Removal of Cationic Organic Dye from Aqueous Solution by Chemical and Pyrolysis Activated Ulva lactuca

: Ulva lactuca has been used to remove many toxic substances from industrial wastewater. In the present study we tried to optimize the efﬁciency of U. lactuca as an adsorbent of methylene blue (MB) in aqueous solution. U. lactuca was chemically treated with sulfuric acid (UL-H) and sodium hydroxide (UL-OH) and by a slow pyrolysis process (carbonization process) at high temperature T = 600 ◦ C (UL-T) and compared to the nonactive Ulva (UL-NA) and the water insoluble substance (UL-WIS). Several spectroscopic analyses were carried out to detect the biosorption mechanisms of Ulva to remove MB in solution. The effects of different parameters on the adsorption process were studied, i.e., pH (2–10), mass concentration (1–10 g L − 1 ), and contact time (0–120 min). The results showed that the best adsorption of MB by Ulva was at pH = 8, with 5 g L − 1 of biomass at 75 min; the best adsorption capacity was 625.0 mg g − 1 for UL-OH, which was able to remove more than 89% of MB compared to UL-T, whose removal rate did not exceed 5%. Fourier-transform infrared spectroscopy (FTIR), energy-dispersive X-ray spectroscopy (EDX), and scanning electron microscopy (SEM) indicated the presence of oxygenated functional groups with a highly porous surface. The kinetic studies conﬁrmed that the majority of treatments follow the pseudo-second-order type. The mathematical models showed that Langmuir model is favorable to UL-OH, UL-WIS, and UL-NA. According to the experimental results, the primary treatment for U. lactuca is a promising environmentally friendly method and an economical strategy for removing MB from aqueous solution. This method can help address the growing demand for adsorbents used in environmental protection processes and the resultant increase in their price.


Introduction
The daily use of dyes has caused both environmental and nutritional complications. Environmental pollution is caused by the discharge of industrial wastewater due to the manufacture of plastic, paper, textiles, rubber, cosmetics, leather, food, pharmaceuticals, etc., which creates a large amount of toxic dyes, mutagens, and carcinogens. Biosorption is the most practical technique for recycling industrial wastewater rich in dyes due to its simplicity and economy [1,2]. Consequently, attention has turned to low-cost biomass, which may consist of residues that can be disposed of by other industries, e.g., peanut shells [3], rice husks [4], water hyacinth roots [5], spent bleaching earth extracted with hexane [6], nonactivated and activated date pits [7], guava seeds [8], the macroalga Sargassum muticum [9], Parthenium plants [10], bacteria and fungi [11], etc. In recent years, algae have become one of the most used sources as a disinfectant for wastewater rich in dyes and heavy metals [12,13].
In the current study, Red sea Ulva lactuca was selected to be an adsorbent of methylene blue (MB) dye due to its low-cost availability over the season and its fast blooming, which

Characterization of the Modified and Nonmodified Algae
In general, the properties and pore structure of biomass can be characterized by nitrogen adsorption, X-ray powder diffractometry (XRD), infrared spectroscopy (FTIR) and scanning electron microscopy (SEM). The specific surface area of activated carbon was determined by the Horvath-Kawazoe BET method, the DFT method, and the methylene blue adsorption method (MBAM). In this study, the following procedures were conducted.

Determination of the Specific Surface Area
The specific surface area was determined by the methylene blue adsorption method (MBAM). For this purpose, 50 mL of methylene blue solution (MB) (C0 = 5 × 10 −5 mol L −1 ) was brought into contact with 1 mg of activated and nonactivated carbon (mC). The suspension is stirred until equilibrium. Samples were taken every ten minutes to make it possible to determine the equilibrium time, and therefore the equilibrium concentration (Ce), of the residual MB solution obtained after centrifugation, by measuring the optical density at λmax. We then calculated Qm, the maximum adsorption capacity of activated carbon for MB, using Equation (1).
where Qm is the maximum carbon adsorption capacity for MB (mol·g −1 ); Co is the initial concentration of the MB solution (mol L −1 ); Ce is the equilibrium concentration of the MB solution (mol L −1 ); mC is the mass of the activated carbon (g); V is the volume of the solution (mL). The SMB specific surface area (determined using MB) [35] is calculated using Equation (2), where SMB is the specific surface area determined using MB as adsorbate (m 2 g −1 ); Qm is the maximum adsorption capacity (mol g −1 ); NA is Avogadro's constant; s is the area occupied by a molecule of MB (175 A 2 ) [36]. The characteristics of the different dry adsorbents determined are presented in Table 1.

Determination of the Specific Surface Area
The specific surface area was determined by the methylene blue adsorption method (MBAM). For this purpose, 50 mL of methylene blue solution (MB) (C 0 = 5 × 10 −5 mol L −1 ) was brought into contact with 1 mg of activated and nonactivated carbon (m C ). The suspension is stirred until equilibrium. Samples were taken every ten minutes to make it possible to determine the equilibrium time, and therefore the equilibrium concentration (Ce), of the residual MB solution obtained after centrifugation, by measuring the optical density at λmax. We then calculated Qm, the maximum adsorption capacity of activated carbon for MB, using Equation (1).
S MB = Qm. N A * s specific surface area determined by (MBAM) (2) where Qm is the maximum carbon adsorption capacity for MB (mol·g −1 ); Co is the initial concentration of the MB solution (mol L −1 ); Ce is the equilibrium concentration of the MB solution (mol L −1 ); m C is the mass of the activated carbon (g); V is the volume of the solution (mL). The S MB specific surface area (determined using MB) [35] is calculated using Equation (2), where S MB is the specific surface area determined using MB as adsorbate (m 2 g −1 ); Qm is the maximum adsorption capacity (mol g −1 ); N A is Avogadro's constant; s is the area occupied by a molecule of MB (175 A 2 ) [36]. The characteristics of the different dry adsorbents determined are presented in Table 1.

FTIR Analysis
The raw (UL-NA), water insoluble substance (UL-WIS), and activated (UL-OH, UL-H, UL-T) algae were analyzed by FTIR (Thermo spectrophotometer, Nicolet IR 200, with KBr) in order to determine the functional groups that take part in the biosorption process. Then, FTIR spectra were recorded between 4000 and 400 cm −1 .

Morphological Characteristics of the U. lactuca Surface
The morphological characterization and microanalysis of the algal biomass at different steps of the biosorption and activation process were carried out using scanning electron microscopy (SEM), equipped with an energy-dispersive X-ray spectroscopy (EDX) unit, in order to deduce any change in the modified biomass compared to raw algae. SEM and EDX were performed on a JEOL JEM−2100 electron microscope.

Study of the Biosorption Process
To evaluate the biosorption capacities of MB by the raw and modified U. lactuca species, a series of batch biosorption experiments was carried out. Note that the various parameters affecting the biosorption, namely pH, mass of adsorbent, and contact time, have already been confirmed in previous works, including El Jamal and Ncibi [37].
In a 100 mL brown glass bottle, four doses of modified or unmodified U. lactuca (0.13, 0.2, 0.26, or 0.5 g) were added to 50 mL of MB solutions of 5 × 10 −5 mol L −1 and stirred at 200 rpm at 25 ± 1 • C for 2 h, which was sufficient to reach equilibrium, in order to draw the biosorption isotherm and deduce the q max (constants that are related to the maximum adsorption capacity). The effect of pH on the biosorption rate of MB on the different biomasses of U. lactuca was studied over a wide pH range (2 to 10). For the different series, the pH of the studied solution was adjusted to the desired values by the addition of 0.1 M HCl/NaOH, and the mixtures were stirred for 120 min.
After 120 min of stirring, the various series were centrifuged at 5000 rpm for 5 min and then decanted. The decanted solution was analyzed at 664 nm, the maximum wavelength of MB, using a UV-Visible double beam spectrophotometer (Specord 200, Analytical Jena, Jena, Germany). The isothermal experiments were carried out in triplicate. The kinetic study was similarly studied by preparing several samples under the same conditions (1 mg of activated and nonactivated biomass, 50 mL of MB of fixed concentration 5 × 10 −5 mol·L −1 ). Then, 2 mL was secluded as a function of time to determine the biosorption rate constant and the order of biosorption.
The amounts of MB adsorbed per unit mass of U. lactuca at equilibrium (qe) or at time t (qt) were calculated according to the following relationships (Equations (3) and (4)).
where C 0 and Ce are the initial and equilibrium concentrations of MB (mg·L −1 ), respectively; Ct is a concentration of MB at time t; V is the volume of the adsorbate MB solution (L); m is the quantity of adsorbent used (g). The percentage of adsorbate elimination (MB) was calculated using Equation (5).

Kinetic Study of Biosorption
Between the adsorbate in the liquid phase and the adsorbent in the solid state, a thermodynamic equilibrium is reached with a speed that depends not only on the speed at which the molecules of the adsorbate diffuse into the adsorbent but also on the adsorbentadsorbate interaction, which can be chemical or physical in nature. The analysis of the temporal biosorption of an impurity on an adsorbent consists of testing the influence of the contact time on its retention. In this context, we applied four models of the kinetic study of the U. lactuca-MB pair in order to deduce the mechanism of the MB biosorption dynamics on the different modified and unmodified algae biomasses. The models studied are the pseudo-first-order model (Equation (6)) [38], the chemisorption's pseudo-second-order model (Equation (7)) [39], the intraparticle diffusion model (Equation (8)) [40], and the Elovich kinetic model (Equation (9)) [41].

Biosorption Isotherm
The objective of this study was to visualize the nature of the U. lactuca-MB interaction in order to validate models and find the optimal conditions that allow for the interpretation and prediction of MB biosorption data [42]. Note that there are several theories of isotherms, and two important isotherms were used during this study in order to determine the equilibrium parameters: Langmuir and Freundlich.
The Langmuir isotherm, being a monolayer biosorption of the adsorbate on a homogeneous surface of adsorbent, does not have transmigration of the adsorbate on the adsorbent [43,44]. The Langmuir equation is in the linearized form presented by Equation (10).
Ce/qe = 1/(q max K L ) + Ce/q max Langmuir equation (10) R L = 1/(1 + K L C i ) Separation factor (11) Log(qe) = log (K F ) + 1/n log (Ce) Freundlich isotherm (12) where Ce is the equilibrium concentration (mg·g −1 ), qe is the adsorption capacity at equilibrium (mg·g −1 ), q max (mg·g −1 ) is the maximum monolayer coverage capacity, and K L is the Langmuir isotherm constant or the biosorption rate (L·mg −1 or L·mol −1 ). By wearing the curve Ce/qe as a function of Ce, a straight line was obtained; q max and q max k L could be estimated from the slope and the intersections, respectively. One of the essential characteristics of the Langmuir isotherm can be expressed by a separation factor; R L values indicate the type of isotherm, which is defined (Equation (11)) by Weber and Chakravorti [43], where C i is the initial concentration of dye (mg· L −1 ). The value of R L indicates whether an isotherm is irreversible (R L = 0), favorable (0 < R L < 1), linear (R L = 1), or unfavorable (R L > 1).
The Freundlich isotherm is determined by Equation (12), where the Freundlich constant K F (mg·g −1 ) (L/mg) 1/n establishes the adsorption capacity of basic dye (MB) for a unit equilibrium concentration, n is the biosorption intensity, and its inverse 1/n is an empirical parameter linked to the rate of biosorption or to the heterogeneity of the surface of the adsorbent, which predicts the favorability of the non-biosorption [44]. The biosorption is considered to be favorable in the case where the value of 1/n is between 0 and 1. The latter can take the following three ranges: 1/n = 1 indicates that the distribution between the adsorbent and adsorbate is independent of the concentration; the most common range is 1/n < 1, which indicates that the dye is favorably adsorbed by the activated carbons; and 1/n > 1 indicates that biosorption is a favorable physical process, which gives greater importance to the rigid interaction between adsorbate molecules [45].

Specific Surface Area of Algal Biomass
The surface characteristics of the untreated and treated dry adsorbents used in this study are shown in Table 1.
According to the results in Table 1, different treatments permitted the development of surface micropores on the materials because treated adsorbents (UL-H, UL-OH, and UL-T) and the water insoluble substance (UL-WIS) have a higher specific surface area than the untreated adsorbent (UL-NA). The increase in the specific surface area testifies to the important modifications that took place at the level of the porous structure of these materials. These modifications are more favored in the basic treated biomass, followed by the water insoluble substance, whereas the acid treatment and the carbonized process produce less porous materials, showing a weak biosorption. Thus, UL-OH and UL-WIS have more anionic sites than UL-H, UL-T, and UL-NA, which attracted the cationic dye [46].

Functional Group Alterations Before and After Biosorption
The results of the FTIR spectral analysis are illustrated in   Table 2 for the activated and nonactivated dried U. lactuca before and after the dye biosorption.
The results give the main information on the functional groups on the surface of different treated and untreated biomasses, before and after biosorption of MB, in order to detect the possible interactions between the dyes and the functional groups of the biomasses. spectra of (UL-NA-75, UL-WIS-75, UL-H-75, UL-OH-75, and UL-T-75) after biosorption. The peaks around 3307-3399 cm −1 ( Table 2) with respect to NH/OH absorbance decreased, and a new peak appeared at 3317-3360 cm −1 as a reinforcement of the CH asymmetric vibration peaks of CH3. This change most likely corresponds to the adsorption of methylene blue on the adsorbent. This means that these two functional groups participate in the MB adsorption process. In addition, the IR spectrum shows the disappearance of absorbance at 1151-1161 cm −1 , corresponding to v(C-O-C) of carbohydrates.
The strength of the adsorption peaks at 1579-1565 cm −1 corresponding to protein amide II band, mainly δ(NH) bending and v(C-N) stretching, were absent in UL-OH and UL-T because of the denaturation of proteins in the presence of the basic medium and at high temperature [48]. Interestingly, the same band appeared strongly in UL-OH after adsorption of MB, which might be attributed to the hydrogen bond between N in MB and H of OH in UL-OH surface [53]. Furthermore, this band shifted and obviously decreased in the different treatments.
The presence and absence of 1579-1565 cm −1 band in UL-OH and UL-T before and after MB adsorption indicate that hydrogen bonds participate in the adsorption process of MB on the UL-OH surface, while the electrostatic attractions contribute to the adsorption process of MB on the UL-T surface.
Regarding the acidic activation (UL-H), acid removes the hydroxyl group in the form of H2O molecules, resulting in negative oxygen functional groups on the activated surface, which would reduce the electrons from  bond, affecting the efficiency of - between C=C or the benzyne ring of MB and the activated surface [54].
These results prove that the (-COOH), (-NH2), and (OH) groups are responsible in general for the chemical and electrostatic adsorption process of MB on the biomass surface [47,53,55].

SEM Analysis
Scanning electron micrographs were applied to different U. lactuca biomasses in order to prove external textures, morphology features, and forms. The texture of the treated and untreated surface of dry algae before and after biosorption was observed by SEM imaging ( Figure 6). The external morphology of the dry UL-NA (raw U. lactuca) exhibits a cave-like surface, which is uneven and has rough clumps and not many pores. The surface of the algae pits is moderately smooth, with fewer cracks and voids than activated carbon prepared by different chemical reagents and by carbonization treatments, which cause an irregular and rough surface that plays an important role in the biosorption of MB (Figure 6a). This is due to the chemical or physical loss of organic compounds during the activation process, confirmed by mass loss 48.0%, 58.0%, 58.4%, and 64.0% of UL-WIS, UL-H, UL-T, and UL-OH biomass, respectively. It is worth mentioning that the treatment of highest mass loss (UL-OH) has an obvious irregular and rough surface compared to the treatment of less mass loss (UL-WIS), which has relatively smooth surface (Table S1, Figure 6a). This reveals side effects, such as the degradation of cellular tissue, which can produce such a surface topology [55,56].
However, this surface modification was irregular in structure and more porous in UL-OH and UL-WIS than UL-H and UL-T. However, the acid treatment (UL-H) and that using carbonization (UL-T) were moderately smooth, with fewer cracks and voids than all other carbon compounds activated by alkaline treatment (UL-OH) and the water insoluble substance (UL-WIS). Therefore, the large surface area explains the better adsorption capacity.
After the biosorption of dye (Figure 6b), a change in bark structure is observed; it appears to have a rough pore surface because it is partially covered by dye molecules, as The infrared spectrum of nontreated dried algae (UL-NA: control) ( Figure 2) gives the number of biosorption peaks of untreated UL-NA biomass, which shows its complex nature. Thus, the spectrum shows that several functional groups, such as -OH and -NH at 3307 cm −1 , correspond to the alcohols, phenols, and carboxylic acids of cellulose and lignin, and to proteins, respectively [47]. Thus, biosorption of MB dye on algal biomass is attributed to the phenolic and acidic groups. In addition, two small peaks correspond to the aliphatic -CH in the methyl group of -CH 2 in lipids at 2958 cm −1 and 2895 cm −1 . Aromatic C=C and C=O at 1638 cm −1 correspond to protein amide I; the secondary amine group at 1579 cm −1 corresponds to protein amide II; N-H bending at 1430 cm −1 , -CH 3 bending at 1369 cm −1 , -SO 3 stretching/P=O at 1236 cm −1 , C−O−C groups of polysaccharide at 1101 cm −1 , and C−O−H groups of polysaccharide at 1048 cm −1 and 1050 cm −1 show that it is a Homogalacturonan-type polysaccharide (HG) [48]. All of the peaks indicate the presence of polysaccharides, amino acids, esters, and pectin, as confirmed by previous studies [49][50][51]. However, for the dry algae treated chemically by carbonization or solvent, we noticed a more complicated spectrum, with less intense bands and the appearance of a multitude of absorption bands in the fields of analysis. The broad band around 3307 cm −1 decreased considerably, but the peaks at 1638 cm −1 and 1048 cm  The MB spectrum shows several intense peaks at 3410 cm −1 (attributed to -NH/-OH) that correspond to the absorbance of stretch vibration, while the peak at 2928 cm −1 corresponds to the symmetrical stretch CH of the peak -CH2. The bands at 1572 cm −1 and 1442 cm −1 belong to the stretch bands of CO and CN of amide II and to the symmetrical stretching peak of carboxyl (-COOH), respectively. The intense peaks at 1140 cm −1 and 854 cm −1 correspond to the flexion band of NH and CN of amide III [52].  (Table 2) with respect to NH/OH absorbance decreased, and a new peak appeared at 3317-3360 cm −1 as a reinforcement of the CH asymmetric vibration peaks of CH 3 . This change most likely corresponds to the adsorption of methylene blue on the adsorbent. This means that these two functional groups participate in the MB adsorption process. In addition, the IR spectrum shows the disappearance of absorbance at 1151-1161 cm −1 , corresponding to v(C-O-C) of carbohydrates.
The strength of the adsorption peaks at 1579-1565 cm −1 corresponding to protein amide II band, mainly δ(NH) bending and v(C-N) stretching, were absent in UL-OH and UL-T because of the denaturation of proteins in the presence of the basic medium and at high temperature [48]. Interestingly, the same band appeared strongly in UL-OH after adsorption of MB, which might be attributed to the hydrogen bond between N in MB and H of OH in UL-OH surface [53]. Furthermore, this band shifted and obviously decreased in the different treatments.
The presence and absence of 1579-1565 cm −1 band in UL-OH and UL-T before and after MB adsorption indicate that hydrogen bonds participate in the adsorption process of MB on the UL-OH surface, while the electrostatic attractions contribute to the adsorption process of MB on the UL-T surface.
Regarding the acidic activation (UL-H), acid removes the hydroxyl group in the form of H 2 O molecules, resulting in negative oxygen functional groups on the activated surface, which would reduce the electrons from Π bond, affecting the efficiency of Π-Π between C=C or the benzyne ring of MB and the activated surface [54].
These results prove that the (-COOH), (-NH2), and (OH) groups are responsible in general for the chemical and electrostatic adsorption process of MB on the biomass surface [47,53,55].

SEM Analysis
Scanning electron micrographs were applied to different U. lactuca biomasses in order to prove external textures, morphology features, and forms. The texture of the treated and untreated surface of dry algae before and after biosorption was observed by SEM imaging ( Figure 6). The external morphology of the dry UL-NA (raw U. lactuca) exhibits a cave-like surface, which is uneven and has rough clumps and not many pores. The surface of the algae pits is moderately smooth, with fewer cracks and voids than activated carbon prepared by different chemical reagents and by carbonization treatments, which cause an irregular and rough surface that plays an important role in the biosorption of MB (Figure 6a). This is due to the chemical or physical loss of organic compounds during the activation process, confirmed by mass loss 48.0%, 58.0%, 58.4%, and 64.0% of UL-WIS, UL-H, UL-T, and UL-OH biomass, respectively. It is worth mentioning that the treatment of highest mass loss (UL-OH) has an obvious irregular and rough surface compared to the treatment of less mass loss (UL-WIS), which has relatively smooth surface (Table S1, Figure 6a). This reveals side effects, such as the degradation of cellular tissue, which can produce such a surface topology [55,56].  The values represent atom% (normalized by total atom%).

Contact Time
The inspection of MB biosorption on biomass obviously requires estimation of the contact time, defined as being the time suitable for the saturation of the adsorbent surface that corresponds to the equilibrium time leading to the end of the biosorption mechanism. In this trial, we followed a simple "batch method", which consists of putting 16 mg/L of MB in contact separately in the presence of two concentrations (low concentration 20 mg L −1 and high concentration 6 g L −1 ) of each biomass treated from dry U. lactuca. In this work, a UV-Visible spectrophotometer analysis was used to assess the residual concentrations of MB during sampling at different contact times. However, the estimation of the equilibrium time serves to describe the biosorption isotherms essential for the determination of the maximum adsorption capacity and for the visualization of the biosorption nature of the MB carried out in single or multiple layers. The results of this study show that the best contact time was 75 min for most but not all treatments at low and high concentrations (Figure 7a,b), which corresponds to a sufficient removal of the dye. At 75 min, all However, this surface modification was irregular in structure and more porous in UL-OH and UL-WIS than UL-H and UL-T. However, the acid treatment (UL-H) and that using carbonization (UL-T) were moderately smooth, with fewer cracks and voids than all other carbon compounds activated by alkaline treatment (UL-OH) and the water insoluble substance (UL-WIS). Therefore, the large surface area explains the better adsorption capacity.
After the biosorption of dye (Figure 6b), a change in bark structure is observed; it appears to have a rough pore surface because it is partially covered by dye molecules, as demonstrated by Annadurai et al. [57].
Various elements were identified from the biomass before and after the biosorption utilizing EDX analysis. The peaks of carbon, oxygen, and sulfur were recorded in the EDX spectrum (Table 3) [58].
The values represent atom% (normalized by total atom%).
However, the chemical composition of treated and nontreated carbon derived from dried U. lactuca before and after biosorption showed that the amount of C and O increased in all adsorbents, while that of Mg, Cl, K, Ca, S, and Na was found to decrease in UL-OH and UL-NA [59] and increase in UL-H, UL-WIS, and UL-T. That is, the salts that are present at the different biomasses are ionized during the adsorption operation. Therefore, their concentrations decrease, but the concentration of carbon and oxygen increases. This happens when MB interacts chemically with surface content; however, when the interaction becomes ionic exchange, the density of ions increases. This has been confirmed by [31,53,59].
Regarding the S amount, it can be clearly observed that the S amount decreases in UL-OH and UL-NA, while it increases in UL-WIS, UL-H, and UL-T. To further confirm adsorption of MB by different untreated and treated U. lactuca, SEM-EDX analyses were conducted to compare chemical composition (see Figure S2 in Supplementary material). According to these analyses, carbon and oxygen peaks are more dominant, followed by magnesium and sulfur peaks and finally calcium, potassium, sodium, and chloride peaks.
However, after MB adsorption, the main element contents (carbon and oxygen) were notably increased, whereas the content of sulfur decreased in UL-OH and UL-NA and increased in UL-WIS, UL-H and UL-T, which suggests that sulfur plays a role in the adsorption process via electrostatic between various sulfuric functional groups in biomass and MB.
Based on IR analysis, the cell wall of different biomasses before the adsorption process ( Table 2, Figures 2-5) clarified that the presence of band at (1026-1067 cm −1 ) corresponds to functional group (CSC) specific sulfated polysaccharides [60] and the vibratory band of the =N + (CH 3 )2 at (1614-1697 cm −1 ) is specific to protein amide I. These former two bands are functional groups existing in the structure of MB [61]. On the other hand, IR spectra after adsorption revealed a very noticeable increase in the adsorption band of (CSC) on the cell surface of UL-OH and UL-WIS and the disappearance of the vibratory band of =N + (CH 3 )2 in the other absorbents (UL-H, UL-NA and UL-T), which confirms the involvement of these two functional groups in the elimination of dye, which in turn leads to the increase or decrease of the sulfur amount in the biomass surface.
However, the main functional groups existing on the majority of treated and untreated U. lactuca biomasses are −OH, −C=O, −NH2 (amide) and -SO3. These results explain that MB (positive charge) interacts by means of these groups (−OH, −C=O, −NH2 (amide) and -SO3) existing on the surface of the biomass through oxygen bonds for C=O, −NH2 (UL-T, UL-H, and UL-NA) and hydrogen bonds for -SO3 (UL-OH and UL-WIS), explaining the increase and the successive decrease of sulfur. Thermodynamic explanation suggests very probably that the binding energies were the result of the physisorption process during the removal of cationic MB dyes, which corresponds well to the formation of an intermolecular electrostatic bond at the solid/liquid interface [62].
It is worth mentioning that EDX data show an inverse relationship between the amount of sulfur versus magnesium along with calcium, which sheds light on an interesting phenomena: when sulfur contributes to the adsorption process, a decrease in the sulfur amount is associated with an increase of magnesium and calcium amount, as shown in UL-NA and UL-OH (Table 3) and vice versa as clearly seen in UL-WIS, UL-H, and UL-T ( Table 3).
The results suggest that the most suitable mechanism in the biosorption process of the adsorbents UL-NA and UL-OH on MB is by chemical bonds rather than by ion exchange [53,59]; thus, in UL-WIS, UL-H, and UL-T, the mechanism in the biosorption process was probably the ion exchange type.

Contact Time
The inspection of MB biosorption on biomass obviously requires estimation of the contact time, defined as being the time suitable for the saturation of the adsorbent surface that corresponds to the equilibrium time leading to the end of the biosorption mechanism. In this trial, we followed a simple "batch method", which consists of putting 16 mg/L of MB in contact separately in the presence of two concentrations (low concentration 20 mg L −1 and high concentration 6 g L −1 ) of each biomass treated from dry U. lactuca. In this work, a UV-Visible spectrophotometer analysis was used to assess the residual concentrations of MB during sampling at different contact times. However, the estimation of the equilibrium time serves to describe the biosorption isotherms essential for the determination of the maximum adsorption capacity and for the visualization of the biosorption nature of the MB carried out in single or multiple layers. The results of this study show that the best contact time was 75 min for most but not all treatments at low and high concentrations (Figure 7a,b), which corresponds to a sufficient removal of the dye. At 75 min, all treatments at low concentration (20 mg/L) removed MB from as low as 5% (UL-T) to as high as 89% (UL-OH) (Figure 7a). For the high concentration, 6 g/L, the extracts of the dry algae eliminated 75-98% of MB at 75 min (Figure 7b). Note that extending the contact time beyond 75 min (120 min) does not lead to significant progress in the removal proportion of MB for most U. lactuca adsorbents at either a low or high concentration. This justifies using this contact time (75 min) for other biosorption experiments. It is worth mentioning that, at 75 min, the amount of U. lactuca in MB solution significantly affected the removal percentage of MB by UL-H and UL-T, as seen in Figure 7a,b. These two treatments removed only 5% at low concentration ( Figure 7a) but removed 98% at high concentration (Figure 7b), which clearly demonstrates the effect of algal biomass on the removal percentage for all treatments, especially for UL-H and UL-T. It can be clearly observed that the increase in contact time for UL-H and UL-T at low algal dose (20 mg L −1 ) increases the removal percentage of MB. This could be due to the availability of vacant functional groups on the surface of the adsorbent (Figure 7a). Further increase in contact time leads to the occupation of active sites, which results in saturation of the cell surface of the alga, causing a state of equilibrium and no additional adsorption. In comparison to previous studies, the current study detected the shortest contact time to reach equilibrium between U. lactuca and MB (Table 4).  [26] ꝉ SW, TW, dW, ddW, represent the preparation procedure of washing U. lactuca biomass to generate bio-adsorbent. SW: sea water; TW: tap water; dW: distilled water; ddW: double distilled water; RT: room temperature.
Other factors, such as algal biomass and pH, can influence the adsorption capacity, as mentioned by Karim et al. [64].

Effect of Adsorbent Dose
To examine the effect of the adsorbent of U. lactuca in removing the adsorbate (the MB dye), we varied the doses of adsorbent while keeping the MB solution constant (16 mg·L −1 ). The results obtained have been grouped in the curve in Figure 8. It can clearly be seen that, from 1 g biomass, the adsorbed quantities of MB no longer evolve for all treatments, except for UL-H and UL-T. This behavior can be illustrated with regard to the increase in the quantity of specific sites for the biosorption of MB by the variation of the dose of the adsorbents used, and this occurs up to a dose of 5 g/L. From here the number of sites becomes stable [65,66]. In contrast, Karimel at [67]. have shown that the cationic dye can easily access the biosorption sites as long as the dose of adsorbent used in the dye solution is low. However, the integration of adsorbents makes it possible to increase the number of biosorption sites to form electrostatic bonds, so at a high dose of adsorbent, the solution becomes congested, which makes it difficult for the cationic dye to approach the biosorption sites. Thus, a large dose of adsorbent causes agglomerations of particles in solution and consequently a reduction in the total biosorption surface and a reduction in  Other factors, such as algal biomass and pH, can influence the adsorption capacity, as mentioned by Karim et al. [64].

Effect of Adsorbent Dose
To examine the effect of the adsorbent of U. lactuca in removing the adsorbate (the MB dye), we varied the doses of adsorbent while keeping the MB solution constant (16 mg·L −1 ). The results obtained have been grouped in the curve in Figure 8. It can clearly be seen that, from 1 g biomass, the adsorbed quantities of MB no longer evolve for all treatments, except for UL-H and UL-T. This behavior can be illustrated with regard to the increase in the quantity of specific sites for the biosorption of MB by the variation of the dose of the adsorbents used, and this occurs up to a dose of 5 g/L. From here the number of sites becomes stable [65,66]. In contrast, Karimel at [67]. have shown that the cationic dye can easily access the biosorption sites as long as the dose of adsorbent used in the dye solution is low. However, the integration of adsorbents makes it possible to increase the number of biosorption sites to form electrostatic bonds, so at a high dose of adsorbent, the solution becomes congested, which makes it difficult for the cationic dye to approach the biosorption sites. Thus, a large dose of adsorbent causes agglomerations of particles in solution and consequently a reduction in the total biosorption surface and a reduction in the amount of adsorbate per unit of mass of adsorbent. The results obtained by Karim et al. [67] and El Sikaily et al. [27] are in agreement with our results for UL-NA, UL-WIS, and UL-OH but are contrary to the results obtained for both UL-H and UL-T [68].

Effect of pH on the Biosorption Process
The hydrogen ion concentration of the system exerted a profound influence on the complete manner of surface assimilation and in particular on the surface assimilation capacity, influencing the characteristics of the adsorbent, namely the charge of its surface, the degree of ionization in solution, and the detachment of functional groups on the active sites of the adsorbent and together with the dye in solution. In general, at high concentrations of hydrogen ions, the adsorbent favorably adsorbs the anions due to the presence of H + ions; however, at low concentrations of hydrogen ions, the MB cations are adsorbed due to the negative charges present on surface sites of the adsorbent [69].
Among the characteristics of the MB dye, it presents as a basic and cationic dye, as indicated by the existence in its structure of a positive charge on nitrogen. The effect of pH can be explained by means of the surface charge on the adsorbent. However, at low pH values (pH < 3), poor MB biosorption has been seen due to the increase in the density of positive charge (protons) at surface biomass sites. This is explained by the electrostatic repulsion that occurs between the MB cations and the positive charges on the surface of the adsorbent [27].
At a higher pH value (pH > 3), the rate of negative charge increases on the surface of the biomass, which allows for good biosorption of MB on the surface of the adsorbent. Similar results have been shown for the biosorption of MB and metals on different adsorbents [70,71]. Figure 9a-e presents the effect of the variation of pH (2, 5, 8, and 10) on the elimination of MB from aqueous solution and at different doses of U. lactuca (3, 4, 5, and 10 g/L) and when keeping the MB concentration constant (16 mg/L = 5.10 −5 mol/L). The results indicate that the initial pH of the MB mixture and the different adsorbents, in the order of 7 to 8, has been found to be favorable for the isolation of MB by all the treated and untreated biomass of U. lactuca. El Jamal and Ncibi [37] found that the favorable pH for the nonactivated green macroalga Chaetophora elegans was six. At pH values above eight, the extent of dye removal for all treatments decreases. However, at a very acidic pH (pH = 2) the percentage of adsorption of MB on the various adsorbents is low; this is most probably due to the fact that the number of positively charged sites is higher than that of negatively charged sites in medium [72] that favorably adsorbs the anion dyes but not

Effect of pH on the Biosorption Process
The hydrogen ion concentration of the system exerted a profound influence on the complete manner of surface assimilation and in particular on the surface assimilation capacity, influencing the characteristics of the adsorbent, namely the charge of its surface, the degree of ionization in solution, and the detachment of functional groups on the active sites of the adsorbent and together with the dye in solution. In general, at high concentrations of hydrogen ions, the adsorbent favorably adsorbs the anions due to the presence of H + ions; however, at low concentrations of hydrogen ions, the MB cations are adsorbed due to the negative charges present on surface sites of the adsorbent [69].
Among the characteristics of the MB dye, it presents as a basic and cationic dye, as indicated by the existence in its structure of a positive charge on nitrogen. The effect of pH can be explained by means of the surface charge on the adsorbent. However, at low pH values (pH < 3), poor MB biosorption has been seen due to the increase in the density of positive charge (protons) at surface biomass sites. This is explained by the electrostatic repulsion that occurs between the MB cations and the positive charges on the surface of the adsorbent [27].
At a higher pH value (pH > 3), the rate of negative charge increases on the surface of the biomass, which allows for good biosorption of MB on the surface of the adsorbent. Similar results have been shown for the biosorption of MB and metals on different adsorbents [70,71]. Figure 9a-e presents the effect of the variation of pH (2,5,8, and 10) on the elimination of MB from aqueous solution and at different doses of U. lactuca (3, 4, 5, and 10 g/L) and when keeping the MB concentration constant (16 mg/L = 5.10 −5 mol/L). The results indicate that the initial pH of the MB mixture and the different adsorbents, in the order of 7 to 8, has been found to be favorable for the isolation of MB by all the treated and untreated biomass of U. lactuca. El Jamal and Ncibi [37] found that the favorable pH for the nonactivated green macroalga Chaetophora elegans was six. At pH values above eight, the extent of dye removal for all treatments decreases. However, at a very acidic pH (pH = 2) the percentage of adsorption of MB on the various adsorbents is low; this is most probably due to the fact that the number of positively charged sites is higher than that of negatively charged sites in medium [72] that favorably adsorbs the anion dyes but not cationic dyes. Thus, at low pH an increase of positive charge density on biomass surface explains the elec-trostatic repulsion between cationic dyes and the positive charged site [27,69]. Furthermore, the biosorption of MB on the different adsorbents of U. lactuca could be due to the strong physical interactions (such as H-bonds) between the adsorbate molecules (MB) and various functional groups, namely hydroxyl, the carbonyl and carboxyl present in the cellulosic cell, and the lignin present in the noncellulosic cell of adsorbents of U. lactuca [66]. cationic dyes. Thus, at low pH an increase of positive charge density on biomass surface explains the electrostatic repulsion between cationic dyes and the positive charged site [27,69]. Furthermore, the biosorption of MB on the different adsorbents of U. lactuca could be due to the strong physical interactions (such as H-bonds) between the adsorbate molecules (MB) and various functional groups, namely hydroxyl, the carbonyl and carboxyl present in the cellulosic cell, and the lignin present in the noncellulosic cell of adsorbents of U. lactuca [66].
These results prove that a slightly basic pH, as a condition of natural water bodies, is a good proxy for MB removal; therefore, there was no need to change the natural value of pH for the current study's conditions. Note that, for the rest of the experiments, we adopted as a constant for all the mixtures thus prepared a pH of 8 and dose of adsorbent of 5 g L −1 . These results prove that a slightly basic pH, as a condition of natural water bodies, is a good proxy for MB removal; therefore, there was no need to change the natural value of pH for the current study's conditions. Note that, for the rest of the experiments, we adopted as a constant for all the mixtures thus prepared a pH of 8 and dose of adsorbent of 5 g L −1 .

Model of the Pseudo-First-Order Kinetics (Lagergren Model)
The mathematical treatment of Lagergren's speed equation, Equation (6), allows us to solve the expression of first-order speed and to calculate the speed constant of biosorption. However, the pseudo-first-order constants were defined by extrapolating the plot of log (qe -qt) as a function of time (t) (Figure 10a,b). The pseudo-first-order model was applied to the five adsorbents at 20 mg L −1 in order to determine the values of the adsorbed quantities, the pseudo-first-order constant K1, and the regression coefficient R 2 , which have been grouped in Table 5. The mathematical treatment of Lagergren's speed equation, Equation (6), allows us to solve the expression of first-order speed and to calculate the speed constant of biosorption. However, the pseudo-first-order constants were defined by extrapolating the plot of log (qe -qt) as a function of time (t) (Figure 10a,b). The pseudo-first-order model was applied to the five adsorbents at 20 mg L −1 in order to determine the values of the adsorbed quantities, the pseudo-first-order constant K1, and the regression coefficient R 2 , which have been grouped in Table 5.

Biosorption Dynamics Kinetics
The values of R 2 were found to be relatively low and between 0.762 and 0.806 for UL-T and UL-OH but higher than 0.9 for UL-H, UL-WIS, and UL-NA. The calculation of qe for the differently treated U. lactuca biomass shows that the quantities of MB adsorbent are high compared to the experimental quantities, except for UL-H and UL-NA, which give a close value. These facts lead us to conclude that the biosorption of MB does not reveal a process of controlled diffusion because it does not follow the pseudo-equation of the first wave given by Lagergren, except for the adsorbents UL-H and UL-NA [73].

Model of the Pseudo-Second-Order Kinetics
The pseudo-second-order kinetic model (Equation (7)) was applied to the different adsorbents of U. lactuca in order to verify the biosorption mode of MB. The results obtained are shown in Figure 11a,b. Table 5 shows the calculated values of adsorbed quantities qe2s, pseudo-second-order constant K2, and regression coefficient R 2 . Overall, it appears that the values of R 2 are high, with all in the order of 0.99, and far exceed those obtained with the pseudo-first-order model, except for UL-T (R 2 = 0.592) and UL-H (R 2 = 0.940). The biosorption capacities at equilibrium (qe2) are comparable to the theoretical values. These last two observations lead us to believe that the UL-WIS, UL-OH, and UL-NA biosorption process follows the pseudo-second-order mode.  The values of R 2 were found to be relatively low and between 0.762 and 0.806 for UL-T and UL-OH but higher than 0.9 for UL-H, UL-WIS, and UL-NA. The calculation of qe for the differently treated U. lactuca biomass shows that the quantities of MB adsorbent are high compared to the experimental quantities, except for UL-H and UL-NA, which give a close value. These facts lead us to conclude that the biosorption of MB does not reveal a process of controlled diffusion because it does not follow the pseudo-equation of the first wave given by Lagergren, except for the adsorbents UL-H and UL-NA [73].

Model of the Pseudo-Second-Order Kinetics
The pseudo-second-order kinetic model (Equation (7)) was applied to the different adsorbents of U. lactuca in order to verify the biosorption mode of MB. The results obtained are shown in Figure 11a,b. Table 5 shows the calculated values of adsorbed quantities qe 2s , pseudo-second-order constant K2, and regression coefficient R 2 . Overall, it appears that the values of R 2 are high, with all in the order of 0.99, and far exceed those obtained with the pseudo-first-order model, except for UL-T (R 2 = 0.592) and UL-H (R 2 = 0.940). The biosorption capacities at equilibrium (qe2) are comparable to the theoretical values. These last two observations lead us to believe that the UL-WIS, UL-OH, and UL-NA biosorption process follows the pseudo-second-order mode.

Intraparticle Diffusion Model
In order to verify the adaptation of the diffusion mechanisms of the different U. lactuca adsorbents, the kinetic results were analyzed using the intraparticle diffusion model. According to Weber and Morris [40], the kinetic expression of intraparticle scattering is frequently given by Equation (8). The plot of qt in terms of t 0.5 , illustrated in Figure 12a,b, gives multilinear curves for each treated biomass studied, but it does not pass through the origin. This signals that intraparticle diffusion is engaged in the biosorption process, but it is not the only mechanism applied. In addition, the y-intercept of the curves tells us the thickness of the boundary layer. However, the higher the value of the intercept, the greater the effect of the boundary layer [74,75].
The first linearity represents the instantaneous biosorption (called the biosorption phase) on the aerial surface, while the second level describes the phase of progressive biosorption-called intraparticle diffusion-that indicates the limiting phase of the biosorption mechanism. Table 5 shows the intraparticle diffusion constants (Ki1, Ki2), which are calculated using Equation (8). As expected, the diffusion rate constant (Ki1) in the first phase is more remarkable than in the second phase (Ki2), which proves that MB was first adsorbed by the external surface due to the high rate of biosorption. After the complete saturation of the external surface, the dye molecules diffuse in the internal cavities of the adsorbent to be finally adsorbed in the internal surface. However, once the MB molecules diffuse through the adsorbent, whether in the internal cavities or along the external wall, the diffusion resistance of the dye increases, and consequently there is a reduction in the diffusion rate. This results in a decrease in the diffusion rate. This phenomenon is favored for the water insoluble substance (UL-WIS (R 2 = 0.999)) and Ulva treated with sodium hydroxide (UL-OH (R 2 = 0.998)).

Intraparticle Diffusion Model
In order to verify the adaptation of the diffusion mechanisms of the different U. lactuca adsorbents, the kinetic results were analyzed using the intraparticle diffusion model. According to Weber and Morris [40], the kinetic expression of intraparticle scattering is frequently given by Equation (8). The plot of qt in terms of t 0.5 , illustrated in Figure 12a,b, gives multilinear curves for each treated biomass studied, but it does not pass through the origin. This signals that intraparticle diffusion is engaged in the biosorption process, but it is not the only mechanism applied. In addition, the y-intercept of the curves tells us the thickness of the boundary layer. However, the higher the value of the intercept, the greater the effect of the boundary layer [74,75].

Elovich's Model
Elovich's model uses a kinetic equation associated with the chemisorption process [76]. This equation (Equation (9)) is frequently used for an adsorbent system containing a heterogeneous surface (Figure 13). Table 5 indicates that the R 2 values found by the pseudo-second-order model are more important than those found by the pseudo-first-order, intraparticle diffusion, and Elovich models. These results prove that UL-WIS, UL-OH, UL-H, and UL-NA describe the kinetic model of the pseudo-second-order more precisely, whereas UL-T describes a kinetic model of the pseudo-first order with MB as the adsorbate. Likewise, the calculated (qe,calc) and experimental (qe, exp) values obtained from the pseudo-second-order model were more consistent than those found from the pseudo-first-order model.
Note that the pseudo-second-order model has been described as being the best biosorption model for cationic dyes, in preference to other adsorbents, as was investigated by Chowdhury and Saha [77], and Maurya et al. [78] who found biosorption of MB on hen feathers and the green microalga Microspora sp. The first linearity represents the instantaneous biosorption (called the biosorption phase) on the aerial surface, while the second level describes the phase of progressive biosorption-called intraparticle diffusion-that indicates the limiting phase of the biosorption mechanism. Table 5 shows the intraparticle diffusion constants (Ki1, Ki2), which are calculated using Equation (8). As expected, the diffusion rate constant (Ki1) in the first phase is more remarkable than in the second phase (Ki2), which proves that MB was first adsorbed by the external surface due to the high rate of biosorption. After the complete saturation of the external surface, the dye molecules diffuse in the internal cavities of the adsorbent to be finally adsorbed in the internal surface. However, once the MB molecules diffuse through the adsorbent, whether in the internal cavities or along the external wall, the diffusion resistance of the dye increases, and consequently there is a reduction in the diffusion rate. This results in a decrease in the diffusion rate. This phenomenon is favored for the water insoluble substance (UL-WIS (R 2 = 0.999)) and Ulva treated with sodium hydroxide (UL-OH (R 2 = 0.998)).

Elovich's Model
Elovich's model uses a kinetic equation associated with the chemisorption process [76]. This equation (Equation (9)) is frequently used for an adsorbent system containing a heterogeneous surface ( Figure 13). Table 5 indicates that the R 2 values found by the pseudo-second-order model are more important than those found by the pseudo-first-order, intraparticle diffusion, and Elovich models. These results prove that UL-WIS, UL-OH, UL-H, and UL-NA describe the kinetic model of the pseudo-second-order more precisely, whereas UL-T describes a kinetic model of the pseudo-first order with MB as the adsorbate. Likewise, the calculated (q e,calc ) and experimental (q e, exp ) values obtained from the pseudo-second-order model were more consistent than those found from the pseudo-first-order model.
Note that the pseudo-second-order model has been described as being the best biosorption model for cationic dyes, in preference to other adsorbents, as was investigated by Chowdhury and Saha [77], and Maurya et al. [78] who found biosorption of MB on hen feathers and the green microalga Microspora sp.
(qe,calc) and experimental (qe, exp) values obtained from the pseudo-second-order were more consistent than those found from the pseudo-first-order model.
Note that the pseudo-second-order model has been described as being the be sorption model for cationic dyes, in preference to other adsorbents, as was invest by Chowdhury and Saha [77], and Maurya et al. [78] who found biosorption of MB feathers and the green microalga Microspora sp.

Adsorption Isotherm
In the case of treated and untreated U. lactuca, Langmuir and Freundlich constants ( Table 6) were determined from the linearized form given by Equations (10) and (12) (Figures 14 and 15). The regression coefficients obtained by using the Langmuir model are higher for UL-OH (R 2 = 0.9985), UL-WIS (R 2 = 0.9836), and UL-NA (R 2 = 0.9789). The applicability of the Langmuir model for the MB-biomass algae system (UL-OH, UL-WIS, and UL-NA) means that the surface biosorption of MB at the adsorbent level is homogeneous. The values of q max obtained for these adsorbents are successively in the order of 625.0, 303.0, and 263.2 mg g −1 , which suggests that the Red Sea U. lactuca biomass has a very high capacity for biosorption compared to other types of plant material (Table 7). Thus, for UL-H and UL-T, we noted a lower maximum adsorption capacity, the opposite of MB (2.0 and 2.9 mg g −1 , respectively). Therefore, the biosorption processes of MB can be adapted to the treatment of water containing MB in a diluted medium.  [82] and commercial activated carbon (Merk) [54]. Thus studies must be conducted to test the effect of low concentrations of NaOH on the tion capacity of activated carbon developed from U. lactuca.  All macro-and micro-algae can be used as bio-adsorbents; however, based observations, U. lactuca is the most available alga along the Red Sea coast due to it to bear the severe environmental conditions as well as the ease of its collection amounts from the coast without effort or manpower. In addition, the obtained r the present study support the above-mentioned advantages of using U. lactuca as sorbent compared to (1) other adsorbents, (2) other biomass, or even (3) U. lactuca c The biosorption intensity between the adsorbate and the adsorbent in the Freundlich model is deduced by the coefficient 1/n, which is a value between 0 and 1 in the present study; 1/n values in Table 6 for the dried macroalga U. lactuca ranged from 0.18 to 0.65 for UL-WIS, UL-OH, and UL-NA, which indicates the favorable biosorption of the adsorbate (MB). Active dried algae in the presence of acid and carbon (UL-H and UL-T) show a high value of 1/n, ranging from 20.04 to 19.22, respectively, signaling a cooperative biosorption; this implies a strong interaction between MB molecules [79].
However, the Freundlich model admits that the isolation of the adsorbate is carried out by means of a heterogeneous adsorbent surface and can be adapted to multilayer adsorption. This is generally used to explain the adsorption properties of the heterogeneous surface [80], while the Langmuir model explains and helps with the maximum adsorption capacity, which is of the monolayer type. Thus, the monolayer adsorption occurs at particular homogenous sites on the adsorbent [81].
In this study, it can be observed in Table 6 that the base-activated carbon UL-OH prepared from U. lactuca biomass can be used as an efficient adsorbent for the adsorption of MB in aqueous solution. This result is in agreement with the result of activated carbon obtained from Ficus carica [82] and commercial activated carbon (Merk) [54]. Thus, further studies must be conducted to test the effect of low concentrations of NaOH on the adsorption capacity of activated carbon developed from U. lactuca.
All macro-and micro-algae can be used as bio-adsorbents; however, based on local observations, U. lactuca is the most available alga along the Red Sea coast due to its ability to bear the severe environmental conditions as well as the ease of its collection in large amounts from the coast without effort or manpower. In addition, the obtained results in the present study support the above-mentioned advantages of using U. lactuca as bio-adsorbent compared to (1) other adsorbents, (2) other biomass, or even (3) U. lactuca collected from other locations, as shown in Tables 4 and 7. Table 7. Adsorption capacities of adsorbents for the removal of MB based on the review of Rafatullah et al. [83].

Adsorbents
Adsorption Capacity (mg.g −1 ) References The novelty of this study can be summarized in the activation of dried U. lactuca collected from the Red Sea by different chemical and pyrolysis treatments. Most of previous studies utilized U. lactuca without activation [26][27][28][29]. The current study shows the highest adsorption capacity (625 mg/g of UL-OH) in comparison to previous studies conducted by El Nemr et al., [26], El Sikaily et al., [27] who found the adsorption capacity of U. lactuca to be 344.83 mg g −1 and 42 mg g −1 , respectively. Other researchers, such as Pratiwi et al., [28], have demonstrated that 1.25 mg g −1 removes 91.92% at a long contact time of 110 min of 25 mg L −1 MB in comparison to the current study and that nonactivated U. lactuca removed 78.44% at a concentration of 20 mg·L −1 and 75% at a concentration of 6 g·L −1 for a shorter time interval (75 min). Moreover, Vakili et al. [97] mentioned that surfaces with higher adsorption capacity require a longer time for equilibrium, indicating that larger capacity is counterbalanced by a longer treatment time and vice versa. The present study contradicts this hypothesis, as the best adsorption capacity was reached by UL-OH (625 mg g −1 ) at only 75 min. Based on these results, new hypotheses might be generated, as the treatment process of adsorbent is the main factor managing the adsorption capacity.

Conclusions
In this study, activated carbon was obtained from dry U. lactuca (UL-NA) by chemical treated with different reagents and by carbonization to obtain UL-H, UL-OH, and UL-T. Furthermore, the solubilization of dry U. lactuca (UL-NA) in double-ionized water gave a water insoluble substance (UL-WIS). However, treated or untreated biomass was adopted as a high-performance adsorbent for the isolation of MB in aqueous solutions. The success of this research can be explained by the rapid retention of MB molecules on biomass, with an optimal contact time of 75 min, thus revealing the character of an effective adsorbent specific to basic dyes and more specifically of MB in aqueous solution. In addition, the optimal values of pH and of the doses of treated and untreated biomass of U. lactuca in an aqueous solution of MB were 8 and 5 g L −1 , respectively. The kinetic model of the pseudo-second-order also justified better retention of MB on most of the treated and untreated biomasses, with the exception of UL-T, which describes a kinetic model of the pseudo-first order, with MB as the adsorbate. The Langmuir and Freundlich mathematical models explained that the biosorption parameters of MB on treated and untreated U. lactuca biomass are favorable for UL-OH, UL-WIS, and UL-NA as well as UL-H and ULT, respectively, thus indicating that the best adsorption capacity (625.0 mg g −1 ) was found for the biomass treated in solution with NaOH (UL-OH). This suggests a monolayer adsorption on an energetically homogenous surface compared to previous studies. The FTIR, EDX, and SEM studies indicate the presence of oxygenated functional groups with a high porous specific surface. However, there is a direct relationship between the rate of biosorption of MB and the quantity of the adsorbent (treated or untreated), which can be explained by the large number of unoccupied reactive cavities of U. lactuca. It is concluded from this study that the activated carbon with basic medium (UL-OH) as well as the water insoluble substance (UL-WIS) obtained from the dry U. lactuca are promising and effective adsorbents for reducing MB from aqueous solution. Thus, these can be used in the future as low-cost and promising substitutes for the biosorption of MB from industrial waters. However, further investigations must be conducted to test the efficiency of activated biomass of U. lactuca as adsorbent of other cationic, anionic heavy metals and industrial pollutants. The present study suggests combining two or more activation processes in U. lactuca biomass to investigate any improvement of U. lactuca biosorption. Based on the best adsorption capacity obtained in this study, different concentrations of alkali solution (NaOH) should be tested to explore the effect of low concentration on the activation efficiency of biomass.
Supplementary Materials: The following are available online at https://www.mdpi.com/article/ 10.3390/w13091154/s1, Figure S1: MB standard curve at pH8, Figure S2: TEM micrograph of raw dry U. lactuca (UL-NA), UL-WIS, and differently treated U. lactuca (UL-OH, UL-H, UL-T) before (a) and after 75 min of contact with methylene blue (b) at 1500 magnification. Table S1: Loss of mass of different biomass compared to the non-activated algae (UL-NA).
Author Contributions: Both authors contributed equally in this study, including experiment performance, data analyses, discussion, writing, and reviewing. All authors have read and agreed to the published version of the manuscript. Data Availability Statement: Data presented in this study are available on request from the corresponding author.