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Article

Fluorescence-Based Detection of Benzene, Toluene, Ethylbenzene, Xylene, and Cumene (BTEXC) Compounds in Fuel-Contaminated Snow Environments

by
Dana J. DiScenza
,
Lauren E. Intravaia
,
Anna Healy
,
Sage B. Dubrawski
and
Mindy Levine
*
Department of Chemistry, University of Rhode Island, Kingston, RI 02881, USA
*
Author to whom correspondence should be addressed.
Chemosensors 2019, 7(1), 5; https://doi.org/10.3390/chemosensors7010005
Submission received: 5 December 2018 / Revised: 3 January 2019 / Accepted: 10 January 2019 / Published: 15 January 2019
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Versions Notes

Abstract

:
Reported herein is the sensitive and selective cyclodextrin-promoted fluorescence detection of benzene, toluene, ethylbenzene, xylene, and cumene (BTEXC) fuel components in contaminated snow samples collected from several locations in the state of Rhode Island. This detection method uses cyclodextrin as a supramolecular scaffold to promote analyte-specific, proximity-induced fluorescence modulation of a high-quantum-yield fluorophore, which leads to unique fluorescence responses for each cyclodextrin-analyte-fluorophore combination investigated and enables unique pattern identifiers for each analyte using linear discriminant analysis (LDA). This detection method operates with high levels of sensitivity (sub-micromolar detection limits), selectivity (100% differentiation between structurally similar compounds, such as ortho-, meta-, and para-xylene isomers), and broad applicability (for different snow samples with varying chemical composition, pH, and electrical conductivity). The high selectivity, sensitivity, and broad applicability of this method indicate significant potential in the development of practical detection devices for aromatic toxicants in complex environments.

1. Introduction

The ubiquitous prevalence of benzene, toluene, ethylbenzene, xylenes, and cumene (BTEXC) in the environment [1] is a result of the fact that they are components of various fuel types, including gasoline [2] and crude oil [3]. The deleterious health effects associated with exposure to these compounds varies somewhat by compound [4], with benzene in particular demonstrated to have high toxicity [5] and carcinogenicity [6]. Even relatively less toxic analytes, such as toluene, have still been reported to have negative health effects for humans [7] and animals [8]. Literature-reported detection methods for BTEXC compounds include gas chromatography-mass spectrometry (GC-MS) [9], liquid chromatography-mass spectrometry (LC-MS) [10], and electrochemical methods [11]. Although many of the mass spectral-based methods provide extraordinarily high levels of sensitivity and selectivity, they are often not suitable for use in real-world environments due to the bulky and costly instrumentation required, nor are they suitable for rapid screening of large numbers of potentially contaminated samples, due to the time required for analysis of each sample. While the electrochemical methods can be portable [12], rapid [13], and highly sensitive [14], the general applicability of such methods has not yet been determined.
The use of fluorescence-based methods for toxicant detection can avoid many of the practical challenges associated with mass spectral detection [15]. In particular, fluorescence-based detection in complex environments can occur using a hand-held device while maintaining high sensitivity [16], and can also be performed rapidly to enable high-throughput sample screening [17]. Fluorescence-based detection methods have been reported for a broad variety of analytes using a range of fluorescent sensors, including explosive detection via fluorescent conjugated polymers [18] and nanoparticles [19], anion detection via supramolecular fluorescent sensors [20], and cation detection via interactions of cationic analytes with small-molecule, high-quantum-yield fluorophores [21]. The use of fluorescence-based methods for BTEXC detection in real-world environments has been reported only rarely to date, in combination with capillary electrophoresis [22] or other chromatographic methods to enable separation prior to detection [23].
Our research group has reported a fundamentally new method for fluorescence-based toxicant detection, using cyclodextrin as a supramolecular scaffold to promote proximity-induced energy transfer from a toxicant to a high-quantum-yield fluorophore acceptor in cases where the toxicant is photophysically active [24], and proximity-induced analyte-specific fluorescence modulation in cases where the toxicant is not photophysically active (Figure 1) [25].
We have demonstrated that this system enables effective detection in the complex environments of human plasma [26], urine [27], and breast milk [28], as well as in aqueous extracts collected from crude oil samples [29], in contaminated marine environments [30], and in extracts from a large-scale fuel spill event [31].
One potential source of BTEXC exposure is through snow melt, a particular concern in geographic regions in which snowfall is prevalent, including in New England [32]. Literature reports indicate that BTEXC is often found in snow [33], and that snow melting leads to BTEXC contamination of the local water supply [34], which affects species who consume the water as well as those who live in the water [35]. Reported herein is the application of our cyclodextrin-promoted system for BTEXC detection in snow melt, collected from several geographic regions throughout the state of Rhode Island, and the ability of the cyclodextrin-based system to accomplish sensitive, selective, and rapid detection of these ubiquitous environmental pollutants. Preliminary efforts towards the development of quantitative detection systems are also discussed.

2. Materials and Methods

2.1. Instruments and Reagents

All toxicant analytes, control analytes, and fluorophores (compounds 1–9, Figure 2) were purchased from Millipore-Sigma chemical company and used as received, unless otherwise noted. All cyclodextrins were purchased from Tokyo Chemical Industry (TCI) and used as received. Fluorescence spectra were obtained using a Shimadzu RF6000 spectrophotofluorimeter with 3.0 nm excitation and emission slit widths. All gas chromatography – mass spectrometry (GC-MS) measurements were obtained using a Shimadzu GC-MS QP2020 gas chromatograph-mass spectrometer (obtained from Shimadzu Scientific Instruments, Marlborough, MA, USA). All pH measurements were obtained using a Microlab FS-522 instrument. Conductivity experiments were performed using a Thermo Scientific Orion 3-Star Benchtop Conductivity Kit.

2.2. Sample Collection Procedures

Snow samples were collected from three locations around Rhode Island: Newport, Providence, and Kingston (Figure 3), 24 hours after a snowfall event. Samples were stored in amber high-density polyethylene bottles obtained from Fisher Scientific chemical company, which were transported to the University of Rhode Island in a climate-controlled vehicle within one hour of collection and stored in the laboratory refrigerator until used for analysis.

2.3. Details for Snow Characterization Experiments

2.3.1. GC-MS Experiments

Approximately 10 mL of melted snow and 10 mL of dichloromethane were added to a separatory funnel. The separatory funnel was shaken vigorously, and the aqueous layer was discarded. Another 10 mL of melted snow was added to the organic layer, and the extraction procedure was repeated. The organic layer was dried with MgSO4, concentrated using a rotary evaporator, filtered, and analyzed using GC-MS.
All GC-MS measurements were obtained on a Shimadzu QP2020 gas chromatograph-mass spectrometer with the following settings: column: Shimadzu SH-Rxi-5Sil MS (30 m × 0.25 mm × 0.25 µm); oven temperature: 45 °C, hold for 3 min, 8 °C/min to 220 °C, hold for 15 min; injection temperature: 200 °C; splitting ratio: splitless; MS ion source temperature: 230 °C; interface temperature: 150 °C; solvent cut time: 3.5 min.

2.3.2. pH Experiments

All pH experiments were performed using a MicroLab FS-522 instrument (obtained from MicroLab, Inc, in Bozeman, MT). The pH probe was calibrated using Fisherbrand pH 4, 7, and 10 pre-made buffer solutions, obtained from Fisher Scientific Chemical Company. pH values were obtained using MicroLab software version 6.3.4.

2.3.3. Conductivity Experiments

All conductivity experiments were performed using a Thermo Scientific Orion 3-Star Benchtop Conductivity Kit. The conductivity probe was rinsed thoroughly with deionized water between samples.

2.4. Details for Fluorescence Modulation Experiments

In a quartz cuvette, 1.25 mL of a 10 mM cyclodextrin solution dissolved in phosphate buffered saline (PBS) and 1.25 mL of a melted snow sample were combined and mixed thoroughly by shaking. For control experiments in the absence of snow, 1.25 mL of a 10 mM cyclodextrin solution in PBS and 1.25 mL deionized (DI) water were combined and mixed thoroughly. Next, 100 µL of a 0.1 mg/mL fluorophore 9 solution in tetrahydrofuran (THF) was added, and the fluorescence emission spectrum was taken four times using a 460 nm excitation wavelength to excite the fluorophore. Then, 20 µL of analytes 1–8 (1.0 mg/mL in THF) were added to the mixture, and the resulting solution was again excited four times at 460 nm. The fluorescence emission spectra were integrated vs. wavenumber on the X-axis using OriginPro software, and the degree of fluorescence modulation was determined by the ratio of the integrated emission of the fluorophore in the presence of analyte to the integrated emission of the fluorophore in the absence of analyte, as shown in Equation (1):
Fluorescence modulation = Flanalyte/Flblank
where Flanalyte is the integrated emission of the fluorophore in the presence of the analyte, and Flblank is the integrated emission of the fluorophore in the absence of the analyte. Fluorescence modulation ratios greater than 1 indicate an enhancement of fluorescence emission of the fluorophore in the presence of the analyte, fluorescence modulation ratios less than 1 indicate a decrease in fluorescence emission of the fluorophore in the presence of the analyte, and fluorescence modulation ratios close to 1 indicate minimal change in the fluorescence emission of the fluorophore in the presence of the analyte.

2.5. Details for Array Generation Experiments

Arrays were generated using SYSTAT 13 statistical computing software with the following settings: (a) Classical discriminant analysis; (b) Grouping variable: analytes; (c) Predictors: cyclodextrins; and (d) Long-range statistics: Mahal.

2.6. Details for Limit-of-Detection Experiments

Limit-of-detection experiments were conducted following literature-reported procedures [36]. In brief, 1.25 mL of a 10 mM methyl-β-cyclodextrin solution and 1.25 mL of a snow sample were added to a quartz cuvette and mixed thoroughly. 100 µL of fluorophore 9 was added to the cuvette, and the solution was excited six times at 460 nm.
Next, 5 µL of analyte was added, and again the solution was excited six times at 460 nm. This step was repeated for 10 µL of analyte, 15 µL of analyte, 20 µL of analyte, 25 µL of analyte, and 30 µL of analyte.
All fluorescence emission spectra were integrated vs. wavenumber on the X-axis, and calibration curves were generated. The curves plotted the analyte concentration, measured in µM, on the X-axis and the fluorescence modulation ratio on the Y-axis. The curve was fitted to a straight line, and the equation of the line was determined. The limit of detection (LOD) was calculated according to Equation (2):
Limit of Detection (LOD) = 3(SDblank)/m
where SDblank is the standard deviation of the blank sample and m is the slope of the calibration curve. In all cases, the LOD was calculated as a concentration in µM.

3. Results

3.1. Component Selection Details

3.1.1. Sampling Location Selection

For this research, we chose areas of Rhode Island that are known to be highly populated—meaning that large populations have potential toxicant exposure—as well as areas that had a lot of traffic, meaning that high concentrations of fuel are used in a relatively small area. Newport snow was obtained from a parking lot of a shopping complex that is frequented by passenger cars, delivery trucks, and buses. Providence snow was collected from a busy street with cars, buses, and waste management vehicles [37]. The samples collected from Providence were of particular interest, as Providence has already been reported as a highly polluted city with significant quantities of acid rain, and the possibility for acidic snow exists as well [38]. Kingston snow was collected from a highly frequented street at the University of Rhode Island, with a lot of cars, buses, and construction vehicles.

3.1.2. Cyclodextrin Selection

Previous work in our group has used a variety of commercially available cyclodextrin hosts, including α-cyclodextrin, comprised of 6 glucose units; β-cyclodextrin, containing 7 glucose units; and γ-cyclodextrin, comprised of 8 glucose units; as well as two β-cyclodextrin derivatives: methyl-β-cyclodextrin, with an average of 1.8 methyl groups per glucose unit [39], and 2-hydroxypropyl-β-cyclodextrin, with an average of 0.65 hydroxypropyl groups per glucose unit [39]. For these experiments, we selected β-cyclodextrin, methyl-β-cyclodextrin, and 2-hydroxypropyl-β-cyclodextrin as supramolecular hosts, based on the previously demonstrated high performance of β-cyclodextrin-derived hosts in promoting highly analyte-specific, proximity-induced interactions, Ref. [31] and as a result of the fact that β-cyclodextrin is a known host for single-ring aromatic guests.

3.1.3. Fluorophore Selection

For these experiments, a commercially available, methyl-substituted boron-dipyrromethene (BODIPY) derivative was used, based on the well-documented ability of BODIPY fluorophores to display high quantum yields and robust performance under a variety of experimental conditions [40,41,42].

3.1.4. Analyte Selection

Analytes 1–7 were selected due to their known prevalence in automobile fuel, as well as their known and suspected toxicities. Analyte 8 was chosen due to its ability to dissolve analytes 1–7, and its miscibility with the melted snow samples, and was used as a control analyte to elucidate any effects of the solvent on the observed fluorescence modulation ratios.

3.2. Undoped Snow Sample Experiments

3.2.1. GC-MS Experiments on Undoped Snow Samples

Gas chromatography – mass spectrometry (GC-MS) was used to characterize the undoped (i.e., analyte-free) snow melt samples (Figure 4), with all samples showing peaks in the chromatograms corresponding to long-chain alkanes [43] and amides [44] that are typically found in fuel and other environmental contamination sources. Snow melt from Newport showed the lowest number of peaks, corresponding to the fewest organic contaminants, likely due to the sampling location selected (Newport sample from parking lot; Providence and Kingston samples from street). Melted snow from Providence showed the highest amount of fuel components, likely due to the known pollution and traffic density in this urban area. Melted snow from Kingston showed a peak from triacetin, which was not found in the other two samples. It is also commonly used as a diesel fuel stabilizer [45], which is likely due to the large number of construction vehicles in the local geographic area. All of the samples showed a peak for 9-octadecenamide, a common surfactant that is added to fuel [46].
Although there were no peaks corresponding to the BTEXC analytes in the GC-MS spectra for each snow sample, peaks corresponding to other components of automobile fuel strongly suggest the presence of fuel contamination (see Table S2 in Supporting Information for more details). Our inability to detect BTEXC compounds in these samples could be due to their higher volatility compared to the other fuel components detected, as well as the fact that these components volatilized prior to analysis [47].

3.2.2. pH and Conductivity Experiments on Undoped Snow Samples

The pH and conductivity of the melted snow samples were measured to quantify compositional differences between the samples (Table 1).
Of note, Providence snow had the lowest pH of the three snow-melt samples, followed by Kingston and Newport, likely as a result of the greater prevalence of acid rain and acid snow in Providence due to significant urban pollution. The conductivity of each snow melt sample was measured as an indicator of the overall salinity and total electrolyte concentration [48]. Newport had the highest conductivity, followed by Kingston and Providence. This could be due to salting of the roads after snow storms in the parking lot where Newport snow was collected, as well as the street at the University of Rhode Island where Kingston snow was collected. Snow treatments in Providence, by contrast, rely less on salting roadways and more on other options, such as sanding.

3.2.3. Fluorescence Experiments on Undoped Snow Samples

Spectroscopic measurements of the emission of fluorophore 9 in undoped (i.e., analyte-free) melted snow further confirmed compositional differences between the samples (Figure 5), as a result of the fact that the fluorophore emission is known to be highly sensitive to environmental differences.
Of all the combinations of cyclodextrins and snow samples investigated, fluorophore 9 showed the highest emission intensity in melted snow obtained from Providence. This is likely due to the presence of a large number of fuel components inherently present in the solution which interact favourably with the fluorophore 9-cyclodextrin host—guest complexes to create localized, non-polar areas, resulting in higher quantum yields. Differences between sampling locations were more pronounced with methyl-β-cyclodextrin and 2-hydroxypropyl-β-cyclodextrin as hosts, which are both more soluble and more hydrophobic than the unsubstituted β-cyclodextrin [49]. Although benzene-derived aromatic compounds form strong host-guest complexes with all β-cyclodextrin derived compounds investigated herein, including β-cyclodextrin [50], methyl-β-cyclodextrin [51], and 2-hydroxypropyl-β-cyclodextrin [52], the enhanced solubility, combined with the greater hydrophobic character of methyl-β-cyclodextrin, promote the stronger complexation of the aromatic guests [53]. This, in turn, results in more sensitive changes in the fluorophore emission signal upon introduction of the BTEXC guests and competitive displacement of the fluorophore from the cyclodextrin cavity.
Array-based analysis was also used to differentiate between integrated fluorescence emission of undoped (i.e., analyte-free) snow samples (Figure 6). In every case, results indicated 100% success in differentiating between melted snow samples, as a result of the known sensitivity of boron-dipyrromethene (BODIPY) dyes to sample-specific environmental differences, such as organic components (as measured by GC-MS) [54], pH (which is affected by the presence of acid rain) [55], and salt content (as measured through conductivity) [56], which results in different fluorescence responses and excellent separation between the undoped sample signals.

3.3. Analyte-Doped Snow Samples

3.3.1. Fluorescence Modulation of Analyte-Doped Snow Samples

Each cyclodextrin, in combination with fluorophore 9 as a signal-transducing element, was used for the detection of specific fuel components within the complex matrices of three real-world snow samples. Micromolar concentrations of analytes 1–7 or control analyte 8 were added to each solution, and the resulting changes in the fluorescence emission of fluorophore 9 in the presence and absence of analyte were calculated using Equation 1. In every case, the fluorescence modulation values were greater than 1, indicating an enhancement in the fluorescence emission of fluorophore 9 upon introduction of analytes (see Tables S3–S5 in the Electronic Supporting Information (ESI) for more details). The conductivity differences between the snow samples (Newport > Kingston > Providence) led to variable differences in the degree of fluorescence modulation. We discovered in our previous work that higher conductivity, corresponding to a greater salt concentration, influences inclusion complexation [57]. Generally, the fluorescence modulation values were higher in the Newport snow samples, likely due to an increase of favourable hydrophobic interactions. The fluorescence emission of fluorophore 9 in the presence of cyclodextrin hosts is greatest in the presence of methyl-β-cyclodextrin, followed by 2-hydroxypropyl-β-cyclodextrin, β-cyclodextrin, and phosphate-buffered saline. This is due to the ability of the cyclodextrin hosts to tightly bind fluorophore 9 in the cavity via hydrogen-bonding interactions, which decreases the accessibility of non-radiative decay pathways. The fluorescence modulation ratios in the presence of cyclodextrin increased only slightly due to attenuated interactions between the fluorophore and analyte, as noted by the low binding-constant values (Table 2) [58,59]. These slight increases can be attributed to the competitive binding with long-chain alkanes. For comparison, the binding constant of heptanol is an order of magnitude higher than for BTEXC compounds in β-cyclodextrin, although pure hydrocarbon alkanes are expected to have decreased affinities, more directly in line with the BTEXC compounds. Fluorescence modulation ratios are greater in the absence of cyclodextrin due to the greater opportunity for hydrogen bonding and π-stacking interactions between the aromatic analytes and fluorophores, leading to a greater enhancement in fluorophore emission. While the fluorescence modulation ratios are higher in the absence of cyclodextrin, it is important to note that fluorescence emission was generally higher in the presence of cyclodextrin compared to in the absence of cyclodextrin, as we have seen in our previous work [60]. These results demonstrate that the fluorescence emission was influenced by the sample matrix and cyclodextrin identity, which in turn affects the interactions of the fluorophore with the aromatic analytes investigated (Figure 7).

3.3.2. Array-Based Analysis of Analyte-Doped Snow Samples

In addition to determining differences in the composition of the snow samples through measuring differences in the fluorescence response patterns, the ability to detect analytes selectively within these complex mixtures is expected to provide significant practical benefits. To that end, the selectivity of the system was determined using array-based analysis of the fluorescence responses of analyte 9 under the different experimental conditions. Linear discriminant analysis of the integrated fluorescence emission of fluorophore 9 using β-cyclodextrin, methyl-β-cyclodextrin, and 2-hydroxypropyl-β-cyclodextrin as predictors, led to 100% differentiation between analytes 1–8, which had significant structural similarity in every snow sample targeted (Figure 8).
When the same linear discriminant analysis procedure was repeated using two predictors rather than three, the selectivity of the system decreased, albeit relatively modestly (Figure 9), with the decrease dependent on the identity of the two predictors that remained. When the two predictors were two different cyclodextrin hosts (β-cyclodextrin and methyl-β-cyclodextrin), the ability of the system to differentiate between structurally similar analytes decreased from 100% to 97% (Figure 8C vs. Figure 9A). When the two predictors were β-cyclodextrin and PBS, the ability of the system to differentiate between structurally similar analytes decreased to 91%. These results indicate that three predictors provide maximum separation, but two predictors can also lead to reasonable separation between structurally similar analytes. The lower selectivity observed when one of the two predictors was PBS compared to the selectivity observed with two cyclodextrin hosts indicates that cyclodextrin hosts are better than PBS at enabling that selectivity to occur.
Additionally, the differences in sampling location were also detectable using array-based analysis. By comparing the fluorescence response patterns of structural isomers 4–6 in the three snow melt samples and in deionized water (Figure 10), 96% separation of signals for each isomer in the different complex environments was observed.
In addition to being able to differentiate single components with high levels of accuracy, the ability to accomplish detection of toxicant mixtures in complex environments has significant additional benefits. To that end, linear discriminant analysis was performed on fluorescence responses of mixtures of analytes 4–6 in Kingston snow and in deionized water, and results of these experiments can be seen in Figure 11. Array-based analysis of the response patterns led to 100% differentiation between the analyte mixtures in both the complex environment of Kingston snowmelt and in the less complex environment of deionized water. Interestingly, the single-component analytes grouped together in both samples, with analyte mixtures appearing on the opposite side of the array. Current efforts in our laboratory are focused on understanding this grouping pattern and on applying our system to additional mixtures of structural isomers in complex environments.

3.3.3. Limit of Detection Experiments

In addition to obtaining high selectivity for both single-component analytes as well as analyte mixtures, high sensitivity is also required. The sensitivity of the system was determined by calculating limits of detection for analytes 1–7 in each snow sample, using methyl-β-cyclodextrin as a supramolecular host (see Tables S8–S10 in the ESI for more details). Methyl-β-cyclodextrin was chosen as the host for these experiments because it generally led to the highest degree of fluorescence modulation, suggesting strong steric complementarity between the host and guest and concomitant sensitivity to the addition of small amounts of analyte. LODs ranged from 4.02 µM to 63.03 µM. In general, limits of detection were higher than in our previously investigated analytes or matrices, which could be attributed to the general complexity of the snow samples, specifically the fact that significant amounts of other organic components can complicate detection results.
Array-based analysis was also applied to different concentrations of analyte 1, with the goal of developing quantitative array-based detection schemes (Figure 12). Of note, this array led to 100% differentiation between different concentrations of analyte 1 in Providence snow melt, meaning that relatively small differences in the concentration of analyte 1—in the concentration range of 25 µM to 148 µM—could be differentiated successfully by using array-based analysis. Future work in our laboratory will be focused on differentiating between lower concentrations of analytes at and near the measured detection limits, and on extending these results to detect other analytes quantitatively.

3.4. Conclusions

Cyclodextrin-promoted fluorescence modulation was used for the detection of BTEXC compounds in fuel-contaminated snow samples. This method was successful in differentiating between: the sites of snow melt; structurally similar analytes in each of the snow samples, including structural isomers ortho-, meta-, and para-xylene; and in different concentrations of a single target analyte in a complex snow sample. Future work in our laboratory will be focused on expanding the array-based detection technique to quantify more analytes in complex samples, and on improving selectivity in the differentiation of structural isomers to achieve 100% selectivity.

Supplementary Materials

The following are available online at https://www.mdpi.com/2227-9040/7/1/5/s1, Supplementary information contains summary tables and summary figures for all experiments.

Author Contributions

This manuscript was written through contributions of all authors. D.J.D. designed the experiments. L.E.I., A.H., and S.B.D. performed the experiments. D.J.D. and M.L. analyzed the data; D.J.D. and M.L. wrote the paper. All authors have given approval to the final version of the manuscript.

Funding

Funding is acknowledged from the University of Rhode Island Chemistry Department and the Rhode Island Idea Network of Biomedical Research Excellence (RI-INBRE; grant # P20GM103430).

Acknowledgments

We would also like to thank Teresa Mako, a graduate student at the University of Rhode Island, for collecting the Providence snow melt sample.

Conflicts of Interest

The authors declare no conflict of interest.

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Figure 1. Scheme of cyclodextrin-promoted fluorescence modulation. This figure shows one possible complexation mode in which both the fluorophore and analyte are bound in the cyclodextrin. Other complexation modes are possible.
Figure 1. Scheme of cyclodextrin-promoted fluorescence modulation. This figure shows one possible complexation mode in which both the fluorophore and analyte are bound in the cyclodextrin. Other complexation modes are possible.
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Figure 2. Structures of analytes 1–7, control analyte 8, and fluorophore 9.
Figure 2. Structures of analytes 1–7, control analyte 8, and fluorophore 9.
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Figure 3. Map of snow sampling locations. The black marker represents Newport snow, the red marker represents Providence snow, and the blue marker represents Kingston snow. The map has been digitally manipulated so that only the state of Rhode Island is in focus.
Figure 3. Map of snow sampling locations. The black marker represents Newport snow, the red marker represents Providence snow, and the blue marker represents Kingston snow. The map has been digitally manipulated so that only the state of Rhode Island is in focus.
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Figure 4. Gas chromatography – mass spectrometry (GC-MS) overlay of snow samples, where the black line represents Newport snow, the red line represents Providence snow, and the blue line represents Kingston snow.
Figure 4. Gas chromatography – mass spectrometry (GC-MS) overlay of snow samples, where the black line represents Newport snow, the red line represents Providence snow, and the blue line represents Kingston snow.
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Figure 5. Comparison of the fluorescence response of undoped snow samples with fluorophore 9 (λex = 460 nm) with (A) β-cyclodextrin; (B) methyl-β-cyclodextrin; (C) 2-hydroxypropyl-β-cyclodextrin; and (D) phosphate-buffered saline. The black line represents Newport snow, the red line represents Providence snow, and the blue line represents Kingston snow.
Figure 5. Comparison of the fluorescence response of undoped snow samples with fluorophore 9 (λex = 460 nm) with (A) β-cyclodextrin; (B) methyl-β-cyclodextrin; (C) 2-hydroxypropyl-β-cyclodextrin; and (D) phosphate-buffered saline. The black line represents Newport snow, the red line represents Providence snow, and the blue line represents Kingston snow.
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Figure 6. Array response patterns using linear discriminant analysis of fluorescence response signals of fluorophore 9 in undoped snow melt samples, with cyclodextrins as predictors.
Figure 6. Array response patterns using linear discriminant analysis of fluorescence response signals of fluorophore 9 in undoped snow melt samples, with cyclodextrins as predictors.
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Figure 7. Fluorescence changes of fluorophore 9 (λex = 460 nm) with (A) analyte 1 with β-cyclodextrin; (B) analyte 1 with phosphate-buffered saline; (C) analyte 8 with β-cyclodextrin; and (D) analyte 8 with phosphate-buffered saline in the different sampling locations. The black line represents Newport snow, the red line represents Providence snow, the blue line represents Kingston snow, and the purple line represents deionized water.
Figure 7. Fluorescence changes of fluorophore 9 (λex = 460 nm) with (A) analyte 1 with β-cyclodextrin; (B) analyte 1 with phosphate-buffered saline; (C) analyte 8 with β-cyclodextrin; and (D) analyte 8 with phosphate-buffered saline in the different sampling locations. The black line represents Newport snow, the red line represents Providence snow, the blue line represents Kingston snow, and the purple line represents deionized water.
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Figure 8. Linear discriminant analysis of fluorescence responses of analytes 1–8 with fluorophore 9 in (A) Newport snow; (B) Providence snow; (C) Kingston snow; and (D) deionized water, using cyclodextrins as predictors.
Figure 8. Linear discriminant analysis of fluorescence responses of analytes 1–8 with fluorophore 9 in (A) Newport snow; (B) Providence snow; (C) Kingston snow; and (D) deionized water, using cyclodextrins as predictors.
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Figure 9. Linear discriminant analysis of fluorescence response patterns of analytes 1–8 with fluorophore 9 in Kingston snow, with (A) β-cyclodextrin and methyl-β-cyclodextrin as predictors, as well as (B) β-cyclodextrin and phosphate-buffered saline as predictors.
Figure 9. Linear discriminant analysis of fluorescence response patterns of analytes 1–8 with fluorophore 9 in Kingston snow, with (A) β-cyclodextrin and methyl-β-cyclodextrin as predictors, as well as (B) β-cyclodextrin and phosphate-buffered saline as predictors.
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Figure 10. Linear discriminant analysis of fluorescence response patterns of analytes 4–6 with fluorophore 9 in Newport snow, Providence snow, Kingston snow, and deionized water, with cyclodextrins as predictors.
Figure 10. Linear discriminant analysis of fluorescence response patterns of analytes 4–6 with fluorophore 9 in Newport snow, Providence snow, Kingston snow, and deionized water, with cyclodextrins as predictors.
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Figure 11. Linear discriminant analysis of mixtures of analytes 4–6 with fluorophore 9 in (A) Kingston snow and (B) deionized water, with cyclodextrins as predictors.
Figure 11. Linear discriminant analysis of mixtures of analytes 4–6 with fluorophore 9 in (A) Kingston snow and (B) deionized water, with cyclodextrins as predictors.
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Figure 12. Array-based detection of various concentrations of analyte 1 with fluorophore 9 in Providence snow, with cyclodextrins as predictors.
Figure 12. Array-based detection of various concentrations of analyte 1 with fluorophore 9 in Providence snow, with cyclodextrins as predictors.
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Table
Table 1. pH and conductivity data for sampling locations.
Table 1. pH and conductivity data for sampling locations.
Sampling LocationpH aConductivity (µs/cm) b
Newport6.48713
Providence6.08101
Kingston6.46584
a pH values were obtained using a MicroLab FS-522 instrument with a pH probe calibrated using Fisherbrand pH 4, 7, and 10 buffer solutions. b Conductivity values were obtained using a Thermo Scientific Orion 3-Star Benchtop Conductivity Kit.
Table
Table 2. Literature-reported binding constants of analytes 1–7 with β-cyclodextrin a.
Table 2. Literature-reported binding constants of analytes 1–7 with β-cyclodextrin a.
CompoundBinding Constant (M−1)
1121
2287
3435
4305
5210
6353
7b
Heptanol1000 [61]
a Binding constant values obtained from Kfoury, 2018. b No binding constant value obtained.

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DiScenza, D.J.; Intravaia, L.E.; Healy, A.; Dubrawski, S.B.; Levine, M. Fluorescence-Based Detection of Benzene, Toluene, Ethylbenzene, Xylene, and Cumene (BTEXC) Compounds in Fuel-Contaminated Snow Environments. Chemosensors 2019, 7, 5. https://doi.org/10.3390/chemosensors7010005

AMA Style

DiScenza DJ, Intravaia LE, Healy A, Dubrawski SB, Levine M. Fluorescence-Based Detection of Benzene, Toluene, Ethylbenzene, Xylene, and Cumene (BTEXC) Compounds in Fuel-Contaminated Snow Environments. Chemosensors. 2019; 7(1):5. https://doi.org/10.3390/chemosensors7010005

Chicago/Turabian Style

DiScenza, Dana J., Lauren E. Intravaia, Anna Healy, Sage B. Dubrawski, and Mindy Levine. 2019. "Fluorescence-Based Detection of Benzene, Toluene, Ethylbenzene, Xylene, and Cumene (BTEXC) Compounds in Fuel-Contaminated Snow Environments" Chemosensors 7, no. 1: 5. https://doi.org/10.3390/chemosensors7010005

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