# Atmospheric Degradation of Perfluoro-2-methyl-3-pentanone: Photolysis, Hydrolysis and Hydration
Derek A. Jackson, † 

## Cora J. Young, † 

## Michael D. Hurley, ‡ 

## Timothy J. Wallington, ‡ 

## and Scott A. Mabury*, †

† Department of Chemistry, University of Toronto, 80 St. George Street, Toronto, ON, Canada M5S 3H6

‡ Ford Motor Company, Mail Drop SRL-3083, Dearborn, Michigan, 48121 United States 

# b S Supporting Information



### ’ 

### INTRODUCTION

Perfluorinated carboxylic acids (PFCAs) are ubiquitous in biotic 1 and abiotic environments. 2,3 Longer-chain (>C 8 ) PFCAs are bioaccumulative 4 and have attracted substantial research interest. Precipitation measurements by Scott et al. 3 have demonstrated that short-chain PFCAs, notably tri fluoroacetic acid (TFA) and perfluoropropionic acid (PFPrA), dominate the PFCA pro file. Although these smaller compounds are not expected to bioaccumulate and are not believed to represent a threat to ecosystems, their source is unclear and requires study. Thermolysis of fl uoropolymers has been suggested as a potential source of TFA observed in rainwater. 5 Other sources of TFA include the atmospheric oxidation of hydro fl uorocarbons 6,7 and polyfl uorinated compounds. 8,9 Small yields of PFPrA have been proposed from thermolysis of fl uoropolymers and atmospheric oxidation of fl uorotelomer alcohols 5,8,9but do not explain the levels of PFPrA observed in precipitation.

Perfluoro-2-methyl-3-pentanone (PFMP) is a fi re protection fluid, marketed as Novec 1230 by 3M. It is a replacement for chloro fluorocarbons (CFCs) and Halons, which deplete stratospheric ozone. The atmospheric lifetime of PFMP from previous work seems to be determined by photolysis and is approximately 1 week. 10,11 PFMP does not contribute to stratospheric ozone depletion and has a negligible global warming potential. 10,11 The major photolysis products are CF 3 C(O)F and COF 2 . 10 The atmospheric fate of CF 3 C(O)F is hydrolysis to yield TFA. It is possible that chemistry in remote environments following the photolysis of PFMP would give small yields of PFPrA or isoperfluorobutanoic acid ( i -PFBA) via reactions of the corresponding perfluoroacyl radicals with HO 2 radicals. 12,13

In addition to photolysis, hydration or abiotic hydrolysis may be a signifi cant sink of PFMP in the environment. In the hydration reaction, PFMP would react either reversibly or irreversibly with water to form a geminal diol which would shut down the photolysis pathway. Ketones are typically unreactive toward hydrolysis because the leaving group after nucleophilic attack is an aliphatic carbanion. Carbanions are highly basic and are not good leaving groups. However, hydrolysis of PFMP gives

Special Issue: Perfluoroalkyl Acid

Received: December 28, 2010 Accepted: March 25, 2011 Revised: March 15, 2011 ABSTRACT: Perfluorinated carboxylic acids are widely distributed in the environment, including remote regions, but their sources are not well understood. Perfluoropropionic acid (PFPrA, CF 3 CF 2 C(O)OH) has been observed in rainwater but the observed amounts can not be explained by currently known degradation pathways. Smog chamber studies were performed to assess the potential of photolysis of per fluoro2-methyl-3-pentanone (PFMP, CF 3 CF 2 C(O)CF(CF 3 ) 2 ), a commonly used fi re- fi ghting fluid, to contribute to the observed PFPrA loadings. The photolysis of PFMP gives CF 3 CF 2 C 3 (O) and

3 CF(CF 3 ) 2 radicals. A small (0.6%) but discernible yield of PFPrA was observed in smog chamber experiments by liquid chromatography

 mass spectrometry

o ffline chamber samples. The Tropospheric Ultraviolet

 Visible (TUV) model was used to estimate an atmospheric lifetime of PFMP with respect to photolysis of 4

 14 days depending on latitude and time of year. PFMP can undergo hydrolysis to produce PFPrA and CF 3 CFHCF 3 (HFC-227ea) in a manner analogous to the Haloform reaction. The rate of hydrolysis was measured using 19 F NMR at two diff erent pHs and was too slow to be of importance in the atmosphere. Hydration of PFMP to give a geminal diol was investigated computationally using density functional theory. It was determined that hydration is not an important environmental fate of PFMP. The atmospheric fate of PFMP seems to be direct photolysis which, under low NO
x conditions, gives PFPrA in a small yield. PFMP degradation contributes to, but does not appear to be the major source of, PFPrA observed in rainwater.a perfluorinated carbanion which, because the fluorine atoms stabilize the departing carbanion through hyperconjugation, is a much better leaving group. This e ffect is the basis of the wellknown Haloform reaction, one of the oldest organic reactions known. 14

Applying the Haloform reaction mechanism to hydrolysis of PFMP should give PFPrA and CF 3 CFHCF 3 (HFC-227ea). HFC-227ea is a long-lived greenhouse gas and its formation would be problematic. A detailed understanding of the rate and products of PFMP hydrolysis under environmentally relevant conditions is clearly desirable.

The present work had three goals: (i) to con firm the rate of atmospheric photolysis of PFMP and to investigate the possible formation of PFPrA, (ii) to determine whether hydrolysis of PFMP is of signifi cance in the environment, and (iii) to investigate whether hydration is an environmental fate of PFMP.



### ’ 

### EXPERIMENTAL DETAILS

Measurements of UV Spectra and Calculations of Photolysis Rates. UV spectra of PFMP in the region 200

 400 nm were recorded in a 6-cm cell using a Perkin-Elmer UV/vis spectrometer with a resolution of 1 nm, a slit width of 0.25 nm, and a scan speed of 15 nm min
 1 . Photolysis rates were estimated using the Tropospheric Ultraviolet

 Visible (TUV 4.2) package. 15 All rates were calculated for 0.5 km above the surface. The quantum yield was assumed to be 0.043, as measured by D ’Anna et al. 11

Smog Chamber Methods. Experiments were performed in a 140-L Pyrex reactor interfaced to a Mattson Sirus 100 FTIR spectrometer. The reactor was surrounded by 10 fluorescent blacklamps (GE F15T8-BL, maximum emission 360 nm) and 12 sunlamps (GE-FS40, maximum emission 310 nm), which were used to photolyze PFMP. The spectral overlap of the emission of blacklamps and sunlamps and the absorption by PFMP has been discussed by Taniguichi et al. 10 All reagents were obtained from commercial sources. Concentrations of reactants and products were monitored by FTIR spectroscopy. IR spectra were derived from 32 coadded interferograms with a spectral resolution of 0.25 cm  1 and an analytical path length of 27 m. Photolysis experiments were performed using mixtures containing 0.49

 0.62 Torr of PFMP in 50 Torr of oxygen. We chose a diluent pressure of 50 Torr for the photolysis experiments as Taniguichi et al. 10 have established that the photolysis proceeds more rapidly at lower total pressures. After photolysis the reaction mixtures were pressurized to 750 Torr with air and sampled as described below.

The experimental conditions employed in the smog chamber experiments (296 K, 50 Torr total pressure of O 2 diluent, in the absence of water vapor, NO
x, and other important atmospheric constituents) are not the same as the range of conditions in the real atmosphere. However, the chemical processes studied in the chamber are very similar to those which will occur in the real atmosphere. Photolysis of PFMP in the chamber will occur via the same mechanism, the fate of the radicals formed (decomposition and addition of O 2 ) will be similar, and subsequent reactions of the peroxy radicals are similar to those in the real atmosphere. Hence, the results from such smog chamber experiments shed important light on the behavior of PFMP in the real atmosphere.

Offline Sample Collection and Analysis. Offline samples were collected by bubbling approximately 5 L of chamber air through 10 mL of sodium carbonate solution (pH 11) after dilution of the chamber contents with air ( P T = 750 Torr).Triplicate samples were collected following 45 min of irradiation. Sodium carbonate solutions were acidified to pH 4 using HCl and analyzed using a Waters 616 LC pump and 600 controller with detection by a Micromass Quattro Micro MS/ MS detector. Analytes were separated on a Genesis C8 column (2.1 mm  50 mm  4 μ m) using a 5-min isocratic run of 40% methanol and 60% water, both containing 10 mM ammonium acetate. Triplicate 10 μ L injections were made using a Waters 717 autosampler. PFCAs were analyzed using a cone voltage of 17 V and collision energy of 9 eV and the following transitions were monitored: PFBA 213 > 169, PFPrA 163 > 119, and TFA 113 > 69. Analytes were quantified using external calibration.

Hydrolysis Kinetic Experiments. To quantify the rate of PFMP hydrolysis and identify the final products of hydrolysis,
19 F NMR was used. The rates of hydrolysis were measured at pH values of 5.6 anad 8.5 to simulate the upper and lower boundaries of realistic environmental pH conditions. To achieve this, either 50 mM potassium hydrogen phthalate (pH 5.6) or 50 mMsodium borate (pH 8.5) buffer was used. A Varian 400 spectrometer equipped with an ATB8123-400 autoswitchable probe tuned to 19 F (376.14 MHz) was used. Reaction solutions were composed of 600 μ L of buffer solution and 200 μ L of D 2 O in a 5-mm NMR tube. Immediately prior to sample insertion, 20 μ L of PFMP was added to the NMR tube followed by inversion. Reaction kinetics were followed by acquiring NMR spectra using a preacquisition delay program such that one complete spectrum was obtained every 20

 30 min. Each spectrum consisted of 12 scans with an acquisition time of 1 s. To ensure quantitive results, a standard of PFPrA under the same reaction conditions as PFMP hydrolysis was subject to a pulse inversion

 recovery T 1 relaxation experiment to determine a suitable relaxation delay time for PFMP. In this case, a delay time of 20 s for PFMP was chosen. After acquisition, data analysis was performed using the VnmrJ software (Agilent Technologies) as it possesses a built-in kinetic analysis module. Each arrayed spectrum was Fourier transformed with a line broadening apodization of 6 Hz to improve its signal-to-noise ratio. Kinetic data were obtained by fitting an exponential growth or decay function to thefluorinated signals in the NMR spectra (see Figure S5, Supporting Information). All hydrolysis experiments were performed
at 25  C.

Computational Method. Calculations to determine the significance of PFMP hydrat ion were performed using the Gaussian 03 program 16 with the WebMO interface. All computations were performe d using Density Functional Theory (DFT) with B3LYP functionals using the 6-311G(d,p) basis set. Computations were carried out for both the gas phase and the aqueous phase using a polarizable continuum solvent model (PCM). 17 Equilibrium constants for hydrationwere computed using the relative method of GomezBombarelli et al. 18 and using a training set calibration of fluoroacetone, trifluoroaceto ne, and hexafluoroacetone (see SI for details).

Reagents. All chemicals were used as received. PFMP was purchased from Synquest Laboratories (Alachua, FL). Disodium tetraborate and potassium hydrogen phthalate were purchasedfrom BDH (Toronto, ON). Trifluoroacetic acid and heptafluoropropionic acid (PFPrA) were purchased from Sigma-Aldrich (Oakville, ON).

### ’ 

### RESULTS AND DISCUSSION
Photolysis Kinetics. Photolysis lifetimes of PFMP have been determined experimentally in two studies, yielding lifetimes of approximately 1

 2 weeks 10 and 1 week. 11 Using the flux conditions and quantum yield (0.043) previously described, 11 and the UV spectrum measured in this study (see SI), photolysis rates for PFMP were estimated. The photolysis rates, presented in Table 1, agree to within a factor of 2 with those reported in previous studies as well as previous measurements of the UV spectrum. 10,11 The 24-h averaged rate constants for photolysis of PFMP for different latitudes are given in the SI. Annual averaged photolytic rate constants ( J) ranged from 3.1  10  6 to 8.2  10  7 s  1 corresponding to lifetimes of 4

 14 days depending on latitude and time of year.

Photolytic Production of PFCAs under Low NOx Conditions. Offline samples were take n to determine if photolytic degradation of PFMP could yield PFCAs. The formation of PFCAs in the chamber is only expected under low-NO
x conditions in the presence of HO 2 radicals. Material was not added specifically for the purpose of forming HO 2 radicals, but it is likely that HO 2 radicals are present in small quantities in all chamber experiments because of hydrocarbon residue on the walls of the chamber (the chamber has been used at Ford for many years to study hydrocarbon oxidation mechanisms). Large initial concentrations of PFMP (520 mTorr) were used in the smog chamber to facilitate detection of small yields of PFCAs.

Photolysis of PFMP can generate two diff erent perfluoroacyl radicals:

CF 3 CF 2 C ð O Þ CF ð CF 3 Þ 2 þ hv f CF 3 CF 2 3 þ 3 C ð O Þ CF ð CF 3 Þ 2 ð 1 Þ

CF 3 CF 2 C ð O Þ CF ð CF 3 Þ 2 þ hv f CF 3 CF 2 C 3 ð O Þ þ

3 CF ð CF 3 Þ 2 ð 2 Þ

Perfluoroacyl radicals either decompose via elimination of CO or add O 2 to give perfluoroacyl peroxy radicals. In low-NO
x environments, perfluoroacyl peroxy radicals can react with HO 2 to give PFCAs: 12

CF 3 ð CF 2 Þ

x C 3 ð O Þ þ O 2 f CF 3 ð CF 2 Þ

x C ð O Þ OO 3 ð 3 Þ

CF 3 ð CF 2 Þ

x C ð O Þ OO 3 þ HO 2 f CF 3 ð CF 2 Þ

x C ð O Þ OH þ O 3 ð 4 Þ The perfluoroacyl radicals derived from the photolysis of PFMP can react to give i -PFBA or PFPrA as follows: ð CF 3 Þ 2 CFC 3 ð O Þ þ O 2 f ð CF 3 Þ 2 CFC ð O Þ OO 3 ð 5 Þ

ð CF 3 Þ 2 CFC ð O Þ OO 3 þ HO 2 f ð CF 3 Þ 2 CFC ð O Þ OH ð i- PFBA Þ þ O 3 ð 6 Þ

CF 3 CF 2 C 3 ð O Þ þ O 2 f CF 3 CF 2 C ð O Þ OO 3 ð 7 Þ

CF 3 CF 2 C ð O Þ OO 3 þ HO 2 f CF 3 CF 2 C ð O Þ OH ð PFPrA Þ þ O 3 ð 8 Þ

PFPrA was observed in o ffline samples taken after 45 min of irradiation, at a concentration of 0.061 mTorr. i -PFBA was not detected in any of the samples.

The high concentrations of PFMP used in the experiments saturated the FTIR signal and a direct determination of the amount of PFMP photolyzed was not possible. The amount ofPFMP lost via photolysis was estimated from the photolysis halflife (determined to be 26 h by the observed formation of CF 3 C(O)F as discussed previously 10 ) in the chamber conditions. We estimate that 10.4 mTorr of PFMP was photolyzed after 45 min and hence the yield of PFPrA is 0.6%. The low PFPrA yield observed in this experiment probably re fl ects the low level of Table 1. Kinetic Data for PFMP Degradation via Photolysis and Hydrolysis ( N = 2) at Two Di ff erent pH Values (For Complete Photolysis Data, Refer to the SI)

mechanism conditions rate constant k (s

 1 ) lifetime τ (hours)

photolysis 45  N 3.5  10  6 a 79.4 June 21 photolysis 45  N 5.9  10  7 a 471
December 21 photolysis 45  N 2.1  10  6 a 132 March 21/Sept 21 hydrolysis pH 5.6 1.9  10  4 ( 1  10  5 b 1.5 ( 0.1 hydrolysis pH 8.5 3.1  10  4 ( 3  10  5 b 0.9 ( 0.1

a Averaged 24 h rate constant. b Pseudo- fi rst-order rate constant.

Figure 1. Proposed mechanistic pathways leading to the formation of PFCAs after photolysis of PFMP in the absence of NO
x . Reaction numbers from the text are given in parentheses. Compounds in black boxes represent stable degradation products observed experimentally. Compounds in red boxes represent stable degradation products that were predicted but not observed.HO 2 radicals available in the system. Sulbaek Andersen et al. 19 reported that the yield of PFPrA from CF 3 CF 2 C 3 (O) via reactions 7 and 8 was 24 ( 4%. Similarly, the yield of n -PFBA in reactions analogous to 5 and 6 was shown to be 10 ( 2%. 12 We expect the yield of i -PFBA following formation of (CF 3 ) 2 CFC 3 (O) radicals in an excess of HO 2 radicals to be similar to that reported for n -PFBA. The low yield of PFPrA observed in the present experiments suggests either that the yield of CF 3 CF 2 C 3 (O) radicals in the photolysis of PFMP is low, or that the concentration of HO 2 radicals in the channel is low and conversion of CF 3 CF 2 C 3 (O) radicals into PFPrA is ine ffi cient. The absence of any discernible formation of i -PFBA suggests the latter explanation is more probable. Figure 1 illustrates some mechanistic pathways leading to PFCAs following photolysis of PFMP in the absence of NO
x . Note, as indicated in Figure 1, decomposition via elimination of CO is a signi fi cant fate of CF 3 CF 2 C 3 (O) radicals. 13

The presence of PFPrA and the absence of i -PFBA suggests reaction 2 is favored over reaction 1. This observation was surprising given the perfluoroisopropyl radical is less stable than the perfluoroethyl radical. In the perfluoroethyl radical, two fluorine atoms are able to donate electron density from their lone pair orbitals into the singly occupied p orbital on the radical center, resulting in stabilization. Because the experimental results suggest this is happening, it is proposed that the stabilities of the corresponding perfluoroacyl radicals must allow this observed regioselectivity to occur.

Hydrolysis Kinetics. The hydrolysis reaction of PFMP can proceed by the well-known Haloform reaction mechanism in which a ketone with a suitable alkyl leaving group reacts with water to form a carboxylate and an alkane.

In a typical Haloform reaction, a methyl ketone is tri-iodinated followed by treatment with base to produce a carboxylic acid and iodoform which precipitates as a yellow solid. This reaction is the classic qualitative test for a methyl ketone. The following steps mechanistically describe the Haloform reaction:

RC ð O Þ CX 3 þ OH  f RC ð O  Þð OH Þ CX 3 ð 9 Þ

RC ð O  Þð OH Þ CX 3 f RC ð O Þð OH Þ þ CX 3  ð 10 Þ

RC ð O Þð OH Þ þ CX 3  f RC ð O Þð O  Þ þ CHX 3 ð 11 Þ

where X = Cl/Br/I.

The fi nal step in the Haloform reaction is a rapid and exothermic proton transfer from the carboxylic acid to the carbanion which makes the whole process irreversible. The overall mechanism of the reaction is B AC 2 which consists ofseparate addition and elimination steps via a tetrahedral intermediate. The rate determining step is reaction 9. The fi nal twoproducts expected from PFMP hydrolysis are PFPrA and HFC227ea. The mechanism for hydrolysis of PFMP is shown in Figure 2.

The hydrolysis of PFMP and the detection of both products has been reported by Saloutina et al. 20 however this study was performed at pH values much higher than those relevant for theenvironment. The objective of the present study was to investigate whether PFMP could undergo hydrolysis at pH values more typical of those found in the environment. The two pH values chosen were 5.6 and 8.5 because pH 5.6 is typical of atmospheric

water. 21 A pH of 8.5 was also chosen to represent the upper environmental limit where hydrolysis would likely be the fastest since the Haloform reaction is base catalyzed.

To measure the kinetics of PFMP degradation, an analytical method to quantify PFMP is required. Liquid chromatography is not suitable to analyze PFMP because authentic standards would rapidly degrade in any protic solvent. It was con fi rmed in a separate study (data not shown) that PFMP reacts rapidly with methanol to produce HFC-227ea and the methyl ester of PFPrA. PFMP is certainly volatile enough to be analyzed by gas chromatography

 mass spectrometry. However aqueous samples would need to be extracted into a suitable GC solvent prior to injection. PFMP was found to have very low solubilities in almost every solvent tested. In addition, such a procedure would require a separate extraction for every time point, greatly increasing the amount of material needed. We decided that 19 F NMR would o ff er the best capability for measuring the kinetics of PFMP in situ. The hydrolysis reaction was performed in an NMR tube and scans of the reaction mixture were taken at various time intervals for subsequent analysis. 19 F NMR o ff ers acceptable signal-to-noise ratios and since neither water nor the bu ff ers used
contain fluorine atoms, a purely deuterated solvent does not need to be used. For NMR data to be considered quantitative to 99 þ % accuracy, it is necessary that the relaxation delay between scans be fi ve times that of the longest spin

 lattice relaxation time ( T 1 ) in the compound of interest. Because T 1 values can depend on the solvent used, a standard of PFPrA in the aqueous bu ff er of interest was used as a surrogate for the T 1 of PFMP. It was found that the longest observed T 1 (PFPrA) = 4.0 s, thus making a suitable relaxation delay for PFMP to be 20 s.

The current Varian NMR processing software, VnmrJ, is capable of analyzing kinetic data using a nonlinear fi tting algorithm, provided the fi t is exponential. Because the concentration of both OH
 and water are constant in each experiment, pseudofi rst-order conditions with respect to PFMP were achieved and an exponential decrease in [PFMP] is expected due to hydrolysis. After fitting the data points, the software provides the 1/e lifetime of the compound ( τ ), which is simply the reciprocal of the pseudo- first-order rate constant, k obs .

The 19 F NMR spectrum of PFMP consists of four peaks: each a multiplet due to the long-range J coupling observed for fluorineatoms. The spectra of PFPrA and HFC-227ea combined resemble that of PFMP but the chemical shifts are distinct and the coupling patterns are very diff erent. Thus, it is straightforward to distinguish PFMP from its degradation products. For examples Figure 2. Hydrolysis mechanism of PFMP to produce PFPrA and HFC-227ea under mildly basic conditions. Reaction numbers in the text are given in parentheses.of 19 F NMR spectra of both PFMP and its photolysis products, please see the SI.

In summary, we observed the 1/e lifetime of PFMP hydrolysis to vary depending on the pH of the buff er used. The reaction was faster in more alkaline solutions as shown in Table 1. This isentirely reasonable given the base-catalyzed nature of the reaction. Both PFPrA and HFC-227ea were positively identi fi ed asthe sole products of the hydrolysis reaction. PFPrA was confi rmed by comparison to an authentic standard. HFC-227ea was

con fi rmed by comparison to a literature spectrum. 22

Saloutina et al. 20 did not report any kinetics in their study on the hydrolysis of PFMP, however it is not surprising they observed high yields in PFPrA and HFC-227ea given the strongly basic conditions of their reaction solutions. A further study by the
same group 23 elaborated on the speci fi city of the C

 C bond cleavage step to exclusively produce the more stable carbanion leaving group. In the case of perfluorinated compounds, the moresubstituted anion is more stable because of increased hyperconjugation from the anion lone pair to the vicinal antibonding C

 F orbitals. Sykes et al. 24 con firmed the regioselectivity of the Haloform reaction for a number of poly fluorinated ketones. Hence, there is precedent for the Haloform reaction to occur regioselectively in fluorinated ketones to produce the less substituted carboxylate and the more substituted hydro fluoroalkane.

Hydration of PFMP. Aldehydes and ketones can react with water to produce a geminal diol by the following reaction scheme.

RC ð O Þ R 0 þ H 2 O f RC ð OH Þð OH Þ R 0 ð 12 Þ

The reaction is catalyzed by both acids and bases and is usually a reversible equilibrium reaction. For most aldehydes and ketones, the equilibrium constant, K hyd , usually strongly favors the carbonyl compound due to the high strength of the C d O bond. Exceptionally, formaldehyde (HC(O)H) exists in aqueous solution purely as the gem-diol (HC(OH)(OH)H) due to its high K hyd value (log K hyd = 3.36). 25 The vast majority of ketones are quite unreactive to hydration (acetone has log K hyd =
 2.85 25 ) and the geminal diol form is usually neglected in reactionschemes. Other exceptions can be halogenated ketones; trichloroacetaldehyde has a log K hyd = 4.45 and hexafluoroacetone- (HFA) has log K hyd = 6.08. 25 E ff ectively, there is quantitative conversion of the carbonyl to the hydrate in aqueous solution and the reverse reaction back to the carbonyl does not occur appreciably at room temperature. For example, HFA is provided commercially as the geminal diol derivative.

It might be reasonable to assume that the electron withdrawing groups of HFA impart a strong partial positive charge at the fluorinated carbonyl carbon, resulting in enhanced electrophilicity and hence, a greater degree of hydration. However, Linderman et al. 26 used Hartree

 Fock computational methods and found most of the positive electric potential in HFA is found on the CF 3 carbons and not the carbonyl carbon. Instead, they propose the lower energy level of the LUMO of fluorinated ketones compared to their hydrogenated analogs is the major cause of the enhanced reactivity toward water. Because PFMP is
perfluorinated like HFA, it would be a reasonable assumption that PFMP could rapidly and irreversibly form a geminal diol in the environment. The PFMP hydrate would not absorb actinic radiation due to the absence of the C d O chromophore. In addition, formation of the diol would increase water solubility and decrease vapor pressure, resulting in a greater rate of wet deposition and enhancing the potential role of hydrolysis. Thus, it is important to determine whether PFMP could form a stable hydrate in the same manner as HFA.

The hydration reaction of PFMP was investigated in our laboratory and no evidence of such a hydrated species was observed (data not shown). This was puzzling as other fluorinated ketones are known to hydrate readily. 25 To provide further insight, computational methods were used to estimate K hyd for PFMP and compare it to other fluorinated carbonyls using the methods of Gomez-Bombarelli et al. 18 The e ff ects of including an aqueous PCM solvent model were also studied although Guthrie et al. 27 previously noted diffi culties of applying the PCM model to halogenated compounds. For full details on the computational work, please see the SI.

Depending onthe method usedto calculate K hyd (see SI), di ff

erent values for PFMP were obtained (

 2.09 < log K hyd <

 0.43) but the range suggests hydrate formation is not signifi cant for PFMP. Given the perfluorinated nature of PFMP and that even partially fluorinated ketones such as trifluoroacetone (log K hyd = 1.54) 25 have large K hyd values we were surprised by the low values of K hyd calculated for PFMP. The computational methods used in the present study (B3LYP/6-311 þþ G(d,p)) were able to compute
K

hyd values for several fluorinated ketones ( fluoroacetone, trifluoroacetone, and hexafluoroacetone) with fairly good accuracy, providing con fi dence in the method used. A single point molecular orbital calculation on geometry-optimized PFMP in the gas phase (B3LYP/6-311 þþ G(d,p)) gave the energy level of the LUMO (

 84.1 kcal/mol) as almost identical to the LUMO of HFA (

 81.4 kcal/mol), especially when compared to the computed LUMO of acetone (

 19.3 kcal/mol). This supports the results of Linderman et al. 26 who proposed these energy diff erences as the reason for the enhanced reactivity of HFA to hydration. In the case of PFMP, steric hindrance could be thereason for its decreased hydration equilibrium constant compared to HFA. We conclude that geminal diol formation is not a signi fi cant environmental fate for PFMP.



### ’ 

### ENVIRONMENTAL IMPLICATIONS

We have investigated the potential for photolysis, hydrolysis, and hydration to contribute to the environmental fate of PFMP. As discussed in the previous section, hydration is not a signifi cant fate for PFMP. While the rate constant for hydrolysis is much greater than that for photolysis, the levels of liquid water in the atmosphere are usually very low. A typical cloud only contains approximately 3  10  7 cm 3 liquid water per mL of total volume 28 and we conclude that even at night, the amount of PFPrA and HFC-227ea produced would not be signi fi cant and that photolysis dominates hydrolysis as the atmospheric fate of PFMP. Cahill and Mackay29 came to the same conclusion in their modeling study. Interestingly, Cahill and Mackay predicted a hydrolysis rate constant at pH 5.6 of 2.2 s
 1 which is approximately 10 4 times larger than the hydrolysis rate constant we measured. Hence, our work suggests hydrolysis is an even less important fate for PFMP compared to photolysis than the ratio Cahill and Mackay 29 predicted; the ratio of rates of photolysis to hydrolysis is approximately 980,000,000:1. For full details on this calculation, please see the SI. Photolysis will always dominate over hydrolysis. It is clear the very low fraction of liquid water in the atmosphere contributes heavily to this ratio and more than

o ff

sets the higher hydrolysis rate constant. This ratio is so great that even at night time during a heavy rain event it is unlikely hydrolysis will occur to any signifi cant extent.Photolysis is the dominant mechanism by which PFMP is removed from the atmosphere. It has been established previously 10,11 that photolysis of PFMP in the presence and absence of NO
x will lead to the formation of CF 3 C(O)F in a molar yield of approximately 100%. The atmospheric fate of CF 3 C(O)F is hydrolysis to give tri fluoroacetic acid (TFA). TFAis a ubiquitous naturally occurring component of the hydrosphere and the additional burden associated with PFMP photolysis is not signi fi cant. In the present work, we also show that small amounts of PFPrA are also formed as a result of PFMP photolysis. To provide a crude upper limit estimate for the amount of PFPrA that might be expected in precipitation as a result of atmospheric degradation of PFMP we applied the following logic (see SI for details). The production of PFMP by 3 M is 100

 1000 t year  1 and began in approximately 2003. 30 Given PFMP is used entirely in fi re-protection systems that are released by an alarm, it can be considered stored emission potential with releases averaging 1

 3% year  1

. 30 Combining the upper limit of production (1000 t year

 1 ) with a 3% emission factor provides an upper limit of 30 t of PFMP released into the atmosphere each year. Reactions subsequent to the formation of CF 3 CF 2 C(O) radicals in air in the presence of excess HO 2 give PFPrA in a molar yield of 24%. 12 Using a simple model (see SI), and assuming the photolysis of PFMP proceeds exclusively via reaction 2, we derive an upper limit of 0.6 ng L
 1 for the average concentration of PFPrA in precipitation resulting from PFMP oxidation. Perfluoropropionic acid has been detected in rainwater at several sites in North America at concentrations on the order of 1

 10 ng L  1 and these levels have yet to be explained. 3 The photolysis of PFMP contributes to, but does not appear to be the major source of, PFPrA observed in precipitation.



### ’ 

### ASSOCIATED CONTENT 

# b S Supporting Information. All computational experiment methodologies, photolysis rate constants from the TUV model, full modeling calculations on the environment fate of PFMP, 19 F NMR spectra, and the UV

 vis spectrum of PFMP. This material is available free of charge via the Internet at http://pubs.acs.org.



### ’ 

### AUTHOR INFORMATION
Corresponding Author *Phone: 416-978-1780; e-mail: smabury@chem.utoronto.ca.



### ’ 

### ACKNOWLEDGMENT

We thank Prof. Mark Taylor and Dr. Mima Staikova for assistance in the computational modelling. Funding to D.A.J. was provided through an Ontario Graduate Scholarship. Funding to C.J.Y. was provided by an NSERC Canada Graduate Scholarship.



### ’ 

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