Organotrialkoxysilane-Functionalized Prussian Blue Nanoparticles-Mediated Fluorescence Sensing of Arsenic(III)

Prussian blue nanoparticles (PBN) exhibit selective fluorescence quenching behavior with heavy metal ions; in addition, they possess characteristic oxidant properties both for liquid–liquid and liquid–solid interface catalysis. Here, we propose to study the detection and efficient removal of toxic arsenic(III) species by materializing these dual functions of PBN. A sophisticated PBN-sensitized fluorometric switching system for dosage-dependent detection of As3+ along with PBN-integrated SiO2 platforms as a column adsorbent for biphasic oxidation and elimination of As3+ have been developed. Colloidal PBN were obtained by a facile two-step process involving chemical reduction in the presence of 2-(3,4-epoxycyclohexyl)ethyl trimethoxysilane (EETMSi) and cyclohexanone as reducing agents, while heterogeneous systems were formulated via EETMSi, which triggered in situ growth of PBN inside the three-dimensional framework of silica gel and silica nanoparticles (SiO2). PBN-induced quenching of the emission signal was recorded with an As3+ concentration (0.05–1.6 ppm)-dependent fluorometric titration system, owing to the potential excitation window of PBN (at 480–500 nm), which ultimately restricts the radiative energy transfer. The detection limit for this arrangement is estimated around 0.025 ppm. Furthermore, the mesoporous and macroporous PBN-integrated SiO2 arrangements might act as stationary phase in chromatographic studies to significantly remove As3+. Besides physisorption, significant electron exchange between Fe3+/Fe2+ lattice points and As3+ ions enable complete conversion to less toxic As5+ ions with the repeated influx of mobile phase. PBN-integrated SiO2 matrices were successfully restored after segregating the target ions. This study indicates that PBN and PBN-integrated SiO2 platforms may enable straightforward and low-cost removal of arsenic from contaminated water.


Introduction
Large numbers of people in Bangladesh and India are exposed to arsenic contamination in potable water. Metallurgical, agricultural, and industrial processes result in the discharge of arsenic into soil and water [1,2]. Long-term exposure to arsenic, even at low concentrations, can lead to oncological, immunological, neurological, and endocrine effects [3]. The World Health Organization recently set an arsenic limit of 10 µg/L for drinking water (Holm, 2002) [4]. Natural water predominantly contains the inorganic species arsenate [HAsO 4 2− , As(V)] and arsenite [AsO 2 − , As(III)]. Inorganic As(III) was noted to be more toxic (10 times), mobile, and water-soluble (4-10 times) than As(V) [5]. The conversion rate of As(III) (arsenite) to As(V) (arsenate) in oxygenated water is a slow process, which depends on certain specific conditions [6]. Consequently, there is an alarming need to develop novel methods for sensing and removal of arsenic from drinking water [7].

Synthesis of PBN, PBN@SiO 2 and PBN@MSNP Mediated through EETMSi 2.2.1. EETMSi-Mediated Formation of PBN
The synthesis of PBN was accomplished using [2][3]ethyl]trimethoxysilane(EETMSi) and cyclohexanone from the single precursor potassium ferricyanide via chemical reduction. The homogeneous colloidal sol of Prussian blue nanoparticles (PBN) was prepared by adding 20 µL of EETMSi (0.1 M) to 100 µL of potassium ferricyanide (0.03 M) under stirring conditions. Subsequently, 20 µL of cyclohexanone was added to the reaction mixture; this mixture was kept in an oven at 343 K for 8 h. The blue-colored colloidal suspension of PBN was characterized byX-ray diffraction (XRD), Transmission electron micrpscopy (TEM), etc.

EETMSi-Mediated Formation of Prussian Blue Nanoparticles Modified Silica (PBN@SiO 2 )
Mesoporous silica was used to obtain PBN-confined mesoporous silica (PBN@SiO 2 ). Typical synthesis involved a multistep procedure as follows: At first, 10 mg of mesoporous silica beads were suspended in 100 mL of EETMSi (1.2 M) aqueous solution under constant stirring conditions. After 3 h, un-adsorbed EETMSi was extracted with methanol, followed by centrifugation. 200 mL of potassium ferricyanide [K 3 Fe(CN) 6 ] aqueous solution (0.03 M) was added to the alkoxysilane-modified SiO 2 suspension under vigorous stirring conditions (800 rpm). Cyclohexanone was added to the alkoxysilane-modified K 3 Fe(CN) 6 @SiO 2 suspension under vigorous stirring and left to stand in oven at 338 K overnight. The unreacted K 3 Fe(CN) 6 and unabsorbed PBN were removed via washing (five times) with methanol/water (2:1) solvent. The residual material was collected after centrifugation; a drying step was subsequently performed.

EETMSi-Mediated Formation of PBN@MSNPs
Mesoporous silica nanoparticles (MSNPs) were used to prepare Prussian blue nanoparticleembedded mesoporous silica nanoparticles (PBN@MSNP). Ten milligrams of mesoporous silica nanoparticles (average particle size 200 nm and pore size 6 nm) were suspended in 100 mL of EETMSi (1.2 M) aqueous solution under stirring conditions. After 3 h, un-adsorbed EETMSi was removed with methanol, followed by centrifugation. Two hundred milliliters of potassium ferricyanide aqueous solution (0.03 M) were added to the alkoxysilane-modified MSNP suspension under vigorous stirring conditions (800 rpm). Cyclohexanone was added to the alkoxysilane-modified K 3 Fe(CN) 6 @MSNPs suspension under continuous stirring and left to stand in oven at 338 K overnight. The unreacted K 3 Fe(CN) 6 and unabsorbed PBN were removed via washing (five times) with methanol/water (2:1) solvent. The residual material (PBN@MSNPs) was collected after centrifugation; a drying step was subsequently performed.

Materials Characterization
The particle size and morphology of as-synthesized PBN/PBN@SiO 2 and PBN@MSNP were analyzed using high-resolution transmission electron microscopy (HRTEM) with 800 and 8100 instruments (Hitachi, Tokyo, Japan) at an acceleration voltage of 200 kV. The topographical properties of as-synthesized PBN over SiO 2 were analyzed using a field emission scanning electron microscopy instrument (FEI (S.E.A.) Pte Ltd., Singapore). The elemental confirmation and mapping analyses were accomplished with an EDX attachment (Oxford Instruments plc, Abingdon, UK). A Rigaku X-ray diffractometer (Rikagu, Tokyo, Japan) with Cu Ka radiation (λ = l.5406 A 0 ) was used to evaluate diffraction data. The XRD analysis was performed over the scan range of 10-90 • for PBN. FTIR spectra were recorded on an ALFA-ATR Fourier transform infrared spectrometer (Bruker, Ettington, Germany). XPS analysis was performed using an ESCA/AES System (Surface Nano Analysis, GmbH, Berlin, Germany), which was equipped with an Al-Kα (1486.6 eV) X-ray source operating at a power of 385 W and a PHOBIOS 150 3D energy hemispherical analyzer with a delayline detector (SPECS Surface Nano Analysis GmbH, Berlin, Germany). The C-1s peak (284.5 eV) Nanomaterials 2021, 11, 1145 4 of 19 was used as an internal reference to calibrate the absolute binding energy. The quantitative detection of elements was performed through ICP techniques. Fluorescence analysis was performed using a 7100 spectrophotometer (Hitachi, Tokyo, Japan). Arsenic speciation was performed using high-performance liquid chromatography (HPLC) with a Shim-packed GIST C18 chromatography column encompassing a hydrophobic (non-polar) stationary phase (column length = 75 mm, inner diameter = 7.6 mm) for the determination of all species. Ammonium phosphate solution was used as an eluent for the entire HPLC experiment. The HPLC mobile phases of ammonium phosphate solution with pH 6.9 were prepared by mixing monobasic (NH 4 H 2 PO 4 ) and dibasic ((NH 4 ) 2 HPO 4 ) salt solutions with an appropriate ratio.

Fluorometric Method
A fluorometric method was used for the determination of As(III) species. Fluorescein (Flo) was used as a probe molecule (λex = 480 nm, λem = 510 nm) for the estimation of As(III) species. The fluorescence experiment was performed under neutral pH (6.8) conditions using Milli-Q water. Different concentrations of As(III) standard solution (10 ppm to 320 ppm) were prepared by adding appropriate amounts of sodium arsenite to Milli-Q water. The result was obtained using the effective concentration of Flo, PBN, and As(III).

Organotrialkoxysilane-Mediated Synthesis of PBN Analogs
Organotrialkoxysilane with an amine functional group, APTMS, in the presence of cyclohexanone was previously used for the controlled conversion of a single precursor, K 3 [Fe(CN) 6 , into Prussian blue nanoparticles under ambient conditions [20]. Subsequently, 2-(3,4-epoxycyclohexyl) ethyltrimethoxysilane (EETMSi) was used to make PBN in the absence of cyclohexanone [9]. Although the process enabled efficient conversion of single precursor, K 3 [Fe(CN) 6 , into Prussian blue nanoparticles, the duration was substantially longer. Accordingly, we attempted to use cyclohexanone along with EETMSi to obtain PBN from a single precursor pathway. Indeed, the process enabled the rapid formation of PBN, as shown in Figure 1; additional details on this process are provided below.

PBN as a Homogeneous Suspension
Slow decomposition under hydrothermal conditions via single precursor synthesis readily produced a blue-colored solution of PBN. The TEM micrographs in Figure 1A,B revealed well-dispersed nanocubes of PBN with an average diameter of 30 nm. The histogram (inset of Figure 1A) shows broad size distribution of crystalline nanoparticles, ranging between 27 and 53 nm. The average width of nanoparticles may be altered by modifying the EETMSi/Fe 3+ /cyclohexanone feed ratio and thermal conditions. Accordingly, we investigated the role of EETMSi in combination with a ketonic reducing agent. The EDX and TEM data provided information on the chemical composition and nanoparticle structure, respectively. Figure 1D shows the contributions to the EDX spectrum from the Fe Kα peak at 6.4-7.0 keV and 0.9 keV, the Cu peak at 7.8-9.0 keV, and the Si peak at 7.057 keV; Fe peak and the peaks for N, O, and C are also noted. The XRD spectrum shown in Figure 1E  We also attempted to insert PBN into mesoporous silica through the synergistic action of EETMSi and cyclohexanone; the product is represented as PBN@SiO 2 . Mesoporous silica with a particle size of 50 micrometers and a pore diameter of 6 nm was used for the synthetic insertion of PBN; these materials have use in column chromatography. SEM micrographs in Figure 2A-C show the topographical features of PBN@SiO 2 and the narrow size distribution of the PBN in the SiO 2 matrix. Figure 2D shows the EDX data for PBN@SiO 2 , which shows a silicon content of 31.9% elemental weight; the inset of Figure 2A shows photographic images of mesoporous SiO 2 (I) and PBN@SiO 2 (II). The XRD spectra of as-made PBN@SiO 2 and mesoporous SiO 2 are shown in Figure 2E(a-b). The results for as-made PBN@SiO 2 and mesoporous SiO 2 demonstrate a broad peak, which is assigned to the 101 plane of amorphous SiO 2 ( Figure 2E(a)); additional peaks for as-made PBN@SiO 2 are assigned to 220, 220 and 400 lattice planes of crystalline PBN. After exposure to the EETMSi-mediated PBN-laden formulation, an alteration in the SiO 2 pore size was detected via BET analysis (Table 1).

Organotrialkoxysilane-Mediated Synthesis of PBN Analogs
Organotrialkoxysilane with an amine functional group, APTMS, in the presence of cyclohexanone was previously used for the controlled conversion of a single precursor, K3[Fe(CN)6, into Prussian blue nanoparticles under ambient conditions [20]. Subsequently, 2-(3,4-epoxycyclohexyl) ethyltrimethoxysilane (EETMSi) was used to make PBN in the absence of cyclohexanone [9]. Although the process enabled efficient conversion of single precursor, K3[Fe(CN)6, into Prussian blue nanoparticles, the duration was substantially longer. Accordingly, we attempted to use cyclohexanone along with EETMSi to obtain PBN from a single precursor pathway. Indeed, the process enabled the rapid formation of PBN, as shown in Figure 1; additional details on this process are provided below. . Bar histogram displaying the particle size distribution curve of the nanoparticles (inset of Figure 1A). SAED pattern of as-synthesized particles (C), EDX profile with all the anticipated elements (D), XRD of EETMSi-functionalized PBN (E). We also undertook the synthetic incorporation of PBN within mesoporous silica nanoparticles. Silica nanoparticles (MSNP) with an average particle size of 200 nm and a pore size of 6 nm were used for this purpose. The porous nanocomposite was obtained primarily in two steps: (a) surface functionalization of the matrix by EETMSi, followed by (b) the uniform distribution of metal precursor throughout the network and subsequent reduction to form nanoscale particles. The in situ growth of PBN was pH controlled. The soluble Fe 3+ species easily adhered to the pore channels in the presence of capping agent EETMSi. The HRTEM micrograph of bare MSNPs (Figure 3a(A)) shows a porous skeleton of spherical morphology. Figure 3a(B) shows PBN inside the mesoporous silica nanoparticles (encircled in red) [26]. The selected area electron diffraction (SAED) pattern of the corresponding hybrid nanoparticle assembly (PBN@MSNP) is shown in Figure 3a(C). The zeta potential value was obtained from dynamic light scattering (DLS) data to understand the solution stability of particles. As shown in Figure 3a(D), the value of zeta potential is nearly −23 mV (i.e., towards the negative side); hence, the PBNPs are also negatively charged.

PBN-Doped Mesoporous Silica Nanoparticles (PBN@MSNP)
We also undertook the synthetic incorporation of PBN within mesoporous silica na noparticles. Silica nanoparticles (MSNP) with an average particle size of 200 nm and a pore size of 6 nm were used for this purpose. The porous nanocomposite was obtained primarily in two steps: (a) surface functionalization of the matrix by EETMSi, followed by (b) the uniform distribution of metal precursor throughout the network and subsequen reduction to form nanoscale particles. The in situ growth of PBN was pH controlled. The soluble Fe 3+ species easily adhered to the pore channels in the presence of capping agen EETMSi. The HRTEM micrograph of bare MSNPs (Figure 3a (A)) shows a porous skeleton of spherical morphology. Figure 3a (B) shows PBN inside the mesoporous silica nanopar ticles (encircled in red) [26]. The selected area electron diffraction (SAED) pattern of the corresponding hybrid nanoparticle assembly (PBN@MSNP) is shown in Figure 3a (C). The zeta potential value was obtained from dynamic light scattering (DLS) data to understand the solution stability of particles. As shown in Figure 3a (D), the value of zeta potential is nearly -23 mV (i.e., towards the negative side); hence, the PBNPs are also negatively charged. The EDX spectrum of PBN@MSNPs is shown in Figure 3a(E). The EDX mapping of the organotrialkoxysilane-functionalized PBN@MSNPs with the elemental composition of (B) carbon, (C) nitrogen, (D) oxygen (E) iron, and (F) silicon is shown in Figure 3b. The crystallographic data for as-prepared PBN@MSNPs and blank MSNPs are shown in Figure 3a

FTIR Analysis of PBN@SiO 2
The peak at 2086 cm −1 in the FTIR spectrum ( Figure 4A of PBN may be attributed to the CN stretching mode of the Fe(II)-C-N-(III)Fe moiety in PBN. The broad bands at 3402 cm −1 and 1642 cm −1 in the spectrum correspond to OH-stretching and H 2 O bending mode of the interstitial water molecule, respectively, within the PBN lattice. The strong band near 2885-2990 cm −1 corresponds to the C-H stretching vibration of sp 2 -hybridized carbon in cyclohexanone.  The EDX spectrum of PBN@MSNPs is shown in Figure 3a (E). The EDX mapping of the organotrialkoxysilane-functionalized PBN@MSNPs with the elemental composition of The peak at 2086 cm −1 in the FTIR spectrum ( Figure 4 (A) of PBN may be attributed to the CN stretching mode of the Fe(II)-C-N-(III)Fe moiety in PBN. The broad bands at 3402 cm −1 and 1642 cm −1 in the spectrum correspond to OH-stretching and H2O bending mode of the interstitial water molecule, respectively, within the PBN lattice. The strong band near 2885-2990 cm −1 corresponds to the C-H stretching vibration of sp 2 -hybridized carbon in cyclohexanone. The broad bands centered at 3548 cm −1 and at 1632 cm −1 are assigned to the stretching and bending vibrations of silanol groups (Si-OH), respectively, in the silica beads [27]. The bands at 1093 cm −1 and 801 cm −1 in the spectrum are associated with the anti-symmetric and symmetric stretching modes (Si-O-Si) of SiO4 units. The prominent peak at 2096 cm −1 (Figure 4 (B) is attributed to the stretching mode of Fe(II)-CN-(III)-Fe moiety in PBN [28] and indicates the successful formation of nanoparticles over SiO2.

Effect of the Addition of As(III) on the Fluorescent Intensity of Fluorescein
Since PBN have already been established as light quenching material, the PBN-mediated fluorescence quenching of fluorescein was evaluated. The impact of As(III) on fluorophore activity was studied via adding a different concentration of As(III) solution to a fixed Flo concentration. Subsequently, 0.01 mL of As(III) (10-320 ppm) and 10 μL of Flo solution (0.2 mM) were transferred into 2 mL of Milli-Q water and allowed to stand for 2 min at room temperature prior to fluorescence analysis. The fluorescence intensity of Flo was found to be enhanced as the function of As(III) ( Figure 5A,B). At a lower As(III) concentration, a less pronounced enhancement phenomenon was observed. This result revealed that the extent of the interaction between Flo molecule and As(III) occurred to a higher extent at a higher As(III) concentration (up to 1.5 fold). The emission intensity was found to enhanced three-fold when the concentration of As(III) was elevated from 0.05 ppm to 2 ppm (effective concentration). The broad bands centered at 3548 cm −1 and at 1632 cm −1 are assigned to the stretching and bending vibrations of silanol groups (Si-OH), respectively, in the silica beads [27]. The bands at 1093 cm −1 and 801 cm −1 in the spectrum are associated with the anti-symmetric and symmetric stretching modes (Si-O-Si) of SiO 4 units. The prominent peak at 2096 cm −1 ( Figure 4B is attributed to the stretching mode of Fe(II)-CN-(III)-Fe moiety in PBN [28] and indicates the successful formation of nanoparticles over SiO 2 .

Effect of the Addition of As(III) on the Fluorescent Intensity of Fluorescein
Since PBN have already been established as light quenching material, the PBNmediated fluorescence quenching of fluorescein was evaluated. The impact of As(III) on fluorophore activity was studied via adding a different concentration of As(III) solution to a fixed Flo concentration. Subsequently, 0.01 mL of As(III) (10-320 ppm) and 10 µL of Flo solution (0.2 mM) were transferred into 2 mL of Milli-Q water and allowed to stand for 2 min at room temperature prior to fluorescence analysis. The fluorescence intensity of Flo was found to be enhanced as the function of As(III) ( Figure 5A,B). At a lower As(III) concentration, a less pronounced enhancement phenomenon was observed. This result revealed that the extent of the interaction between Flo molecule and As(III) occurred to a higher extent at a higher As(III) concentration (up to 1.5 fold). The emission intensity was found to enhanced three-fold when the concentration of As(III) was elevated from 0.05 ppm to 2 ppm (effective concentration). PBN were employed to observe the effect of the nano-sized particles over Flo. A constant amount of PBN nanosol (0.3 mM) was added to a known concentration of Flo (0.2 mM); the mixture was allowed to stand at room temperature for 2 min. The results re-

Interaction of Fluorophore with PBN
PBN were employed to observe the effect of the nano-sized particles over Flo. A constant amount of PBN nanosol (0.3 mM) was added to a known concentration of Flo (0.2 mM); the mixture was allowed to stand at room temperature for 2 min. The results revealed that PBN quenched the fluorescence property of Flo as shown in Figure 5C. Furthermore, the effect of PBN concentration over the emission intensity of Flo was investigated. Mixtures containing various concentrations of PBN with Flo were used to understand the interaction of nanoparticles with the fluorophore. The mixtures (i) PBN (0.06 mM) with Flo (0.2 mM) and (ii) PBN (0.3 mM) with Flo (0.2 mM) were evaluated. It was shown that EETMSi functionalized PBN acted as a quencher for Flo since the intensity of the fluorophore was found to diminish in the presence of PBN ( Figure 5C). On increasing the concentration of PBN from 0.06 mM to 0.3 mM, only a small reduction in the emission intensity was observed ( Figure 5C).

Effect of As(III)/PBN System over Flo Intensity
To understand the active role of PBN over As(III) interaction, we performed two experiments. In the first experiment, different concentrations of As(III) varying from 0.05 ppm to 1.6 ppm (effective concentration) were added to the fixed content of Flo (0.3 mM); the Flo-As(III) system was then exposed to a constant amount of PBN (0.3 mM) (as shown in Figure 6). In the second experiment, PBN (0.3 mM) were initially added to the Flo solution (0.2 mM); a variable concentration of As(III) between 0.05 ppm and 1.6 ppm (effective concentration) was then added to the PBN-Flo system (Figure 7). The substantial fluorescence quenching of the Flo-As(III) system in the presence of PBN was calculated using the relation F 0 /F, where F 0 and F denote the fluorescent intensity of the Flo-As(III) system in the absence and in the presence of PBN, respectively ( Figure 8A). Similarly, the substantial fluorescence quenching of the Flo system in the presence of PBN was calculated using the relation F 0 /F, where F 0 denotes the fluorescence intensity of the Flo system in the absence of PBN and As(III), and F denotes the fluorescence intensity of Flo in the presence of PBN and As(III) ( Figure 8B).     It was observed that As(III) interacted predominately with the available quantity of the PBN moiety; the residual available As(III) was associated with the rise in emission intensity after interacting with Flo ( Figure 8C-I). The subsequent addition of PBN It was observed that As(III) interacted predominately with the available quantity of the PBN moiety; the residual available As(III) was associated with the rise in emission intensity after interacting with Flo ( Figure 8C-I). The subsequent addition of PBN achieved maximum quenching after interacting with available As(III), as displayed in Figure 8C-I. This result indicates that 0.54 mM PBN was sufficient to obtain complete interaction with 2 ppm arsenite. A similar concentration of 2 ppm of As(III) was added to the Flo-PBN system, which contained both PBN and Flo. The results ( Figure 8A-I and Figure 8B-I) showed a decrease in fluorescent intensity of Flo-As(III) and Flo as a function of PBN; PBN altered the fluorescence influencing properties of As(III). It is surmised that Prussian blue interacted with As(III) more efficiently than the Flo-As system throughout the fluorescence process. A separate experiment was performed to discover the PBN loading for complete removal of As(III) from a concentration of 2 ppm (effective concentration). For this study, primary emission spectra of Flo-As(III) were recorded while adding As(III) aqueous solution (2 ppm) to the blank solution containing Flo (0.2 Mm) only ( Figure 8C). A similar concentration of 2 ppm of As(III) was added to the Flo-PBN system, which contained both PBN.

As(III) Decontamination from Aqueous Solution Using PBN@SiO 2
The heterogeneous PBN@SiO 2 system was studied in order to understand the dynamic interaction occurring between As(III) and PBN. Accordingly, inexpensive and non-reactive silica beads were used for the modulation of active PBN in the formulation of the heterogeneous matrix. Heterogeneous methods are considered to play an influential role in catalysis due to their straightforward separation and large-scale applicability. For As(III) decontamination, the as-synthesized PBN@SiO 2 (0.05 g) was successfully packed in a column of 10 mm diameter. The standard As(III) solution (10 ppm) was prepared via adding an appropriate amount of sodium arsenite salt in Milli-Q water; 10 mL of the solution was passed through the PBN@SiO 2 enclosed column. The fluorescence analysis of separated supernatant (PBN@SiO 2 processed) was performed using Flo (0.2 mM) under similar conditions. In this study, 10 µL of as-eluted supernatants (PBN@SiO 2 processed and unprocessed As(III) solution) were added separately with Flo and left to stand at room temperature for 2 min. Their emission spectra were recorded to understand PBN@SiO 2 interactions with As(III). Unprocessed As(III) solution was observed to enhance the emission intensity of Flo many-fold ( Figure 9A) as compared to the PBN@SiO 2 processed As(III) solution ( Figure 9B). PBN@SiO 2 was shown to significantly remove the As(III) from the contaminated solution. The ICP analysis of PBN@SiO 2 processed As(III) aqueous solution was performed to quantify the arsenic concentration in the solution. The result showed 0.0018 ppm arsenic (As) content for the PBN@SiO 2 processed As(III) solution. In addition, 0.13 ppm Fe content was also detected in the processed As(III) solution. The ICP analysis indicated that some of the iron species of PBN ([Fe III [Fe II (CN) 6 ]) leached out with the eluent during interaction with the As(III) species. To investigate the presence of active iron species in the eluent, we studied the addition of ferrous sulfate with active ferrous species (Fe +2 ) to the colorless supernatant eluent. During this process, we added the ferric chloride-containing active ferric species to the colorless supernatant eluent. We observed that colorless supernatant changed immediately to an intense blue color (resembling the Prussian blue color) when ferric chloride was added. However, no such changes were observed when ferrous sulfate (containing Fe +2 ) was added.
We performed a fluorometric experiment in which supernatant (SN) was employed to observe its modulation of the Flo fluorescence properties. Fluorescent emission spectra were recorded after adding Flo (10 µL) to 10 µL of PBN@SiO 2 processed supernatant (SN). A small change in intensity (I o = 102.23) was observed with respect to the Flo (I o = 98.74) as seen in Figure 9C (1 and 2). A study that involved adding ferric chloride to the Flosupernatant (Flo-SN) mixture showed that the Flo fluorescence property was quenched (I = 31.73) when compared to Flo (I = 98.74), as shown in Figure 9C (3). Supernatant-containing ferrocyanide species had an instant interaction with the added ferric chloride, which instantly converted into PBN. Nanomaterials 2021, 11, x FOR PEER REVIEW 12 of 20 similar conditions. In this study, 10 μL of as-eluted supernatants (PBN@SiO2 processed and unprocessed As(III) solution) were added separately with Flo and left to stand at room temperature for 2 min. Their emission spectra were recorded to understand PBN@SiO2 interactions with As(III). Unprocessed As(III) solution was observed to enhance the emission intensity of Flo many-fold ( Figure 9A) as compared to the PBN@SiO2 processed As(III) solution ( Figure 9B). PBN@SiO2 was shown to significantly remove the As(III) from the contaminated solution. The ICP analysis of PBN@SiO2 processed As(III) aqueous solution was performed to quantify the arsenic concentration in the solution. The result showed 0.0018 ppm arsenic (As) content for the PBN@SiO2 processed As(III) solution. In addition, 0.13 ppm Fe content was also detected in the processed As(III) solution. The ICP analysis indicated that some of the iron species of PBN ([Fe III [Fe II (CN)6]) leached out with the eluent during interaction with the As(III) species. To investigate the presence of active iron species in the eluent, we studied the addition of ferrous sulfate with active ferrous species (Fe +2 ) to the colorless supernatant eluent. During this process, we added the ferric chloride-containing active ferric species to the colorless supernatant eluent. We observed that colorless supernatant changed immediately to an intense blue color (resembling the Prussian blue color) when ferric chloride was added. However, no such changes were observed when ferrous sulfate (containing Fe +2 ) was added.
We performed a fluorometric experiment in which supernatant (SN) was employed to observe its modulation of the Flo fluorescence properties. Fluorescent emission spectra were recorded after adding Flo (10 μL) to 10 μL of PBN@SiO2 processed supernatant (SN). A small change in intensity (Io = 102.23) was observed with respect to the Flo (Io = 98.74) as seen in Figure 9C (1 and 2). A study that involved adding ferric chloride to the Flo-supernatant (Flo-SN) mixture showed that the Flo fluorescence property was quenched (I = 31.73) when compared to Flo (I = 98.74), as shown in Figure 9C (3). Supernatant-containing ferrocyanide species had an instant interaction with the added ferric chloride, which instantly converted into PBN. To analyze the role of the residual ferrocyanide species in the supernatant over the emission spectra, a fluorescence experiment centered on the ferrocyanide concentration was conducted. We prepared and added different amounts (1 mM to 4 mM) of ferrocyanide solution to a constant amount of Flo (0.2 mM) to analyze the influence of the solution over the Flo emission intensity. Ferrocyanide acted as a weak enhancer ( Figure 9D). These results indicate that the As(III) was supposed to undergo oxidation into arsenate in the presence of PBN. The iron species in the PBN undergo reduction into Fe +2 throughout the As(III) removal process. On the addition of active ferric species to the supernatant, an immediate reaction leads to the formation of PBN after the interaction with residual ferrous species. The collected PBN@SiO 2 was characterized with XPS to observe the significance of arsenic treatment over the PBN@SiO 2 phase (as discussed in a subsequent section). Moreover, the resultant eluent was collected into separate vials and underwent HPLC analysis for the detection of arsenic species.

HPLC Results on PBN@SiO 2 Treated Arsenic(III)
All the separated species were noted in the ion-chromatogram at their respective retention time such as arsenobetaine (AsB) at 2.17/2.42/2.55 min, dimethylarsinic acid (DMA) at 3.57 min, As(III) at 3.8/3.9 min, and As(V) at 7.7 min. The chromatogram shown in Figure 10A-D was obtained as the result of HPLC separation of the arsenic species after treatment with PBN@SiO 2 at different pH values (2.2-8.5). HPLC analysis illustrates that the removal efficiency of As(III) (( Figure 10A) by PBN@SiO 2 increased from 33.52% ( Figure 10B) to 59.90% ( Figure 10C) with a pH increase from 2 to 6.5; this improved to 95.13% ( Figure 10D) under a mild alkaline condition (pH-8.5). The ion chromatogram results also showed an insignificant peak at a retention time of 7.35 min ((Area% = 1.4) at pH = 6.5 and (Area% = 9.09) at pH = 8.5), which was associated with leaching of As(V) in an aqueous solution during the oxidation-adsorption process. All of the arsenic species (As(III), DMA, AsB) identified at various retention times along with their relative concentration in a HPLC environment are shown in Table 2.               AsB, which frequently existed in the zwitterionic form due to the interaction between the positively charged arsenic and the negatively charged carboxylic group, starts to migrate immediately after interacting with the hydrophobic C18 Shim-pack column. However, As(III) is a neutral species (pKa = 9.2) up to a pH of 8, which eluents slowly with the solvent front. Consequently, negatively charged DMA and As(V) species feasibly eluent by a variety of interactions (e.g., H bonding and ion-exchange) along with hydrophobic effects. The obtained result was acquired after a total run time of 25 min and repeated twice to minimize the experimental error. After peak fitting, the spectrum can be de-convolved into three peaks. Figure 10E shows the XPS peaks centered on binding energies of 721.27 and 708.34 eV for Fe 2p 1/2 and Fe 2p 3/2 , respectively; these features are characteristic of the Fe +2 moiety in Prussian blue.
In addition, a spectrum shows a peak at a binding energy of 712.12 eV, which corresponds to Fe +3 species. The position of these peaks is in good agreement with the results in the literature for the characteristic Fe +3 and Fe +2 components of Prussian blue compounds [30].

As(III)-PBN@SiO 2 and As(V)-PBN@SiO 2
The cation As(III) and the oxidized species As(V) detected on the PBN@SiO 2 substrate with XPS after a decontamination process are shown in Figure 11. The binding energy values (in eV) for O (1s), Si (2p), Fe (2p), and N (1s) in PBN@SiO 2 and As-PBN@SiO 2 are listed in Table 3. The XPS survey scan as shown in Figure 11D shows peaks at a binding energy of 49.03 eV, which are associated with the presence of As(V) and indicate the successful sorption of As(V) by PBN@SiO 2 [31]. The other peak located at 43.23 eV is associated with the adsorption of As(III) over SiO 2 prior to the oxidation process [32]. However, the peak positions observed for the Fe +3 and Fe +2 core level (2p) spectra of PBN@SiO 2 are shifted slightly to a lower binding energy relative to the unreacted and unabsorbed PBN@SiO 2 species. This shift in the peaks for Fe 2+ 2p 3/2 (binding energy of 708.19 eV) and Fe 2+ 2p 1/2 (binding energy of 721.42 eV) may be attributed to arsenic adsorption [33]. The shift in the peak position (with a reduction in intensity) of Fe +3 2p 3/2 (binding energy of 712.86 eV) relative to pure PBN@SiO 2 suggests the reduction of the material during arsenic oxidation [34]. The position of the characteristic peak of Fe +2 (binding energy of 55.04 eV, 3p) remained unchanged throughout the As(III) oxidation and adsorption process [31]. A peak emerged at a binding energy of 398.99 eV, which was attributed to the presence of nitrogen in the environment. Alterations in the peak position of PBN@SiO 2 relative to that of As-PBN@SiO 2 were associated with chemical adsorption by PBN@SiO 2 of arsenic species.

Effect of pH on Arsenic Removal
The results in Figure 10 illustrate the effects of pH on the removal of As(III) u PBN@SiO2. As can be observed, As(III) removal was dependent on pH; the greate moval efficiency occurred under moderate pH (pH = 6-9) and was found to dimin highly acidic pH (pH < 3). As reported earlier, surfaces of silica beads were posit charged in highly acidic conditions and acquired a negative charge in the pH range 10 [35]. Subsequently, moderate pH was found to be favorable for a sorbent surface decreased protonation is supposed to enlarge the attraction force between the negat

Effect of pH on Arsenic Removal
The results in Figure 10 illustrate the effects of pH on the removal of As(III) using PBN@SiO 2 . As can be observed, As(III) removal was dependent on pH; the greatest removal efficiency occurred under moderate pH (pH = 6-9) and was found to diminish at highly acidic pH (pH < 3). As reported earlier, surfaces of silica beads were positively charged in highly acidic conditions and acquired a negative charge in the pH range of 3-10 [35]. Subsequently, moderate pH was found to be favorable for a sorbent surface since decreased protonation is supposed to enlarge the attraction force between the negatively charged PBN@SiO 2 surface and the positively charged As(III) cationic species. This result is similar to earlier findings by Gupta et al. who reported a significant increase in As(III) adsorption onto iron oxide-coated quartz sand with an increase in pH from 4.5 to 7.5 [36]. At a highly acidic pH (<3), repulsion occurred between the positively charged adsorbent sites and the adsorbate species (As +3 ), which prevented the adsorption and arsenic oxidation processes. No substantial rise in As(III) removal efficiency was observed with an elevation in pH.

Analysis of PBN@SiO 2 Surface through SEM-EDX after As(III) Remediation
After the As(III) removal process, the PBN@SiO 2 surface was analyzed using SEM. The result showed the change in morphology of PBN (cubic to spherical) after arsenic interaction ( Figure 11E). The EDX results suggest that the material is comprised of an inner SiO 2 chemistry and an outer ferric hexacyanoferrate (Fe +3 [Fe +2 (CN) 6 ]) chemistry, with some As(III) enrichment over the PBN@SiO 2 surface. The presence of the anticipated elements was confirmed through EDX analysis.

Recyclability and Proposed Mechanism
It has been well established that Prussian blue is comprised of Fe metal in Fe +2 (low spin) and Fe +3 (high spin) states, which are linked via CN bridges. Prussian blue can undergo reduction to what is known as Prussian white (Fe II -C≡N-Fe II ) or oxidation to what is known as Prussian yellow (Fe III -C≡N-Fe III ) [37,38]. Reduction of Prussian blue to Prussian white on the surface of silica gel was found to facilitate the As(III) oxidation to As(V) and their subsequent removal. Conversion of Fe 3+ to Fe +2 was shown during the decontamination in PBN and validate the altered chemical environment due to arsenic interactions. The addition of ferric chloride to the white-blue colored arsenite-treated PBN@SiO 2 residue instantly generated a blue color; this phenomenon is attributed to the conversion of hexacyanoferrate Fe II (CN) 6 species of K 2 [Fe II Fe II (CN) 6 ] into Prussian blue K[Fe III Fe II (CN) 6 ) through the interaction with ferric species (ferric chloride). The reaction during Prussian blue synthesis has been shown as: The variation of surface charge of SiO 2 with a change in pH was found to be the fundamental framework for PBN activity over the course of arsenic removal.

Mechanism of PBN Based Fluorescence Sensing of As(III)
The findings as shown in Figures 4-6  The intervalence transition may be evaluated based on changes to the absorption spectrum. The fluorescein-PBN interaction is associated with fluorescence resonance energy transfer as recently described [39,40]; this material is capable of quenching the emitted fluorescence of fluorescein. When PBN undergo interaction with As(III), there is a conversion of PBN into Prussian white nanoparticles, followed by a conversion of As(III) to As(V); thus, the quenching ability is lost. The Prussian white nanoparticles can further be converted into PBN after treating the same with acid as discussed above. This scheme provides an effective and inexpensive method for PBN-mediated removal of As(III) udermvisible light.

Characterization of Recyclable PBN@SiO 2
After arsenic elimination, the recycled PBN@SiO 2 was investigated with XRD, SEM, and FTIR to understand the effect of the recycling process on PBN@SiO 2 morphology, size, and crystallinity. An SEM image of the recycled PBN@SiO 2 is shown in Figure 12. More spherical-shaped than cube-shaped particles were observed; the aggregation of PBN with no precise shape was also observed. XRD analysis demonstrated a shifting inward of the peak position (θ) as compared with the unused PBN@SiO 2 . The presence of anticipated elements was identified via EDX analysis. In addition, characteristic CN stretching in PBN was noted; this feature was noted at a considerably lower wavenumber (2054 cm −1 ), which is attributed to particle aggregation [39]. The PBN characteristics before and after the recycling process as obtained from XRD, SEM, and FTIR analysis are listed in Table 4. spherical-shaped than cube-shaped particles were observed; the aggregation of PBN with no precise shape was also observed. XRD analysis demonstrated a shifting inward of the peak position (θ) as compared with the unused PBN@SiO2. The presence of anticipated elements was identified via EDX analysis. In addition, characteristic CN stretching in PBN was noted; this feature was noted at a considerably lower wavenumber (2054 cm −1 ), which is attributed to particle aggregation [39]. The PBN characteristics before and after the recycling process as obtained from XRD, SEM, and FTIR analysis are listed in Table 4.

Conclusions
PBN are a light-sensitive material that is processed through functional alkoxysilaneand cyclohexanone-mediated conversion of a single precursor, potassium hexacyanoferrate. The synthetic incorporation of PBN within mesoporous silica (PBN@SiO2) was also studied; the morphology of these particles was characterized using TEM, SEM, XRD, and XPS. The as-made PBN were studied as a fluorescent quencher. The quenching ability of the materials is found to be a function of arsenic (III) concentration; this result suggested a novel application of PBN for fluorescence sensing of arsenic. In addition, XPS studies confirmed that arsenic is adsorbed on PBN@SiO2 as arsenite (As(III)) and arsenate (As (V)) irrespective of the initial oxidation state of the material; this result indicated a novel application of PBN for the removal of arsenic (III) from a given sample.

Conclusions
PBN are a light-sensitive material that is processed through functional alkoxysilaneand cyclohexanone-mediated conversion of a single precursor, potassium hexacyanoferrate. The synthetic incorporation of PBN within mesoporous silica (PBN@SiO 2 ) was also studied; the morphology of these particles was characterized using TEM, SEM, XRD, and XPS. The as-made PBN were studied as a fluorescent quencher. The quenching ability of the materials is found to be a function of arsenic(III) concentration; this result suggested a novel application of PBN for fluorescence sensing of arsenic. In addition, XPS studies confirmed that arsenic is adsorbed on PBN@SiO 2 as arsenite (As(III)) and arsenate (As(V)) irrespective of the initial oxidation state of the material; this result indicated a novel application of PBN for the removal of arsenic(III) from a given sample.