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Article

Reproducible Design for the Optical Screening and Sensing of Hg(II) Ions

by
Emad A. Elshehy
1,†,
Sherif A. EL-Safty
1,2,* and
Mohamed A. Shenashen
1,‡
1
National Institute for Materials Science (NIMS), 1-2-1 Sengen, Tsukuba-shi, Ibaraki-ken 305-0047, Japan
2
Graduate School for Advanced Science and Engineering, Waseda University, 3-4-1 Okubo, Shinjuku-ku, Tokyo 169-8555, Japan
*
Author to whom correspondence should be addressed.
†
Permanent address: Nuclear Materials Authority, El Maadi, Cairo, Egypt.
‡
Permanent address: Egyptian Petroleum Research Institute (EPRI), Nasr City, Cairo, Egypt.
Chemosensors 2014, 2(4), 219-234; https://doi.org/10.3390/chemosensors2040219
Submission received: 1 April 2014 / Revised: 22 September 2014 / Accepted: 25 September 2014 / Published: 24 October 2014
(This article belongs to the Special Issue Nanosensors)
Browse Figures
Versions Notes

Abstract

:
We fabricated silica nanotubes with hexagonally ordered mesopores (6 nm) inside a membrane disc with a uniform channel neck size of 200 nm and a longitudinal thickness of 60 μm to design an optical sensor membrane (OSM) for the screening and sensing of extremely toxic Hg(II) ions. The optical detection and quantitative recognition of Hg(II) ions in water were conducted even at trace concentrations without the need for sophisticated instruments. The OSM design was based on the physical interaction of a responsive organic probe with silica pore surfaces followed by strong and selective binding Hg(II)–probe interactions under specific sensing conditions, particularly at pH 5. Ultra-trace concentrations of Hg(II) ions were easily detected with the naked eye using the OSM. The remarkable ion spectral response of Hg(II) ion–OSM ensured the excellent quantification of the OSM for Hg(II) ion sensing over a wide range of concentrations with a detection limit of 1.75 × 10−9 M. This result indicated that low concentrations of Hg(II) ions can be detected with a high sensitivity. One of the key issues of OSM is the Hg(II) ion-selective workability even in the presence of high doses of competitive matrices and species. The OSM design showed significant Hg(II) ion-sensing capability despite the number of reuse/recycles using simple decomplexation. Given its high selectivity, fast response, and sensitivity, the OSM could be developed into a specific Hg(II) ion-sensing kit in aqueous solutions.

1. Introduction

The selective and sensitive detection of toxic heavy metal ions is important because of their negative effects on human health and the environment [1,2,3,4,5,6]. Among these ions, Hg(II) is the most ubiquitous because of its high toxicity and bioaccumulation [7,8,9,10]. Hg(II) is highly hazardous because both elemental and ionic Hg can be converted by bacteria in the environment into methylmercury, which is subsequently bioaccumulated along the food chain. High exposure to Hg(II) affects the brain and its associated functions, causing irritability, nervousness, tremors, vision problems, deafness, and the loss of muscle coordination, sensation, and memory. Methylmercury also damages the kidneys, stomach, heart, and intestines [11,12,13]. According to World Health Organization guidelines, the concentration of Hg(II) in drinking water must be below 2 µg/L [12]. Therefore, the development of highly sensitive and selective methods for the timely and accurate removal and monitoring of trace Hg(II) is urgently needed. Currently used analytical methods to monitor low Hg(II) levels include inductively coupled plasma mass spectrometry, ion-selective electrodes, atomic absorption spectrometry, and atomic fluorescence spectroscopy [14,15,16,17,18]. However, the applications of these methods are limited by their time-consuming process, high cost, low sensitivity and selectivity, and complicated sample preparation. To avoid these problems, we designed a new method with simple operation, rapid completion, low consumption, high sensitivity and selectivity, and possible applications in field tests and on-site Hg(II) monitoring [19,20,21,22]. Chemical precipitation, ion exchange, filtration, electrochemical separation, reverse osmosis, evaporative recovery, solvent extraction, and adsorption have been used to remove and preconcentrate heavy metal ions from water resources [23,24,25,26,27,28,29]. Among these techniques, adsorption is the most promising because of its low operational and maintenance costs; however, the potential of this method is limited by its low efficiency to completely remove heavy metal ions at low concentrations without the preconcentration process [19,20,21,22]. High-performance adsorbents have attracted increasing attention because of their capacity to remove toxicants and detect ultra-trace concentrations of these species [2,3,4,5,6,7,8,19,20,21,22].
Mesoporous inorganic monolithic membranes have received considerable interest in the last two decades because of their uniform and tunable pores with 2 and 3D hexagonal and cubic geometrical structures, thermal/ hydrothermal stability in organic and inorganic phases [30,31,32,33]. These mesoporous micrometric-size particle-like monoliths have many potentialities in control design of membrane applications in wide-range fields running from separation [34,35,36], catalysis [37,38] gas sensing [39] energy storage devices [40] to adsorption [2,3,4,5,6,7,8,19,20,21,22], Among these nanomaterials, 1D nanoscale channel-based materials have gained attention in recent years because of their unique electronic, optical, and mechanical properties as well as great potential for nanotechnology applications [41,42,43,44]. New types of hierarchical membrane materials for various industrial filtration applications have been synthesized [45,46,47,48,49,50]. Since Martin [44] discovered 1D nanochannels inside anodic alumina membranes (AAMs), controlled architecture over arranged armed pores and uniformly shaped nanochannel dimensions has led to vast advancements in materials science [45,46,47,48,49,50]. Particularly, 2D hexagonal and 3D cubic mesoporous silica mesostructures with pore sizes of 3–17 nm range hybrid the columnar pores of AAM nanochannels have been fabricated through template-guided methods using amphiphiles; these materials differ in character and structure under various conditions, leading to efficient size-exclusion separation and molecular transport technology [50]. In well-controlled environments, the detection of hazardous in the real-life environments particularly that associated in low level of concentration is crucial [51]. Thus, control design of optical chemical sensing is unquestionable. In this systematic optical sensor design, the color changes of the receptors are induced via nonspecific interaction with ion hazardous species, indicating significant signaling and selective response to the hazardous species [51,52,53,54,55,56,57,58]. Effective mesoporous sensor designs have enabled researchers to control assessment of sensing and removal techniques for continuously tracking pollutants up to nanomolar concentrations via visual color changes. In such systematic mesoporous sensor architectures, anchoring organic ligands into inorganic networks with well-defined pores promotes the sensibility of toxic analytes. However, the development of simple solid sensors for the selective detection of toxic ions in basic laboratory assays remains challenging [2,3,4,5,6,7,8,52,53,54,55,56,57,58].
In this study, silica nanotubes (NTs) with hexagonally ordered mesopores (6 nm) inside hybrid AAM channels were decorated by an organic dye probe without distorting the mesostructure geometry inside the NTs. An optical sensor membrane (OSM) was fabricated by imbuing the surfaces and pores of the NTs with organic scaffolds that can detect Hg(II) within 2–3 min. The decoration or covering the interior NTs by organic dye layers that are chemically stable and selectively active binding to target ions led to transport nonselective target species without absorption or binding with the NT wall (Scheme 1). The OSM offers Hg(II) ion-selective workability even in the presence of high doses of competitive matrices and species under specific sensing conditions, particularly at pH 5. The OSM also enables the development of a simple, portable, and reusable chemical sensing device even under rigorous chemical treatment despite the number of reuse/recycles.

2. Experimental Section

2.1. Chemicals

All materials were analytical grade and used as purchased without further purification. Tetramethylorthosilicate (TMOS), Brij76 [C18H35(OCH2CH2)10OH], dodecane (C12-alkane), and the organic dye diphenylthiocarbazone (DPTZ) were purchased from Sigma–Aldrich Company Ltd. (St. Louis, MO, USA). Hg(II) and other metal ion-standard solutions were obtained from Wako Company Ltd. (Osaka, Japan). The concentration of Hg(II) ions was calculated by comparing the color intensity of OSM after detecting Hg(II) samples and standard Hg(II) ion samples, which were prepared with known concentrations of Hg(II) analyte solutions. AAM with a pore size of 200 nm, a diameter of 2.5 cm, and a thickness of 60 μm was purchased from Whatman, Co. Ltd. (Maidstone, UK).

2.2. Synthetic Design of OSM

Mesoporous silica NTs inside the AAM nanochannels were fabricated through a direct method. The first step was the formation of microemulsion liquid crystalline phases, in which 1.0 g of Brij76, 0.5 g of dodecane, 2 g TMOS, 1.25 g of H2O–HCl, and 10 g of ethanol were applied dropwise onto the AAM nanochannels. The penetration of the precursor solution into the membrane was achieved within a vacuum at a starting pressure of ≤0.04 MPa. For the second step, silica NTs were cast along the entirety of the AAM nanochannel islands under suction, controlling the deposition of the surfactant/silica–NTs onto the inner pores of the AAM. The hybrid organic–inorganic membrane was placed in a sealed container at 45 °C for 10 h to complete drying. In the third step, the hybrid organic–inorganic membrane was thoroughly washed several times in a Soxhlet apparatus using ethanol/acidified H2O to remove the surfactant template and then dried at 60 °C [46,52]. The resulting materials were calcined at 550 °C under air. The solid scaffolds can be used to immobilize a 100 mL ethanolic solution of 45 mg DPTZ. The solution was directly dispersed or exposed to 1 g of the scaffold under static conditions at 50 °C for 10 h. DPTZ immobilization was repeated several times until the equilibrium adsorption capacity or “saturation” of the DPTZ molecule into the silica NTs was achieved. The resultant OSM was thoroughly washed with deionized water until no elution of the DPTZ into the solution was observed. The released/eluted DPTZ color was detected by measuring the absorbance spectra at ʎmax = 445 nm (Scheme 1).

2.3. Instrumental Analysis

High-resolution transmission electron microscopy (HRTEM) was performed using a JEOL JEM model 2100F microscope. Energy dispersive X-ray spectroscopy (EDS) was conducted using a Horiba EDS-130S directly connected with a Hitachi FE-SEM S-4300. FE-SEM images were measured using a field-emission scanning electron microscope (Hitachi S-4300). Small-angle powder X-ray diffraction (XRD) patterns were measured by using a 18 kW diffractometer (Bruker D8 Advance) with monochromated CuKα radiation and with scattering reflections recorded at 2θ angles between 0.1° and 6.5° corresponding to d-spacing between 88.2 and 1.35 nm. N2 adsorption–desorption isotherms were measured using a BELSORP MIN-II analyzer (JP. BEL Co. Ltd, Osaka, Japan) at 77 K. The pore size distribution was determined from the adsorption isotherms through nonlocal density functional theory. The absorbance spectrum of the OSM was obtained using a UV-Vis-NIR spectrophotometer (Shimadzu 3700). Hg(II) ion concentrations were determined via inductively coupled plasma atomic emission spectrometry (ICP-MS, Perkin Elmer Elan-6000).

3. Results and Discussion

3.1. Building Design of OSM Architectures

Mesoporous silica NTs with a mesocylinder pore of approximately 6 nm inside AAM channels of 200 nm neck pores may serve as a new class of membranes with toxic ion-sensing functionality. However, the functionalization of vertically aligned silica NTs casting nanochannels with a large area-to-volume ratio and uniformly-packed mesopores led to the dense connection and condensed decoration of DPTZ into NTs and then to the formation of interior coating layers for Hg(II) ion-selective species from water (Scheme 1). The design of OSM with macroscopic length disc (2.5 cm) and ordered mesopores inside NTs was based on sufficiently physisorbed interactions (Scheme 2) between the silanol groups of silica NTs and the heteroatoms of DPTZ. This process led to the high loading capacity and accessibility of the DPTZ probe. Moreover, the long-term dispersion time and deep cavitation of DPTZ into >>20 µm channel length offer the required interactions with the NT wall to prevent the leaching of probe receptors from the OSM disc. No elution of the OSM platforms occurred during the detection of Hg(II) ions in aqueous solutions (Scheme 1E–F). These results indicated that the stability of the fabricated OSM incorporated with DPTZ may enhance the fast response optical color signal, Hg(II) ion-stripping under severe condition of reuse/recycles, and selectivity of Hg(II) ions among competitive matrices and species (Scheme 1).
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Scheme 1. Schematic of mesoporous silica NT-supported anodic alumina membranes (AAM) channels (A–C), optical sensor membrane (OSM) (D), and ion-sensing functionality processes in terms of visualization (E), stripping (G), and selectivity (F). The silica nanotube (NT) scaffolds were fabricated through template-assisted synthesis, in which the chemical composition containing Brij/alkane/TMOS/ethanol/H2O could be penetrated through AAM channels by a pressure-assisted method (A, B). The calcined NT/AAM (C) could be used to synthesize OSM through the stepwise immobilization of DPTZ (D). Bench-top contact method for controlling the optical Hg(II) ion-screening/sensing in water using OSM (E–F).
Scheme 1. Schematic of mesoporous silica NT-supported anodic alumina membranes (AAM) channels (A–C), optical sensor membrane (OSM) (D), and ion-sensing functionality processes in terms of visualization (E), stripping (G), and selectivity (F). The silica nanotube (NT) scaffolds were fabricated through template-assisted synthesis, in which the chemical composition containing Brij/alkane/TMOS/ethanol/H2O could be penetrated through AAM channels by a pressure-assisted method (A, B). The calcined NT/AAM (C) could be used to synthesize OSM through the stepwise immobilization of DPTZ (D). Bench-top contact method for controlling the optical Hg(II) ion-screening/sensing in water using OSM (E–F).
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3.2. Characterization of the Fabricated OSM Architectures

NT scaffolds and OSM were successfully fabricated, as evidenced by HRTEM and SEM micrographs (Figure 1A,B), EDM analyses (Figure 1C), and XRD and N2 isotherm profiles (Figure 1D,E). High-resolution TEM (HR-TEM) images (inset in Figure 1A) showed that each NT had ordered mesoporous arrays circularly arranged around the tube axis in the OSM. The OSM NTs clearly contained open pores with regular and continuous alignment along the perpendicular axis of the AAM host surfaces. SEM images (Figure 1B) revealed that this synthetic design allowed the control of the vertical alignment of the silica NTs parallel to the axis of the AAM nanochannels. We observed rigid, free-standing OSM clearly featuring open pores with regular and continuous alignment along the perpendicular axis scaffold platforms. The results clearly indicated the formation of condensed mesoporous OSM NTs, permitting the ion-sensing and removal of toxicants from water. EDS analysis (Figure 1C) revealed the presence of Si, Al, O, C, S, and N in the fabricated OSM. The EDS, TEM, and SEM results indicated that the decoration of DPTZ and the formation of OSM occurred via deep accommodation into the entire mesopore NTs/AAM and with orientational axis parallel to NTs [50].
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Figure 1. HRTEM micrograph patterns of the OSM (A). FESEM micrographs of the OSM (B) and EDS of the fabricated OSM indicate the presence of Si, Al, O, C, S, and N (C). Small-angle XRD patterns (D); N2 adsorption/desorption isotherms (E) of the silica NTs/AAM scaffolds (a), OSM fabricated by immobilization of the DPTZ probe on silica NTs scaffolds (b), and OSM after Hg(II) ion screening/sensing (c).
Figure 1. HRTEM micrograph patterns of the OSM (A). FESEM micrographs of the OSM (B) and EDS of the fabricated OSM indicate the presence of Si, Al, O, C, S, and N (C). Small-angle XRD patterns (D); N2 adsorption/desorption isotherms (E) of the silica NTs/AAM scaffolds (a), OSM fabricated by immobilization of the DPTZ probe on silica NTs scaffolds (b), and OSM after Hg(II) ion screening/sensing (c).
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The XRD patterns of the hexagonal silica NTs/AAM scaffolds and OSM are shown in Figure 2D. Reflection peaks with high-intensity and well-defined resolution were observed in the range of 1.2 < 2θ < 3.0, which strongly suggested the formation of ordered hexagonal mesostructures of scaffolds and OSM with 100 and 110 reflection planes (Figure 1Da–Dc). The high-intensity peak of OSM patterns (Figure 1Db,Dc) shifted to a high 2θ, which indicated the immobilization of DPTZ in the interior of the NT mesopores. In general, the XRD profiles indicated the retention of the hexagonal structure of OSM despite the immobilization of DPTZ probes in the inner pores of the NTs and the multiple uses of OSM for Hg(II) detection/removal (Figure 1Dc). N2 adsorption isotherms also implied mesoporous OSM formation (Figure 1E). The N2 isotherms (Figure 1E) showed well-defined isotherm steepnesses, indicating the formation of channel-like mesopores with no constrictions. The isothermal shape and capillary evaporation indicated the formation of uniform cylinder-like structures. Consequently, the presence of large hysteresis H1 and H3 loops (Figure 1Ec) for typical hexagonal mesocylinder materials was revealed. This result coincided with previous studies on bulk mesoporous materials functionalized with organic molecules [59,60,61,62]. Table 1 shows the Brunauer–Emmett–Teller surface area (SBET), pore volume (Vp), and pore diameter (D) of the support material modified with organic scaffolds and after multiple uses for Hg(II) ion screening/sensing. Upon DPTZ immobilization, the surface area and pore volume of the material slightly decreased (Table 1), and the width of the hysteresis loop reduced (Figure 1Eb,Ec). This result indicated the inclusion of the probe within the inner pores of the OSM. The OSM demonstrated high affinity binding with Hg(II) ions, as evidenced by the color reactions for trace Hg(II) concentrations. These reactions were clearly visible to the naked eye (see Section 3.3).
Table
Table 1. N2 adsorption parameters of silica NTs (a), OSM fabricated by immobilization of the probe on silica NTs (b), and OSM after Hg(II) ion screening.
Table 1. N2 adsorption parameters of silica NTs (a), OSM fabricated by immobilization of the probe on silica NTs (b), and OSM after Hg(II) ion screening.
MaterialS(BET) m2/gVp cm3/gD/nm
Silica NTs1300.666.1
Silica NT-Captor700.605.7
Silica NT-Captor/Hg400.405.2

3.3. Optical Screening/Sensing of Hg(II) Ions Using OSM

The optical screening/sensing of Hg(II) ions in water using OSM was assessed by the top-bench contact time technique. Under this protocol, the OSM was fixed in an ordinary filtration apparatus under static conditions (Scheme 1). A mixture containing specific concentrations of Hg(II) ions was adjusted at appropriate pH 5 solutions at a constant volume (20 cm3) and then added to the OSM. After approximately 2 min of response time, the solution was filtrated under gentle vacuum at 0.04 MPa and room temperature. The aliquot/rejected solution was collected and monitored by ICP-MS. The color change of the solid OSM indicated the visual detection and quantitative recognition of Hg(II) ions (Scheme 1 and Scheme 2).
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Scheme 2. The chemical formation of [Hg-DPTZ)2] complex during the selective ion-OSM sensing conditions. The feasibility of reusing OSM was obtained by addition of 0.05 M of ClO4− solution as stripping agent.
Scheme 2. The chemical formation of [Hg-DPTZ)2] complex during the selective ion-OSM sensing conditions. The feasibility of reusing OSM was obtained by addition of 0.05 M of ClO4− solution as stripping agent.
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To control the optimal sensing experiment conditions, particularly pH, batch sensing experiments were performed at a wide range of pH (2–12) (Figure 2A). The different pH values were established by mixing 0.2 M KCl with HCl (pH 1–3), CH3COONa with CH3COOH (pH 4–6), 3-morpholinopropane sulfonic acid with NaOH (pH 6.5–8.5), and N-cyclohexyl-3-aminopropane sulfonic acid with NaOH (pH 9–12). To determine the optimum pH for the donor–acceptor combinations between the OSM and Hg(II) ions, the reflectance spectra of the formed Hg(II)–DPTZ binding events on OSM were carefully monitored over a wide range of pH solutions. The DPTZ immobilized on the silica NTs had different donor atoms, such as N and S, which can be neutral or protonated, depending on the pH of the medium that can form metal complexes because of a deficiency in the d-orbitals of the metal ion centers (Scheme 2) [54,55]. UV–vis reflectance spectra were used to monitor the changes in the OSM color upon the formation of the [Hg–(DPTZ)2] complex (Scheme 2). The maximum changes in the color and reflectance spectra of OSM implied the sensitive and flexible changes in the electronic structure of the DPTZ at pH 5. The change in the color and reflectance intensity of the [Hg–(DPTZ)2] complex was recorded at λmax = 485 nm and at pH 5. The effect of Hg(II) ion concentration on the reflectance spectra and sequential color response of OSM at pH 5 was examined (Figure 2B). The prompt reflectance spectral responses by OSM showed the effective detection of Hg(II) ions at ʎmax = 485 nm, with color transitions at a frequency that could be detected by the naked eye even at trace concentrations [51,52,53,54,55,56,57,58].
Figure 2C shows the calibration curve of Hg(II) ion–OSM. The quantitative analysis (i.e., calibration curve) depicted the reflectance spectral responses of the OSM as function of Hg(II) ion concentrations under optimized sensing conditions of 2 min contact time, pH 5, and 20 °C temperature. The R−Ro relationship was obtained by measuring the relative reflectance of the [Hg-(DPTZ]2]n+ complex (R) formed relative to a blank solid of OSM (Ro). The limit of detection (LOD) of the OSM for Hg(II) ions estimated from the linear part of the calibration curve according to the following equation LOD= k Sb/m, where Sb and m are the standard deviation and the slope of the calibration curve, respectively, and the constant k is 3. The LOD of OSM at a particular pH was calculated to be 1.75 × 10−9 M for Hg(II) ions, indicating of the efficiency of the Hg(II) ion-sensing method for the estimation and detection of trace Hg(II) ion concentrations. Thus, the proposed method may be appropriate for household and environmental monitoring [62].
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Figure 2. pH-dependent curves of OSM in the measurement of the reflectance spectra “signal” response and the color profiles of the [Hg–(DPTZ)2] complex during the optical screening of Hg(II) ions at 485 nm (A); Reflectance spectra and sequential color response of OSM at different concentrations of Hg(II) ions at pH 5 (B). Calibration curve of the reflectance spectra of OSM for various Hg(II) concentrations at 485 nm. The inset in the graph shows the low-limit colorimetric responses of Hg(II) ions with a linear fit line in the linear concentration range before saturating the calibration curve (C). The solid line represents the calibration curve of the Hg(II) ions in the presence of active interfering species [i.e., Co(II), Mn(II), Cu(II), Zn(II), Fe(III), and Ni(II)] under the same sensing/screening conditions.
Figure 2. pH-dependent curves of OSM in the measurement of the reflectance spectra “signal” response and the color profiles of the [Hg–(DPTZ)2] complex during the optical screening of Hg(II) ions at 485 nm (A); Reflectance spectra and sequential color response of OSM at different concentrations of Hg(II) ions at pH 5 (B). Calibration curve of the reflectance spectra of OSM for various Hg(II) concentrations at 485 nm. The inset in the graph shows the low-limit colorimetric responses of Hg(II) ions with a linear fit line in the linear concentration range before saturating the calibration curve (C). The solid line represents the calibration curve of the Hg(II) ions in the presence of active interfering species [i.e., Co(II), Mn(II), Cu(II), Zn(II), Fe(III), and Ni(II)] under the same sensing/screening conditions.
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3.4. Feature and Functionality of the Hg(II) Ion–OSM Sensing System

An important analytical feature of OSM is its response time, which is controlled by the time required for Hg(II) ions to diffuse from the bulk of the solution to the OSM interface to form Hg(II)–DPTZ complexes. Figure 3 shows the effect of time on Hg(II) ion sensing/screening at pH 5, 20 °C, and different Hg(II) ion concentrations (20, 50, and 200 ppb), as determined by ICP-MS analysis. With prolonged time, the equilibrium concentration of Hg(II) ions decreased. This decrease in concentration resulting from the uptake of Hg(II) into the OSM decreased the diffusive transport of the Hg(II) ions. The OSM under optimum sensing conditions reached more than 95% of its uptake at 2 min. In addition, the change in the reflectance signaling and color transition (Figure 3B) was proportional to the concentration of metal ion uptake into solid OSM. In this solid analysis, the increase in the reflection spectra as a function of time indicated the adsorption of Hg(II) ions into the NT cavity of the OSM.
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Figure 3. Effect of time on the uptake of Hg(II) on the OSM at different Hg(II) concentrations. The inset shows the reflectance spectra for OSM (blank) and OSM–Hg(II) ions uptake at pH 5 and color transition map tested at the total volume of 20 mL and temperature of 20 °C.
Figure 3. Effect of time on the uptake of Hg(II) on the OSM at different Hg(II) concentrations. The inset shows the reflectance spectra for OSM (blank) and OSM–Hg(II) ions uptake at pH 5 and color transition map tested at the total volume of 20 mL and temperature of 20 °C.
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Figure 4. Selectivity studies of OSM for [500 ppb]Hg(II) ion removal carried out in groups at pH 5, 20 mL total volume, and 20 °C temperature. Sequential color and reflectance signaling at characteristic λmax = 485 nm, indicating the response to the OSM sensor (blank, i.e., metal-free assay) and with the addition of interfering cationic species and target ions.
Figure 4. Selectivity studies of OSM for [500 ppb]Hg(II) ion removal carried out in groups at pH 5, 20 mL total volume, and 20 °C temperature. Sequential color and reflectance signaling at characteristic λmax = 485 nm, indicating the response to the OSM sensor (blank, i.e., metal-free assay) and with the addition of interfering cationic species and target ions.
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One of the main characteristics of OSM technology is its ion-sensitive selectivity to the target Hg(II) ions. Figure 2B and Figure 3B (inset) show that the OSM can be used as an optical kit to yield preconcentration efficiency, allowing the visual inspection and rapid monitoring of a wide range of Hg(II) ion concentrations, including ultra-trace concentrations (Figure 2B). We studied the potential selectivity of our material in the presence of interfering cations at pH 5 (Figure 4). No significant changes were observed in the visible color patterns and the reflectance spectra of the OSM (blank) even after adding high concentrations of various competitive ions. This result indicated that the negative disturbance affected OSM. We examined the specificity of OSM by assessing its capacity to selectively detect Hg(II) ions in the presence of a multi-metal interference system under optimum sensing conditions (Figure 4). No obvious changes were detected in the visible color or reflectance patterns in the presence of other interfering species, even at high loading levels [5 to 10 times the amounts of Hg(II) ions]. This result indicated the rapid binding response and stability of Hg(II)–OSM complexes within the pore surfaces, which allowed the selective determination of toxic ions in real samples [2,3,4,5,6,7,8].
A key component of OSM is its reversibility against repeated uses (Scheme 2), thereby allowing the multiple reuse of OSM. This OSM feature can significantly reduce reagent consumption. The main objective of this study is to determine a method to efficiently control the reuse of our engineered OSM (Scheme 1 and Scheme 2). Sensing experiments with reuse/recycle were performed under the Hg(II) ion selective conditions of 20 °C, pH 5, 20 mL total volume, 1 ppm [Hg(II)], and 2 min response time. Hg(II) ion–OSM regeneration was carried out through a chemical treatment process, in which a specific concentration of Hg(II) ion stripping agent was added with a minimum volume and concentration. The best results were obtained using a 0.05 M ClO4− solution, which permits complete regeneration in an optimally reasonable conditioning time (i.e., 15 min) (Scheme 2). The feasibility of reusing OSM after a number of sensing/capturing and regeneration cycles was investigated (Figure 5). After eight regeneration/reuse cycles, the reflectance slightly decreased. This result indicated that a slight decrease in efficiency can slightly affect the overall efficiency of the OSM.
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Figure 5. Multiple reuse cycles of the sensor for Hg(II) ions after eight regeneration/reuse cycles (the reusability efficiency was measured compared to the first cycle at λmax = 485 nm, inset). Experiments were performed under the following conditions: pH 5, total volume 20 mL, and temperature at 20 °C; [Hg(II)] of 500 ppb.
Figure 5. Multiple reuse cycles of the sensor for Hg(II) ions after eight regeneration/reuse cycles (the reusability efficiency was measured compared to the first cycle at λmax = 485 nm, inset). Experiments were performed under the following conditions: pH 5, total volume 20 mL, and temperature at 20 °C; [Hg(II)] of 500 ppb.
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4. Conclusions

We report the design and engineering of OSM based on the tailored channel arrays of hexagonal mesocylinder silica NTs inside AAM. In solid-state ion-sensing systems, the physical features of OSM, such as the large surface area-to-volume ratios of the modified layers of organic scaffolds and the uniform pores, enabled the synthesis of a multi-particulate sensing system for the highly selective and sensitive optical screening and fast-response monitoring of Hg(II) ions, even at trace concentrations, in drinking water. The constructed sensory system can be repeatedly used in aqueous solutions. Thus, our OSM design can continuously generate readable optical signals, which are suitable for reporting recognition events without the need for other treatments or complex instruments.

Author Contributions

The present work is designed to pursuit Professor Sherif’ Lab goals, motivation, and research variety in the environmental field. This research work introduces the idea of Prof. Sherif; however, the other Authors effectively achieved the experimental facts towards goal attainment. All Authors are shared in discussion, writing down the texture body of the manuscript.

Conflicts of Interest

The present findings of research impacts show the real degree of variety among all presented work reported by the Authors and other groups. We here declare that there is no confliction of interests in this research work.

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MDPI and ACS Style

Elshehy, E.A.; EL-Safty, S.A.; Shenashen, M.A. Reproducible Design for the Optical Screening and Sensing of Hg(II) Ions. Chemosensors 2014, 2, 219-234. https://doi.org/10.3390/chemosensors2040219

AMA Style

Elshehy EA, EL-Safty SA, Shenashen MA. Reproducible Design for the Optical Screening and Sensing of Hg(II) Ions. Chemosensors. 2014; 2(4):219-234. https://doi.org/10.3390/chemosensors2040219

Chicago/Turabian Style

Elshehy, Emad A., Sherif A. EL-Safty, and Mohamed A. Shenashen. 2014. "Reproducible Design for the Optical Screening and Sensing of Hg(II) Ions" Chemosensors 2, no. 4: 219-234. https://doi.org/10.3390/chemosensors2040219

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