) for the Temkin model for novel modified adsorbents are more than those for unmodified adsorbents. Hence, this model is also the best fit, like the Langmuir isotherm shown in Table 3. ese parameters indicate the physisorption instead of chemisorption and heterogeneity [98].
e abovementioned nonlinear equations were used to check the validity of the equilibrium data of isothermal models. Equation (8) was also used to calculate the root mean square errors of each adsorbent shown in Table 3. Smaller RMSE values indicated the fitness of experimental data to the calculated one for the adsorption of BGD on unmodified and modified adsorbents.
3.6.2. Kinetics Studies. e kinetics models for the adsorption of BGD on unmodified (R-TNP and R-CLP) and chemically modified with citric acid (CA-TNP and CA-CLP) adsorbents were studied using pseudo-first-order and pseudo-second-order kinetics, shown in Figures 15 and 16, respectively.
(i) Pseudo-first-order model: e linear form of pseudo-first-order kinetics is shown in equation (12) [88,100] and is graphically expressed in Figure 15.
where "k 1 " is the rate constant for the pseudo-firstorder model, q e (mg·g −1 ) is the amount of BGD taken at equilibrium, and q t (mg·g −1 ) is the amount of BGD in milligrams adsorbed on one gram of each adsorbent (adsorption of BGD on R-TNP, CA-TNP, R-CLP, and CA-CLP) at a given time per minute. From Figure 15, a linear plot between ln (q e − q t ) vs. t for the adsorption of BGD on unmodified (R-TNP and R-CLP) and citric acid-modified novel adsorbents (CA-TNP and CA-CLP) was obtained, and the pseudo-first-order parameters are displayed in Table 4. e less values of R 2 for the adsorption of BGD on each unmodified and citric acid-modified novel adsorbent indicate that the Lagergren equation (12) for the pseudo-first-order mechanism did not fit completely in a good way for the whole adsorption phenomenon. (ii) Pseudo-second-order model: For the pseudo-second-order mechanism, the linear form is given in equation (13) [69,90] and is graphically expressed in Figure 16.
In equation (13), the (K 2 ) is the rate constant for the pseudo-second-order model which is calculated using intercept. e slope obtained from the plot (t/ q t ) vs. (t) in Figure 16, gives the value of q e . e correlation coefficients (R 2 ) for the adsorption of BGD on unmodified (R-TNP and R-CLP) adsorbents are less than those on citric acid-modified novel adsorbents 14 Journal of Chemistry (CA-TNP and CA-CLP), elaborated in Table 4. R 2 values of all adsorbents reflect the high fitness of this kinetic model than the pseudo-first-order model.

Root Mean Square Error and Percent
Relative Deviation of Kinetic Models. Root mean square errors for kinetic models were calculated using equation (14) [101,102]. A  comparison of the experimental RMSE results with the calculated ones indicates the more fitting of kinetic models for the adsorption of BGD on all adsorbents. ese RMSE results calculated from equation (14) and shown in Table 4 have lesser values for second-order kinetics than the first order. is favors the high suitability of second-order kinetics for the adsorption of BGD on unmodified (R-TNP and R-CLP) and novel citric acid-modified (CA-TNP and CA-CLP) adsorbents.
where N is the number of observations performed and q t(cal) and q t(exp) are the adsorption binding capacities (mg/g) at any instant of time (t). e percent relative deviation (P) quantitatively analyses the fitness of kinetic model during adsorption process. Lower values of percent relative deviation indicate the better fitness of the kinetic model for the adsorption studies. Percent relative deviation values for the adsorption of BGD on unmodified (R-TNP and R-CLP) and novel citric acid-modified (CA-TNP and CA-CLP) adsorbents are summarized in Table 4. For second-order kinetics, the lowest values of "P" favor its fitness and suitability for the adsorption of BGD on all adsorbents than first-order kinetics. Percent relative deviation was calculated from the following equation [103]: where N is the number of total observations performed, q e(exp) is the experimental value of adsorption binding capacity, and q e (cal) is the calculated value of adsorption binding capacity in (mg/g) [104].
3.6.4. ermodynamic Approach. Figure 17 represents the comparison of thermodynamic parameters for the adsorption of BGD on unmodified adsorbents (R-TNP and R-CLP) and citric acid-modified novel adsorbents (CA-TNP and CA-CLP). e increase in temperature, directly related with the kinetic energy of brilliant green dye molecules, consequently, increases the diffusion of adsorbate (BGD) ions. is influenced and enhanced the adsorption mechanism probability due to the porous surface of lignocellulosic materials [105] (dry biomass) of R-TNP, R-CLP, CA-TNP, and CA-CLP. e Gibbs free energy (∆G 0 ), enthalpy change (∆H 0 ), and entropy of the system (∆S 0 ) are the effective thermodynamic parameters to determine the adsorption rate of BGD on unmodified and novel citric acid-modified adsorbents indicated in Table 5. e increase in negative values of Gibbs free energy with a rise in temperature determines the possibility of the adsorption process being spontaneous and exothermic at a fast rate. e higher ∆G 0 is can be calculated from the following equation [106]: where R is the general gas constant (8.314 J·mol −1 K −1 ), T is the temperature in Kelvin, and K D is the distribution coefficient which can be calculated from the following equation: e change in enthalpy determines whether the adsorption phenomenon is physical or chemical in behavior. ∆H 0 ranging from 2.1 to 20.9 kJ·mol −1 determines the physical behavior of the adsorption process [107], whereas values ranging from 80 to 200 kJ·mol −1 indicate the chemical nature [107]. is indicates that the adsorption of BGD on all adsorbents (unmodified and novel citric acid-modified adsorbent) is chemical in nature, elaborated in Table 5. e more values of ∆H 0 calculated from equation (18) favor this behavior for novel citric acid-modified adsorbents than their unmodified forms. Another important parameter, change in entropy (∆S 0 ), calculated from equation (18)    distortedness at the solid-liquid interface in this system, and its increased positive values indicate the feasibility of the adsorption phenomenon. e linear and mathematical form of Van't Hoff equation [106,108] is given as follows: From equation (18), it can be seen that a plot between "lnK D " and "1/T" gives a straight line, elaborated in Figure 17.
e slope and intercept of this line were used to calculate the values of ∆H 0 and ∆S 0 [109] for the adsorption of BGD on unmodified (R-TNP and R-CLP) and novel citric acidprocessed adsorbents (CA-TNP and CA-CLP). e higher values of ∆S 0 indicate better adsorption of BGD on novel citric acid-modified adsorbents than their unmodified forms, summarized in Table 5. Equation (19) is used to calculate the ∆H 0 and ∆S 0 [110,111]: e energy of activation was calculated from the Arrhenius equation (20) for the adsorption of BGD on R-TNP, R-CLP, CA-TNP, and CA-CLP. It is important to determine whether the process of adsorption is physically or chemically controlled. Its value ranging from5 to 40 kJ·mol −1 indicates the physical adsorption and from 40 to 800 kJ·mol −1 indicates chemical adsorption [112]. In Table 5, values of E a for the adsorption of BGD on unmodified and citric acid-modified adsorbents are summarized which indicate the physiosorption process.
where "K" is the rate constant, "A" is Arrhenius constant or frequency factor, R is universal gas constant (8.314 J·mol −1 K −1 ), T (K), and E a is the energy of activation (kJ·mol −1 ) for the adsorption of BGD and was obtained from the slope of plot between ln K and 1/T.

Chemistry of Dye Removal by Chemically Treated
Biomass. FTIR and SEM analysis indicated that native adsorbents' (TNP and CLP) surfaces are composed of carboxyl and hydroxyl groups. ese are esterified with the citric acid during the chemical modification, and they provide additional adsorption sites to adsorb the BGD cations. A schematic proposed mechanism is shown in Figure 18. Citric acid, being a tricarboxylic acid, enhanced the acidity of the adsorbents by providing excessive carboxyl and hydroxyl groups, resulting in the decrease and maintenance of the final pH of the solution. CA-TNP detoxifies 92.6% of BGD before adsorption at pH � 5 and after adsorption at pH � 4, while CA-CLP showed high efficiency of removal of 98% BGD before adsorption at pH � 5 and after adsorption at pH � 4.5, as discussed in Section 3.5.5. Citric acid also breaks and decreases the cellulose crystallinity of lignocellulosic biomass, resulting in an increase in the porosity and surface area of TNP and CLP [66]. Total emplacement sites on the biosorbent surface can be increased by providing additional functional groups during the chemical treatment with suitable modifying agents [67,68].
us, the surface of adsorbents favor more electrostatic and hydrogen bonding interactions with the cationic molecules of BGD due to the presence of a lot of negatively active binding sites on them. Hence, the citric acid chemicalprocessed Trapa natans and Citrullus lanatus peels as novel adsorbents showed more favorable, efficient, and good results during this investigation. A comparison of the adsorption efficiency of novel citric acid-modified biosorbents with that of the previously reported biosorbents is shown in Table 1.

Desorption and Regeneration of Biosorbents.
For the regeneration of adsorbents, desorption studies of used samples were carried out. Various eluents were used to investigate better and efficient results for the desorption of BGD and regeneration of TNP and CLP for their further use in adsorption. For this purpose, various concentrations of 0.01, 0.05, and 0.1 molar acidic solutions of each HCl, H 2 SO 4 , and HNO 3 , respectively, were used to provide acidic media, while various concentrations of 0.01, 0.05, and 0.1 molar basic solutions of NaOH and KOH were employed to provide basic media. It was investigated during this study that 0.1 M NaOH eluent gave the maximum desorption efficiency of 88% for BGD-R-TNP, 86.7% for BGD-R-CLP, 84% for BGD-CA-TNP, and 89.6% for BGD-CA-CLP. It was also observed that as the number of recycling experiments increases, the adsorption capacity of regenerated adsorbents decreases.

Conclusions
It was investigated experimentally that low cost, easily, and abundantly available ecofriendly chemically processed, citric acid-modified Trapa natans peels and Citrullus lanatus peels showed efficient adsorption capabilities against cationic, hazardous, and toxic model brilliant green dye, as compared to their unmodified and native forms. ese were characterized by FTIR and SEM for their surface morphology to identify the various functional groups such as -OH and -COOH and NH 2 groups. It was observed that citric acidmodified novel adsorbents have more acidic groups for better adsorption than their unmodified forms. From the comparative study of mathematical isothermal models, Langmuir, Freundlich, and Temkin, it was found, that the adsorption phenomenon was more efficiently followed by Langmuir isotherm due to high values of q max for novel citric acid chemically modified adsorbents, providing more negatively binding sites than their unmodified forms (q max for CA-TNP 128 mg·g −1 than its unmodified form R-TNP 108.6 mg·g −1 while CA-CLP 188.68 mg·g −1 than its native form R-CLP 144.9 mg·g −1 ). High regression coefficients and R 2 of Langmuir isotherm for citric acid-modified adsorbents indicate that the adsorption phenomenon is monolayer, homogeneous, and associated with chemisorption due to esterification reaction. Temkin isotherm indicates the physical behavior of adsorption process. e pseudo-second-order kinetic model fits well than the pseudo-first-order kinetic model, and negative ΔG 0 values of all adsorbents determine that the adsorption phenomenon is exothermic and spontaneous in nature. e other thermodynamic parameters, enthalpy change (∆H 0 ), entropy of the system (∆S 0 ), and energy of activation (E a ), indicated the more efficient physicochemical adsorption of BGD on novel citric acid-modified adsorbent, CA-TNP and CA-CLP, than their unmodified forms, R-TNP and R-CLP. From the adsorption efficiency and compared with the previously reported biosorbents, it is concluded that novel citric acid chemically modified Trapa natans peels and Citrullus lanatus peels have better capability to eradicate brilliant green dye from aqueous media than their native and raw forms.

Data Availability
All data related to this work are presented in the article.

Conflicts of Interest
e authors have no conflicts of interest regarding the publication of this paper.