A dual-wavelength photothermal aerosol absorption monitor: design, calibration and performance
- 1Haze Instruments d.o.o., Ljubljana, Slovenia
- 2Department of Condensed Matter Physics, Jozef Stefan Institute, Ljubljana, Slovenia
- 3Center for Atmospheric Research, University of Nova Gorica, Nova Gorica, Slovenia
- 4Faculty for Mathematics and Physics, University of Ljubljana, Ljubljana, Slovenia
- 5Advanced Materials Department, Jozef Stefan Institute, Ljubljana, Slovenia
- 6Department for Analytical Chemistry, National Institute of Chemistry, Ljubljana, Slovenia
- 7GEMMA Center, University of Milano-Bicocca, Milan, Italy
- 8Institute for Sensors and Electronics, University of Applied Sciences Northwestern Switzerland, Windisch, Switzerland
- 9Federal Institute of Metrology METAS, Bern, Switzerland
- 10Experimental Aerosol & Cloud Microphysics, Leibniz Institute for Tropospheric Research, Leipzig, Germany
Correspondence: Luka Drinovec (firstname.lastname@example.org)
There exists a lack of aerosol absorption measurement techniques with low uncertainties and without artefacts. We have developed the two-wavelength Photothermal Aerosol Absorption Monitor (PTAAM-2λ), which measures the aerosol absorption coefficient at 532 and 1064 nm. Here we describe its design, calibration and mode of operation and evaluate its applicability, limits and uncertainties. The 532 nm channel was calibrated with ∼ 1 µmol mol−1 NO2, whereas the 1064 nm channel was calibrated using measured size distribution spectra of nigrosin particles and a Mie calculation. Since the aerosolized nigrosin used for calibration was dry, we determined the imaginary part of the refractive index of nigrosin from the absorbance measurements on solid thin film samples. The obtained refractive index differed considerably from the one determined using aqueous nigrosin solution. PTAAM-2λ has no scattering artefact and features very low uncertainties: 4 % and 6 % for the absorption coefficient at 532 and 1064 nm, respectively, and 9 % for the absorption Ångström exponent. The artefact-free nature of the measurement method allowed us to investigate the artefacts of filter photometers. Both the Aethalometer AE33 and CLAP suffer from cross-sensitivity to scattering – this scattering artefact is most pronounced for particles smaller than 70 nm. We observed a strong dependence of the filter multiple scattering parameter on the particle size in the 100–500 nm range. The results from the winter ambient campaign in Ljubljana showed similar multiple scattering parameter values for ambient aerosols and laboratory experiments. The spectral dependence of this parameter resulted in AE33 reporting the absorption Ångström exponent for different soot samples with values biased 0.23–0.35 higher than the PTAAM-2λ measurement. Photothermal interferometry is a promising method for reference aerosol absorption measurements.
Absorption of sunlight by aerosols, especially black carbon, and the related (semi)indirect effects of these aerosols are collectively the second leading cause of atmospheric warming (Bond et al., 2013). The same light-absorbing aerosols have serious detrimental health effects (Janssen et al., 2011, 2012). They can be directly emitted into the atmosphere (primary aerosols – black carbon and a fraction of the light-absorbing organic aerosols) or produced in the atmosphere from precursor gases (secondary aerosols – some of the light-absorbing organic aerosols) and their optical properties changing with ageing (Saleh et al., 2013; Kumar et al., 2018). Their short atmospheric lifetime (compared to CO2) makes them an appealing target for fast abatement and is responsible for their heterogeneity. Climate models do not agree with or capture all the complexity of aerosol absorption observations (Bond et al., 2013; Samset et al., 2018). In order to quantify any reduction in atmospheric heating (Ferrero et al., 2014), aerosol absorption needs to be measured precisely and accurately in many different types of sites, especially regional background sites (Zanatta et al., 2016). Moreover, the measurement of absorption coefficient should be done at different wavelengths for understanding the direct and semi-indirect aerosol effects on the climate (Samset et al., 2018) and for determining the heating rates, the contribution of sources to these effects and the role of clouds (Ferrero et al., 2021a). The increase in absorption at lower wavelengths can be parameterized as an increased absorption Ångström exponent (AAE) compared to AAE =1 exhibited by black carbon. This increase can be due to the presence of absorbing organic aerosol (Kirchstetter et al., 2004) or organic and inorganic coatings on black carbon (Zhang et al., 2018; Virkkula, 2021). The source-specific (or combustion-efficiency-specific) AAE can be used in source apportionment of black carbon (Sandradewi et al., 2008; Zotter et al., 2017). However, the measurement of the aerosol absorption coefficient is still a challenging task.
The absorption coefficient has been most often determined using the most practical instrumentation – filter absorption photometers: the Aethalometer, the particle soot absorption photometer (PSAP), the continuous light absorption photometer (CLAP) and the multiple angle absorption photometer (MAAP) (Rosen et al., 1978; Drinovec et al., 2015; Bond et al., 1999; Ogren et al., 2017; Petzold et al., 2002), where the measurement of light attenuation in the sample-laden filter relative to the clean filter is converted to mass equivalent black carbon concentration (BC) (Petzold et al., 2013a) or the absorption coefficient. This type of measurement requires different assumptions which are hard to verify. The enhancement of absorption in the scattering filter matrix and the mass absorption cross sections are two external parameters which need to be determined. Additionally, the measurement is non-linear, and the reduction of the sensitivity due to filter loading and the cross-sensitivity to scattering are artefacts, the contributions of which are either assumed (Bond et al., 1999; Ogren et al., 2017) or measured to different extents (Petzold et al., 2002; Drinovec et al., 2015). Post-processing algorithms were developed to compensate for the loading or concentration effects (Weingartner et al., 2003; Virkkula et al., 2007; Collaud Coen et al., 2010; Hyvärinen et al., 2013). These effects are, to a degree, sample dependent, so the data analysis requires more sophisticated approaches (Drinovec et al., 2015, 2017), and an additional measurement of scattering is needed (Arnott et al., 2005; Ogren et al., 2017; Yus-Díez et al., 2021) to fully compensate for the sensitivity dependence on the sample single-scattering albedo (SSA) and other artefacts.
In situ methods (i.e. without collecting the sample on a filter) offer advantages over filter photometers, such as separate measurements of aerosol extinction and scattering coefficients, where the absorption coefficient is calculated as the difference between these two parameters, hence the name of the method extinction minus scattering (EMS). The integration of these two measurements in a single instrument (Petzold et al., 2013b) allows the measurement of these quantities for the exact same sample, and calculation of their difference yields the absorption coefficient. Thus, this method was used as a reference for filter photometer characterization (for example, Bond et al., 1999). However, this measurement is still severely restricted when measuring aerosol exhibiting high SSA, as measurement errors of several percent can result in absorption coefficient errors exceeding 100 %, which requires adherence to a strict measurement and data post-processing algorithm to minimize these errors (Modini et al., 2021). On the other hand, the fractal nature of low-SSA black carbon aerosol and the effect of this morphology on the scattering truncation correction of the nephelometer present a systematic source of error also for measurements at low SSA (Modini et al., 2021). The large errors in the determined absorption coefficient at high SSA limit the use of EMS in regional and background sites, which are necessary for the quantification of the influence of absorbing aerosols on the climate.
A direct measurement of the aerosol absorption coefficient would therefore avoid the described issues. This is possible in photoacoustic instruments – photoacoustic spectrometers (PAS), in which an air sample is drawn through the sample chamber, where it is illuminated with a powerful pump laser beam. The light absorbed by the aerosol is converted to heat, causing an increase in local temperature. Transport of heat causes changes in density, and the acoustic wave is amplified in a chamber that acts as an acoustic resonator. The pump beam is modulated, and phase-sensitive detection is used to amplify the signal over the measurement noise. Acoustic resonance amplifies the signal by orders of magnitude.
Photothermal interferometry similarly employs a modulated pump laser to heat the sample with the absorbed laser light. A second interferometric laser probes the change of the refractive index caused by light absorption and the subsequent heating and decrease in the density of the sample. The response of photothermal interferometer (PTI) to the aerosol absorption coefficient is linear. The first proposed and realized PTI instruments employed a folded Jamin interferometer due to its inherent mechanical stability and a glancing pumping geometry, where the pump beam and the probe interferometric beam overlap at an acute angle in the sample (Moosmüller and Arnott, 1996; Sedlacek, 2006; Sedlacek and Lee, 2007; Lee and Moosmüller, 2020). A novel folded Mach–Zehnder interferometric design employs a single laser for both heating and interferometric detection (Visser et al., 2020).
A photoacoustic spectrometer is conceptually similar to the PTI; both use optical excitation to heat the sample. The difference is that a PAS employs an acoustic resonator, while PTI uses an optical resonator – the interferometer. PAS needs to actively track the acoustic resonant frequency to maintain maximum sensitivity, otherwise it can experience drastic changes in sensitivity. PTI maintains the maximal sensitivity by keeping the interferometer in the quadrature point, where the sensitivity is linear with phase and the change of phase is proportional to the normalized difference of the two intensities measured by the two detectors in the Mach–Zehnder (Visser et al., 2020; and our study) or Jamin (Sedlacek, 2006) interferometers.
The photoacoustic instruments may experience systematic biases when the sample contains semi-volatile organic coatings or water. As these substances evaporate from the aerosol, the latent heat causes a reduction of the detected acoustic signal (Arnott et al., 2003; Murphy, 2009; Langridge et al., 2013). As shown theoretically in Moosmüller et al. (2009), the evaporation of semi-volatile species from the particle phase reduces the sensitivity in PAS only for particles larger than a few micrometres using typical photoacoustic design/operating parameters. We have shown in experiments with coated soot that PTI and PAS instrumentation agree (Kalbermatter et al., 2022) and that evaporation does not play a role in investigation of soot particles coated with α-pinene-derived secondary organic matter.
Measurements of the effect of absorbing aerosols on the (regional) climate cannot be performed satisfactorily without reference methods. Reference instruments can be used to calibrate simpler but ubiquitous instrumentation. Reference instrumentation needs to measure the aerosol absorption coefficient directly, accurately and precisely. The vast majority of field instrumentation for the determination of the aerosol absorption coefficient is filter photometers. It is thus crucial to calibrate their response when converting the measured attenuation coefficient into absorption and to determine the limitations of filter-based measurements. This is especially so at (regional) background measurement sites, where climate change is monitored and where measurements are taken at high SSA – this is a limitation for filter photometers (Yus-Díez et al., 2021) and also for extinction minus scattering (Modini et al., 2021).
Standardization, validation and calibration of the aerosol absorption coefficient measurement require well-defined reference samples: particles or absorbing gases (Arnott et al., 2000). The greatest advantage of in situ methods is the ability of calibration with gases (Arnott et al., 2000; Lack et al., 2006, 2012; Nakayama et al., 2015; Davies et al., 2018), while filter photometers need to be compared with each other (Müller et al., 2011; Cuesta-Mosquera et al., 2021) or with other reference instruments (Bond et al., 1999; Arnott et al., 2003) using model aerosols: fullerene soot, spark discharge particles, soot generated with controlled gas combustion and dyes, especially nigrosin (Bond et al., 1999; Schnaiter et al., 2006; Müller et al., 2011; Cuesta-Mosquera et al., 2021). The advantage of using gases for calibration is conceptual – gas concentration can be measured with great precision and accuracy, and its absorption cross section is usually well known. It is also practical – gas calibration can be performed in the field, while instruments calibrated with aerosolized particles need to be sent to a calibration laboratory as this effort requires a sophisticated setup.
Calibration with NO2 is very common, especially for climate studies, because it is usually performed at green wavelengths, where the solar spectrum features a maximum. It is also convenient experimentally thanks to the large absorption cross section of NO2 in this part of the visible spectrum. However, calibration with gases at longer wavelengths (e.g. in the red or infrared parts of the spectrum) is either extremely challenging or impossible. However, these regions are important as they allow the determination of the aerosol absorption wavelength dependence over the whole solar spectrum. This enables a conceptually simple definition of BC, separate from light-absorbing organic aerosols, which feature most of their absorption at lower wavelengths (Kirchstetter et al., 2004; Lack et al., 2008), and the conversion of the optical measurement into BC. To calibrate absorption instruments at longer wavelengths, absorbing particles can be used instead of gases, e.g. Aquadag (Foster et al., 2019), absorbing polystyrene spheres (Lack et al., 2009) and especially nigrosin (Lack et al., 2006; Bluvshtein et al., 2017; Foster et al., 2019). Nigrosin is water soluble and forms spherical aerosols, which can be well described using Mie theory. It has been shown that polydisperse nigrosin can be used for calibration (Foster et al., 2019).
This work describes a novel photothermal interferometer design, which allows for simultaneous and colocated absorption measurements at two wavelengths. The article has been divided into a number of sections to provide a thorough treatment of the instrument: firstly the physical construction of the instrument is described, with a special focus on the novel geometry of the pump and probe beams in the sample chamber. The temporal evolution of the signal measured by the photodiodes during the modulation period of the pump beam and the selection of the modulation frequency are then discussed. Subsequently a noise analysis is performed, showing the sources of noise in the instrument. Following this the operation of the interferometer and the interferometric signal is detailed. A section of the article is then dedicated to the two-wavelength calibration procedure. The linearity of the measurement is demonstrated, and the stability and noise of the instrument are determined. Finally, the results obtained with the instrument during a number of laboratory and ambient campaigns are presented.
Nigrosin (Acid black 2, Nigrosin water soluble, CAS 8005-03-6) and ammonium sulfate (Mascagnite, ReagentPlus®, CAS 7783-20-2) were obtained from Sigma-Aldrich. Aqueous solutions of nigrosin (labelled, N1–N4) and ammonium sulfate (AS1–AS3) were prepared by dissolving chemicals in ultrapure water (Milli-Q) (Table 1).
Solid nigrosin samples were prepared on microscope slides by drying the aqueous solutions of nigrosin (see sample photographs in Fig. S5.3 in the Supplement). Glass slides were first cleaned with isopropyl alcohol, and then a hydrophilic layer was produced by dipping the slide into a 4 % detergent solution (Hellmanex III) for 30 s and flushing the slide with Milli-Q water. Finally 0.2 mL of nigrosin solution was spread on a surface of approx. 6 cm2 and left to dry for 12 h.
Two bottles of 1 µmol mol−1 NO2 in synthetic air were acquired (Traceline, Messer Schweiz AG) for the calibration. Calibration of the photothermal aerosol absorption monitor (PTAAM-2λ) at 532 nm was performed by filling a 10 L Tedlar® SCV gas sampling bag (Sigma-Aldrich) with the calibration gas and connecting it to the inlet of the instrument.
2.2 Generation of NO2 reference gas mixture
Poor stability of reference gas mixtures in the nmol mol−1 range in pressurized cylinders is a well-known issue for NO2 due to its reactivity (USEPA, 2017; Flores et al., 2021). To generate dynamically SI-traceable NO2 reference gas mixtures at low amount fractions in the field, METAS developed the “traceable mobile permeation generator” (TMPG), which is based on the permeation method (Haerri et al., 2017). The main components of the TMPG are a temperature-stabilized permeation chamber, with a calibrated temperature sensor in the chamber and a calibrated mass flow meter. Calibrated permeation units are placed in the permeation chamber. At a constant temperature, the permeation rate, which here is the transfer of NO2 from the reservoir of the permeation device through its membrane, becomes stable after a stabilization time of at least 24 h. After stabilization, the NO2 reference gas mixture is continuously generated at the desired amount fraction by setting the flow of the dilution gas.
First, the permeation rate of the permeation unit (produced by Fine Metrology S.r.l.s., Italy) containing high-purity NO2 was calibrated in a magnetic suspension balance (MSB; Swiss primary reference system) at 40 and 45 ∘C at an absolute pressure of 1080 mbar in synthetic air 5.6 for several days. The permeation unit was then placed in the permeation chamber of the TMPG that mimics the conditions in the MSB. TMPG was sent to Ljubljana. After 4 d of stabilization the generated gas was used for calibration of PTAAM-2λ and CAPS NO2 monitors. After shipment back to METAS, the permeator was again analysed in MSB.
2.3 Laboratory aerosol generation
Nigrosin and ammonium sulfate aerosols were generated using the ATM 226 nebulizer (Topas GmbH, Germany) set to 4 L min−1 sample flow. The nebulizer was connected to diffusion driers to reduce relative humidity below 30 %.
2.4 Soot samples
Diesel exhaust was collected from the tailpipe of a EURO3 Volkswagen Passat 1.9 TDI at 2500 rpm. An average black carbon emission factor of 1.31 g kg−1 was previously determined for the selected vehicle (Ježek et al., 2015).
Soot generated by a miniCAST 5201 Type BC (Jing Ltd., Switzerland) was also used as a test aerosol. The physical and optical properties of the soot particles have been reported elsewhere (Ess et al., 2021).
Propane soot samples were obtained by collecting the exhaust of a portable propane burner/torch. After ignition the air inlets were closed to generate fuel-rich combustion. Because of slow sample dilution large soot agglomerates were formed.
2.5 Absorbance measurements
Absorbance of nigrosin was measured using a Shimadzu UV-3600 UV-VIS-NIR spectrophotometer (Shimadzu, Japan). Aqueous solutions of nigrosin were measured in the 10 mm path quartz cuvette. Solid nigrosin samples were placed at the entrance of the ISR-3100 integrating sphere, which collected all the transmitted illumination.
2.6 Reflectance measurements
Reflectance of nigrosin using a perpendicular beam at 520 and 1064 nm was measured to correct for the reflection losses during the absorbance measurements. Reflectance was calculated by dividing the intensity of the reflected beam with that of the incident beam.
To determine the real part of the refractive index, a measurement of the Brewster θB angle was performed at 633 and 1064 nm. Measurement was performed on a thick film of nigrosin on a glass slide.
2.7 Online instrumentation
The size distribution of the aerosol particles was measured using a scanning mobility particle sizer (TSI model 3936L75). The instrument was used with an impactor with a 0.0508 cm nozzle. Measured spectra were corrected using the diffusion and the multiple charge correction algorithms. Scattering was measured with the Aurora 4000 polar nephelometer (Ecotech, Australia) set to measure the total and back-scattering coefficient.
Two filter photometers, an Aethalometer model AE33 (Magee Scientific, USA) and a CLAP (Haze Instruments, Slovenia), were used to obtain attenuation coefficients. The AE33 features a built-in filter loading compensation algorithm (Drinovec et al., 2015) and was using the M8060 filter. The CLAP was run using the Azumi 371M filter, and the data have been compensated for manually using the algorithm by Ogren et al. (2017). For comparison with PTAAM-2λ, the AE33 data were linearly interpolated from 520 and 590 to 532 nm. The 950 nm data were extrapolated to 1064 nm using the Aethalometer's Ångström exponent.
Two NO2 monitors based on cavity ring-down spectroscopy were used to determine NO2 amount fraction. In 2020, a NO2 analyser – model T500U (Teledyne, USA) was used. In 2021, the CAPS NO2 monitor (Aerodyne research, USA) was used.
2.8 Offline instrumentation
To determine the morphology of the diesel exhaust, propane soot and nigrosin samples, a FEI HeliosNanolab 650 (Thermo Fisher Scientific, Waltham, MA, USA) scanning electron microscope (SEM) operating at 1 kV accelerating voltage was used. The samples were mounted on SEM holders with carbon tape and coated with a few nanometres of carbon to prevent charging effects.
To determine the laser stability during warmup and operation, the spectra of the 532 nm DPSS laser were measured with a spectrometer (Shamrock SR-500i, Andor) equipped with a cooled EMCCD camera (Newton DU970N, Andor).
An atomic force microscope (AFM) Nanoscope IIIa – MultiMode AFM (Digital Instruments, Santa Barbara, CA) equipped with J scanner (100 µm horizontal range) operating in contact mode was used to determine the thickness of the solid nigrosin samples. Measurements were performed by carving a groove in the thin layer of the nigrosin sample all the way down to the glass substrate and measuring the depth of the groove.
2.9 Mie calculation
Mie calculations were performed using MATLAB routines for homogeneous spheres (Mätzler, 2002).
2.10 Measurement campaigns
The presented data were collected during several measurement campaigns:
Ljubljana ambient winter campaign 2020 – duration: 26 February 2020–24 March 2020; instrumentation: the PTAAM-2λ and the AE33.
Ljubljana laboratory campaign 2020 – first PTAAM-2λ characterization campaign; instrumentation: Aurora 4000, AE33, CLAP, Teledyne NO2 monitor.
AeroTox laboratory campaign 2020 – study on the influence of coating on absorption (Kalbermatter et al., 2022); PTAAM-2λ and SMPS measurements of the uncoated CAST soot and nigrosin are used here.
Ljubljana laboratory campaign 2021 – additional PTAAM-2λ characterization measurements; instrumentation: Aurora 4000, AE33, CLAP, Aerodyne research NO2 monitor; SMPS.
The experiment setup for Ljubljana campaigns is presented in Sect. S7 in the Supplement.
3.1 The instrument setup
The dual-wavelength photothermal aerosol absorption monitor (PTAAM-2λ) uses the photothermal effect to measure aerosol absorption. A folded Mach–Zehnder interferometer is used to measure the difference of the optical path between the two interferometer beams (Fig. 1). For the probe beam a HeNe laser is coupled into a polarization-maintaining single mode fibre. The beam exits the fibre via a fibre collimator, providing a 0.25 mm diameter free-space beam, which is split into two interferometer beams within a beam-splitter block. The returning beams are combined, and the intensity is measured using silicon photodiodes PD1 and PD2 connected to the lock-in amplifier (Zurich instruments, model MFLI).
The sample cell contains pressure, temperature and relative humidity sensors. The interferometer is sealed in the enclosure to protect it from acoustic noise and pressure fluctuations. The optical path length of one of the interferometer beams is controlled by a pressure cell connected to a computer-controlled syringe pump.
A 2 W frequency-doubled Nd:YAG laser (532 nm) and a 3 W Nd:YAG (1064 nm) laser are coupled to the multimode optical fibres. Parts of these fibres are shaken by an electromagnetic actuator to homogenize the profiles of the beams exiting the fibres. The pump beams, which are modulated at different frequencies, are collimated and introduced by dichroic mirrors into the interferometer. The powers of the pump beams are monitored with photodiodes P1 and P2.
Our photothermal interferometer configuration utilizes an axicon to focus the pump beams into the sample chamber where they overlap with the probe beam (Drinovec and Močnik, 2020). The pump beams exiting the fibres are collimated and subsequently combined using two dichroic mirrors and then directed into the measuring chamber using a custom drilled mirror – two drilled holes allow the interferometer beams to pass through the mirror without interacting with the pump beam. A custom axicon, drilled to allow passage of the probe beams, is used to provide an elongated focus of the pump beams along the axis of the probe beam inside the sample cell. The diameters of the probe and pump beams in the sample cell are shown in Fig. 2. The pump beams are aligned with the probe beam using a CCD camera. During 1.5 years of instrument testing (including road shipment in excess of 3000 km to the two measurement campaigns), there was no need to realign the optics.
This setup allows for simultaneous measurement of absorption at two wavelengths in the same sample volume by modulating the probe beams at different frequencies (91 and 96 Hz, for example). The retention time of the aerosol particles in the pump beam (approx. 5 s for a 100 nm particle) is much longer compared to the duration of the modulation interval (11 ms).
For “in situ” aerosol absorption measurement the pump beam intensity should be kept low enough so that the heating does not modify the physical properties of the particles. The use of an axicon for focusing the pump beams results in a pump illumination intensity of approx. 2 W mm−2, which is much lower compared to the glancing setup (Sedlacek, 2006) and the modulated single-beam PTI (Visser et al., 2020).
3.2 Photothermal effect
When the sample air is illuminated with the pump beam, some of the light is absorbed by the gases and particles in the sample. Heat is then transferred to the surrounding air, causing an increase in temperature. This, in turn, causes a small reduction in the air refractive index. This change of the refractive index is measured as the reduction of the optical path in the folded Mach–Zehnder interferometer.
The pump beam is modulated ON or OFF with a 50 % duty cycle. When the pump beam is switched ON, there is first a linear increase in the photodiode voltage, which later starts to saturate due to increasing heat transfer to the surrounding air (Fig. 3). The exact shape of the detected voltage depends on the intensity profile of the pump beam during the heating period and the geometry of the pump and probe beams. For the pump frequencies between 90 and 100 Hz, we observed an exponential rise and decay of the detector voltage during the ON and OFF part of the modulation period. Here, we show the results obtained for nigrosin using pump lasers operating at 532 and 1064 nm. The amplitude of the 532 nm channel voltage is approximately 7-fold higher compared to the 1064 nm channel, but the shape does not change with amplitude. Therefore, nonlinearities in the instrument response can be avoided, and a lock-in amplifier can be used to measure the amplitude of the photodiode voltage.
3.3 Investigation of photothermal signal and noise
When the optical path of the interferometer changes, we observe a voltage increase on one of the photodiodes and a decrease on the other. To increase the signal-to-noise ratio, the difference between the photodiode voltages (UPD1-UPD2) is used to calculate the photothermal signal. This difference is fed to the lock-in amplifier using the pump beam modulation frequency as the reference frequency. The lock-in amplifier multiplies the signal with a sine–cosine function at the modulation frequency and filters out other frequencies; this results in two output signals, Ux and Uy, which represent the dynamic components phase-shifted by . The highest lock-in signal for the selected modulation frequency is obtained at a certain phase β, approx. 2 radians for a modulation frequency of 91 Hz. The projection of the lock-in signal is calculated as a scalar product:
The instrument response S strongly depends on the duration of the modulation period (Fig. 4). The signal increases with the duration of the modulation period but shows a saturation effect because of the increased heat transfer. In general, the measurement noise (defined as standard deviation of the 1 s data) also increases with the length of the modulation interval.
Increased noise at lower frequencies can also be observed on fast Fourier transformation of the photodiode signal (Fig. S3). Noise is highest below 10 Hz; there is a plateau between 10 and 100 Hz and increased noise between 200–300 Hz. There are also certain noise peaks, which should be avoided to reduce the measurement noise. Frequencies of 91 and 96 Hz were selected to attain the highest signal-to-noise ratio.
When there is no absorbing sample in the measurement cell, it is possible to measure an offset with the magnitude of 8 µV for the 532 nm channel and 39 µV for the 1064 nm channel. This offset is generated in phase with the measurement frequency. The main sources of the offset are electronic interaction (signal at the pump frequencies is leaked into the photodiode signal) and interaction of the pump beam with the probe beam on the shared optical elements. Variation in the offset is an additional source of measurement noise.
There are several sources of noise which are independent of the pump frequency, including the noise of probe lasers, photodiodes, sample air flow turbulence, pump laser power oscillations, mechanical resonances of the optical elements and random electronic noise. The sources of noise were investigated by comparing different experimental setups (Fig. 5).
PD – pump and probe lasers are switched OFF, and noise is generated by photodiodes and electronics.
HeNe – the HeNe probe laser is switched ON with one of the interferometer arms blocked, and measured noise comes from the variation in the HeNe laser power.
Interferometer – the HeNe probe laser is switched ON, and this is a measure of the interferometer noise.
Interferometer + flow – the HeNe probe laser is switched ON, sample flow (0.4 L min−1) is switched ON, and there is some increase in noise due to the airflow in the sample cell.
Interferometer + pump beam – probe and pump lasers and sample flow are switched ON, and the noise coming from offset variation is added.
The results show that the majority of the noise comes from the interferometer. It may be related to the vibration of the optical elements of the interferometer. For the 1064 nm channel about one-half of the noise is caused by the offset variation.
3.4 Calculation of the PTAAM-2λ signal
The response of the photothermal interferometer is highest when the interferometer is operating in the so-called quadrature point – where the difference of the optical paths between the two arms of the interferometer is exactly . The interferometer response in the quadrature point is linear, as photodiode voltages in both interferometric arms intersect at the steepest (and linear) part of the sine curve (Fig. 6). The quadrature point can be determined by performing an interferometric scan (measurement of the photodiode signal while changing the optical path difference). The pressure cell is used to regulate the optical path of one interferometer arm to maintain the interferometer in the quadrature point.
For an interferometer in the quadrature point, the lock-in signal is proportional to the amplitude of the interferometer signal UI0. It is determined from the maximum and minimum voltages for both photodiodes determined during the interferometer scan:
Because the HeNe laser intensity slowly changes with time, a special procedure to determine the instantaneous interferometer amplitude UI was developed, which holds when the interferometer is in the quadrature point:
UPD1 and UPD2 are the instantaneous photodiode signals in the quadrature point, and UPD10 and UPD20 are the photodiode signals in the quadrature point when the interferometer scan was performed. The projections of the lock-in signals for the two channels are
The absorption coefficient is calculated by dividing S with the instantaneous interferometer amplitude UI, reported at the selected pressure p0 and temperature T0, where p and T represent instantaneous conditions. The response is adjusted by the calibration constant A and the ratio between the nominal Pλ,0 and instantaneous pump laser power Pλ, separately for each channel:
The baseline offset is determined for the filtered air sample and subtracted from the total signal to provide the absorption coefficients babs, 532 nm and babs, 1064 nm:
The instrumental response depends on the overlap between probe and pump beams. After beam alignment, both channels need to be calibrated.
4.1 Calibration of the 532 nm channel
Similarly to the calibration of photoacoustic instruments (Arnott et al., 2000; Lack et al., 2006; Bluvshtein et al., 2017), we decided to use NO2 for calibration of the 532 nm channel. An absorption cross section of cm2 was determined from the measured laser spectrum and the high-resolution absorption spectrum of NO2 by Vandaele et al. (2002) (Sect. S4). An absorption coefficient of 1 µmol mol−1 NO2 at 100 kPa and 25 ∘C of 357.3 Mm−1 was obtained.
Calibration of the 532 nm channel was performed by filling the Tedlar bag (Sigma-Aldrich) with NO2 from the bottle of nominally 1 µmol mol−1 NO2 in synthetic air (Messer Schweiz AG). This procedure features much lower noise compared to connecting the instrument inlet directly to the bottle. The Tedlar bag was filled with NO2 and emptied several times to passivate the bag's inner surface. After the passivation procedure the NO2 amount fraction in the bag agreed within 1 % with the source concentration. During the offset measurement, a second Tedlar bag, filled with synthetic air, was sampled.
The measured NO2 amount fraction of different bottles with a nominal amount fraction of 1 µmol mol−1 differed up to 21 %. To reduce this uncertainty, we performed the calibration with a “traceable mobile permeation generator” (TMPG) developed by METAS (Haerri et al., 2017). The generated amount fraction of NO2 during the campaign in Slovenia was 292 nmol mol−1 with the expanded measurement uncertainty of +12 and −3 nmol mol−1 (k=2). This value was used to determine the accurate amount fractions of NO2 in the bottles used for calibration. The calibration parameter A532 nm was calculated taking into account the measured losses of NO2 and particles in the instrument sample lines.
4.2 Calibration of the 1064 nm channel
Calibration of the 1064 nm channel is more complicated as there are no appropriate absorbing gases available at that wavelength. Particles with known optical properties can be used here to transfer the calibration from the NO2 calibrated 532 nm channel to 1064 nm as proposed by Arnott et al. (2000) and Foster et al. (2019). We decided to use water-soluble nigrosin (Acid black 2, CAS 8005-03-6) because it forms spherical particles when nebulized and dried (Sect. S6). To calibrate the 1064 nm channel, the absorption ratio needs to be calculated. The absorption ratio is determined using Mie calculations based on
sphericity of nigrosin particles confirmed by scanning electron microscopy (Sect. S6),
nigrosin particle size distribution measured with SMPS,
the complex refractive index of solid nigrosin at 532 nm and 1064 nm.
With respect to the nigrosin refractive index investigation, the imaginary part can be determined from its absorbance. Absorbance measurements of both aqueous nigrosin solution and nigrosin film were conducted (Sect. S5.2 and S5.3). The absorbance of the aqueous solution of nigrosin was measured in a 1 cm path cuvette. Solid nigrosin samples were produced by drying nigrosin solution on the microscope slides. The absorbance of the solid nigrosin film on these slides was measured with an integrating sphere spectrometer. The results show large (up to ±30 %) differences in the imaginary part of the refractive index between the aqueous and solid nigrosin (Fig. 7a). This means that calculating absorption using aqueous solution data can lead to substantial systematic errors. The imaginary part of the solid nigrosin refractive index at 532 nm was determined to be 0.223, which is somewhat lower compared to 0.26 obtained by Bluvshtein et al. (2017). This difference can be attributed to the variability in the nigrosin quality provided by the manufacturer or the measurement method.
The real part of the refractive index was determined by the Brewster angle measurement on nigrosin film (Sect. S5.1). Measured values are on average 0.03 lower compared to Bluvstein et al. (2017) (Fig. 7b), which is just outside the measurement uncertainty of 0.02. The following values of the refractive index have been used for Mie calculations:
Nigrosin particles were generated using the Topas ATM 226 nebulizer with a 0.1 g L−1 nigrosin solution (sample N2) for which we obtained a number size distribution spectrum with a peak at 47 nm. Mie calculation was performed for each size channel separately and summed together to obtain the absorption coefficients at 532 and 1064 nm. The calculated absorption ratio for different particle sizes is quite flat between 15 and 300 nm (Fig. 8a). Calculation of the absorption ratio for different polydisperse distributions shows it to be stable for a wide range of sizes: for aerosolized nigrosin with a number mode size between 30 and 60 nm, there is only 2 % variation in the absorption ratio (Fig. 8b). This shows that the calibration with nigrosin is quite a robust procedure not depending greatly on the nigrosin size distribution.
During different measurement campaigns the absorption ratio was calculated for the measured nigrosin size distributions. Due to the increased measurement uncertainties for particles bigger than 400 nm, these data were not used for Mie calculation. Absorption ratio obtained with sample N2 ranged between 0.0781 and 0.0785 (Sect. S5.5). The calibration parameter A1064 nm was adjusted so that the measured absorption ratio agrees with the calculated value.
4.3 Validation of Mie calculation at 532 nm
The 532 nm channel of the PTAAM-2λ is calibrated using NO2, which allows the validation of the Mie calculation of nigrosin particle optical properties at that wavelength. The comparison was performed for several nigrosin measurements during the AeroTox 2020 and Ljubljana 2021 campaigns (Table 2). For the AeroTox campaign, the average Mie calculated absorption was 6 % while scattering was 17 % higher compared to the measurement. For the Ljubljana 2021 campaign, the average Mie calculated absorption was 24 % higher compared to the measurement, and the scattering was 26 % higher. The biases of Mie calculated absorption and scattering are similar, indicating a similar source for both parameters – the uncertainty of the SMPS measurements might play a role.
5.1 PTAAM-2λ stability and noise
Before conducting the measurement campaigns, the PTAAM-2λ was calibrated using ∼1 µmol mol−1 NO2 gas and aerosolized nigrosin particles. The same procedure was used to validate the instrument sensitivity during the Ljubljana 2020 campaign (Fig. 9a) assuming a stable NO2 amount fraction and nigrosin absorption ratio. The 532 nm channel was very stable with 1 % variation during 1 week of the campaign. For the 1064 nm channel the variation was higher at 3 % and showed a slow decline. A very stable instrument sensitivity was also obtained during the AeroTox campaign (Kalbermatter et al., 2021).
Absorption measurements with the PTAAM-2λ are performed by first measuring the filtered air to determine the baseline offset, with the procedure being performed automatically using the internal HEPA filter (Fig. 9b). This offset is later subtracted from the measurement of the sample air. During the Ljubljana 2020 campaign we measured offsets of 29 and 166 Mm−1 and standard deviations of 6 and 8 Mm−1 for the 532 and 1064 nm channels, respectively (Fig. 10a). When applying an additional external HEPA filter, the calculated absorption signal was close to zero with similar standard deviation as observed for the offset. The noise of the instrument was analysed in detail by calculating the Allan variance. The Allan plot of the instrument noise shows a peak which is characteristic for the smoothed data (Fig. 10b) and is related to the filtering functions used in the lock-in amplifier. For the 532 nm channel we observe a linear decrease in the Allan variance with τ. For the 1064 nm channel the slope is lower due to noise caused by the slow variation in the offset.
5.2 PTAAM-2λ response linearity for gas and particles
The linearity of the instrument response was tested with absorbing gases and particles. For NO2 samples with amount fraction below 1 µmol mol−1 we observed a linear response for the 532 nm channel with a R2 value of 0.9996 (Fig. 11a). The measurement at 1064 nm confirms that NO2 does not absorb at this wavelength. The linearity was also tested using nigrosin particles. Since the size distribution of the particles was stable, we were able to use the scattering coefficient as a reference parameter proportional to the particle concentration. The absorption of nigrosin particles was linear, with the scattering signal in the absorption range up to 1200 Mm−1 for the 532 nm channel and up to 100 for the 1064 nm channel (Fig. 11b), with the corresponding R2 values of 0.997 and 0.968, respectively.
Interestingly, the noise behaviour for gas measurements differs substantially from that of particle measurements (Fig. 12). There is no significant increase in noise (standard deviation at 1 s time resolution) with the NO2 amount fraction. For nigrosin particles the noise increases linearly with the absorption signal and converges toward 1 % of the signal. For NO2, light is absorbed directly by the gas, in contrast to nigrosin, for which heat is transferred from the particles to the gas. This may result in transient temperature inhomogeneities in the sample volume.
5.3 PTAAM-2λ response to scattering and absorption
Because scattering does not produce thermal effects, we do not expect photothermal instruments to be sensitive to the scattering of the sample. We generated purely scattering aerosol by nebulizing different aqueous solutions of ammonium sulfate (Fig. 13). For the 532 nm channel, we observed a constant signal of about 1.5 Mm−1 above the background. This might be caused by the presence of absorbing gases; this absorption is subtracted by the measurement of the filtered air during the offset determination, but the filtering might also remove a small part of the absorbing gases due to their adsorption on the filter fibres. For the 1064 nm channel, we observe a small negative signal which represents 0.2 % of the reported scattering coefficient.
5.4 Laboratory campaigns: the use of PTAAM-2λ as a reference instrument for correction of filter photometer artefacts
As shown, the PTAAM-2λ measures the aerosol absorption coefficient without size and scattering artefacts. This makes the instrument suitable to study optical properties of aerosols and the response of other absorption instruments, especially filter photometers. During the Ljubljana laboratory campaign in 2021, we investigated filter artefacts in the Aethalometer AE33 and CLAP. The response of the AE33 and CLAP to purely scattering aerosol was tested using aerosolized ammonium sulfate of different sizes (Fig. 14a). The scattering artefact is most pronounced for small particles (volume size mode of 50 nm) where the attenuation coefficient in green approximately equals the scattering coefficient. For larger particles it is reduced and reaches 6 % at a particle volume size mode of 122 nm. These values are higher compared to the ones in Drinovec et al. (2015), where values between 1.2 %–3.4 % were obtained for the old-type TFE-coated glass fibre filter type (Pallflex “Fiberfilm” T60A20).
Similarly to scattering, there is also a strong dependence of the filter photometer response on the size of absorbing particles. The enhancement of light absorption in the filter matrix relative to particles suspended in air is described by the multiple-scattering parameter C (Weingartner et al., 2003). For attenuation coefficient compensated for filter loading effect, it holds that The AE33 data was extrapolated to 532 and 1064 nm to match the PTAAM-2λ wavelengths, whereas for CLAP only the 532 nm signal was analysed. For both filter photometers the parameter C for soot samples (Sect. 2.4) of different sizes shows higher absorption enhancement for smaller particles compared to larger ones (Fig. 14b). The dependence of the parameter C on the size is quite steep at lower and atmospherically relevant sizes, and then it levels off. For the AE33, the parameter C decreases at 532 nm from 5.3 to 3.2 and at 1064 nm from 4.2 to 2.6 when the volume size mode increases from 100 to 500 nm. These values are higher compared to the values between 2.8 and 3.6 obtained by Bernardoni et al. (2021), Yus-Díez et al. (2021) and Ferrero et al. (2021b) at 520 and 660 nm. Similarly to our results, Bernardoni et al. (2021) and Ferrero et al. (2021b) observed higher values of the parameter C at shorter wavelengths.
The dependence of the parameter C on the wavelength results in erroneous determination of the absorption Ångström exponent in filter photometers – reporting about 0.23–0.35 higher values compared to the PTAAM-2λ (Table 3). PTAAM-2λ values of the Ångström exponent are about 0.1 lower compared to some model predictions (Scarnato et al., 2013). Optical models for soot are much more complicated compared to nigrosin because of its complex structure: loose agglomerates behave similarly to single monomers with an Ångström exponent close to 1, in contrast to compact agglomerates, which behave more like big homogenous particles, for which the Ångström exponent decreases with size (Liu et al., 2018). The exact value of the Ångström exponent of soot is still difficult to predict as the modelled absorption coefficients differ from measurements for up to 30 % (Bond and Bergstrom, 2006; Liu et al., 2020).
The dependence of the AE33 measured attenuation coefficient on the sample single-scattering albedo (SSA) was tested with an external mixture of propane soot (441 nm volume mode) and ammonium sulfate (123 nm volume mode). The experiment was performed by filling a barrel with soot at the start, followed by continuous injection of ammonium sulfate particles (Fig. 15). SSA increased from 0.25 to 0.997. There is an increase in attenuation ratio shortly after the start of the experiment, but after the filter change (at 14:28 LT) the ratio returns to the initial value, which indicates that the filter loading compensation was not working optimally for the selected sample. The second filter spot loading was lower and did not affect the measurement – the attenuation ratio shows a big increase for SSA >0.995 where the AE33 signal is more than doubled. This effect has been observed in ambient measurements when the AE33 was compared to a MAAP in three different sites (Yus-Díez et al., 2021). The increase in the ratio was more than 3-fold at regional background sites during the periods of high SSA.
5.5 Winter ambient campaign
The winter campaign was carried out in Ljubljana (Slovenia) in February and March 2020 to evaluate the PTAAM-2λ performance for ambient measurements. Absorption above 30 Mm−1 at 532 nm was measured regularly during the night (Fig. 16). During the day the absorption was lower, making it difficult to determine the Ångström exponent with a high time resolution – as the instrument was operating with a higher-than-normal noise level. Comparisons with the AE33 show similar parameter C values (Fig. 16c and d) as obtained for larger particles during the laboratory campaign. Ångström exponents in the range between 0.7 and 1.3 have been obtained, with the AE33 providing 0.35 higher AAE values. For more precise ambient measurements the instrument noise at 1 s time resolution should be reduced to 1 Mm−1 or lower.
5.6 Uncertainty analysis
The uncertainty of the measured absorption coefficient results from the calibration, method and instrumental uncertainties (Table 4). The calibration of the 532 nm channel depends strongly on the uncertainty of NO2 amount fraction in the calibrating gas mixture. The standard uncertainty of NO2 amount fraction produced by TMPG was below 2 %.
The calibration of the 1064 nm channel depends on both the uncertainty of the 532 nm channel and the uncertainty of the calculated nigrosin absorption ratio ; this parameter depends on the correct determination of the nigrosin refractive index and the measured size distribution. The uncertainties of the real part of refractive index of 0.02 and of the imaginary part of 3 % result in 2 % uncertainty of the absorption coefficient (Sect. S5.6). For well-serviced SMPS instruments, the uncertainty is below 10 % (Wiedensohler et al., 2018), and the uncertainty of the ratio of the absorption coefficients is lower, resulting in 4 % uncertainty. Instrument operation can be influenced by the scattering artefact and the presence of absorbing gases. The absorption of gases is subtracted by measurement of filtered air, but a small amount of the gas can be adsorbed to the filter material. The combined uncertainty of scattering and gases of 1 % is assessed. The final uncertainty contribution comes from the stability of the instrument response (3 %).
Combined standard uncertainties for the determination of absorption coefficients and absorption Ångström exponent are presented in the lower part of Table 4. The 1064 nm channel uncertainty (6 %) is higher compared to the 532 nm channel (4 %) due to the additional calibration step with nigrosin particles. The uncertainty of the absorption Ångström exponent (9 %) is higher compared to the absorption coefficients because of the properties of the logarithmic function. Ångström exponent depends mostly on the correct determination of nigrosin refractive index at the measurement wavelengths.
We report on the design and operation of the first dual-wavelength photothermal interferometer (PTAAM-2λ) for measurements of aerosol absorption. The instrumental design allows for simultaneous measurement of the same sample at both wavelengths.
The instrument was calibrated with NO2 at 532 nm, and the calibration was transferred to 1064 nm using aerosolized nigrosin. We were able to use Mie theory to calculate the ratio of the absorption coefficients at the two wavelengths due to the spherical shape of these particles. The comparison of this modelled absorption coefficient with the measured one for polydisperse nigrosin at 532 nm shows a 6 % and 24 % difference for the AeroTox 2020 and Ljubljana 2021 campaigns, respectively. This validates our approach.
The PTAAM-2λ is one of the few instruments able to measure aerosol absorption coefficients at high SSA. We have demonstrated the long-term stability of the instrument and shown that the determination of the absorption coefficient is artefact-free. Uncertainties of 4 %, 6 % and 9 % were determined for the absorption coefficients at 532 and 1064 nm and the absorption Ångström exponent, respectively. We have used the dual-wavelength photothermal interferometer to determine the artefacts of filter photometers and quantify their dependence on the wavelength and the aerosol size. The PTAAM-2λ shows lower AAE compared to filter photometers, demonstrating a wavelength dependence of the filter photometer multiple-scattering parameter C. We have also shown how the quantification of the filter photometer sensitivity on the aerosol size is determined and that for low SSA filter photometers perform satisfactorily if correct values of parameter C are used.
We believe that the demonstrated operation and performance make the PTAAM-2λ a strong candidate for reference measurements of the aerosol absorption coefficient.
The raw data and measurement logs are available at http://repozitorij.ung.si/Dokument.php?id=23720 (Drinovec et al., 2022). Additional related data can be made available upon request.
The supplement related to this article is available online at: https://doi.org/10.5194/amt-15-3805-2022-supplement.
LD and GM designed and developed the PTAAM-2λ. LD carried out the majority of experiments and analysed the data. EW, BV and JR provided input into the experimental design of the photothermal interferometer. UJ performed measurements of nigrosin refractive index and laser spectra. LP performed scanning electron microscopy. MŠ performed measurements with an atomic force microscope. MK performed integrating sphere measurements, and KrV performed SMPS measurements during the 2021 Ljubljana campaign. LF and UJ performed Mie calculations and quality control. DMK and KoV carried out experiments during the AeroTox 2020 campaign. TB and CP prepared and tested traceable mobile permeation generator of NO2 for PTAAM-2λ calibration. TM and AW collaborated with nephelometer measurements and calibration. LD and GM wrote the paper, with other authors providing valuable additions. All co-authors contributed to the paper discussion and revision.
Luka Drinovec, Griša Močnik and Uroš Jagodič are or were employed by Haze Instruments d.o.o., the manufacturer of the described instrument. Technologies described here-in have been protected with patents.
Publisher’s note: Copernicus Publications remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
We thank Martin Gysel (PSI) for the use of the AE33, Teledyne API and EAS Envimet Analytical Systems GmbH for the loan of the NO2 CAPS. We thank AMES d.o.o. for the technical support.
This research has been supported by the Schweizerischer Nationalfonds zur Förderung der Wissenschaftlichen Forschung (grant no. 200021_172649), Eurostars (grant no. 11386), the Javna Agencija za Raziskovalno Dejavnost RS (grant nos. P1-0385, P1-0099 and I-0033), and the European Metrology Programme for Innovation and Research (EMPIR Black Carbon and EMPIR AeroTox grants).
This paper was edited by Mingjin Tang and reviewed by three anonymous referees.
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