Over the past decade, hyperspectral infrared sounders on satellites have offered global measurements of atmospheric ammonia (NH3), providing valuable insights into its sources. However, due to their coarse spatial resolution and gaps in spatial coverage, inferring emissions from smaller sources or utilizing data from single overpasses remains very challenging. While a high-spatial-resolution imaging sounder would greatly enhance monitoring capabilities, developing an instrument that combines high spatial and spectral resolution is technologically difficult and expensive. Here, we analyze the feasibility of measuring NH3 with instruments having a largely reduced spectral coverage and resolution compared to current operational sounders. We explore the performance trade-offs using simulated spectra, measurements from the Infrared Atmospheric Sounding Interferometer (IASI) satellite sounder, and spectra obtained from aircraft. The measured spectra are degraded spectrally, and their performance is evaluated using metrics such as NH3 measurement uncertainty, signal-to-noise ratio, and false alarm rate. Instruments that measure across a continuous spectral interval and instruments covering specific well-chosen spectral bands are both examined. We demonstrate that a future dedicated NH3 sounder with as few as 3 spectral bands of 1–5 cm−1 is feasible and would enable the detection of NH3 both at high spatial resolution and across continental scales. The advantage of choosing well-defined spectral bands is demonstrated, e.g., by showing that an instrument with 5 specific bands of 5 cm−1 performs similarly to one with 20 contiguous channels across 900–1000 cm−1. Additionally, we show that at high spectral resolutions (below 5 cm−1), the NH3 measurement capability is primarily driven by the instrumental noise. As the spectral resolution or number of measurement bands decreases, spectral interferences from other atmospheric constituents and the surface start to dominate the NH3 retrieval uncertainty budget, fundamentally limiting the unambiguous identification of NH3.
Introduction
Atmospheric ammonia (NH3) plays a key role in the formation of secondary particulate matter, which leads to chronic respiratory illnesses and premature deaths . Excess NH3 also poses a significant threat to the environment, particularly through the acidification and eutrophication of ecosystems, leading to a loss of biodiversity, degradation of water and soil quality, and other environmental issues . The primary source of excess atmospheric NH3 is intensive agricultural activities, including livestock farming and the use of synthetic fertilizers .
Global measurements of NH3 are currently provided by satellites equipped with hyperspectral infrared sounders, such as the Infrared Atmospheric Sounding Interferometer (IASI; ) and the Cross-track Infrared Sounder (CrIS; ). Their measurements have provided valuable insights into the distribution and sources of NH3 in the atmosphere. In particular, they revealed that strong point sources such as animal feedlots and industrial fertilizer production facilities dominate ambient NH3. However, their spatial resolution (larger than 10 km) and non-contiguous coverage pose significant challenges for detecting smaller NH3 emission sources and quantifying emissions from single overpasses. The agricultural landscape in Europe, for instance, features hundreds of thousand of farms that are too small or too agglomerated to be quantified individually with IASI . Even future instruments, such as the IASI-New Generation (IASI-NG; ) or the hyperspectral Infrared Sounder (IRS; ), while offering considerable improvements, are not expected to provide the high spatial resolution necessary for resolving small-scale point sources. In the context of ESA's Earth Explorer 11 call, a mission called Nitrosat was proposed for measuring NH3 and nitrogen dioxide (NO2) at high spatial resolution. Within the Phase 0 studies, it was demonstrated that a dedicated sounder capable of measuring NH3 at sub-kilometer resolution within a contiguous image 80 km across track is well within the capabilities of current technology. While the immense scientific and societal benefits of such a mission are unquestionable given the major disruption to the nitrogen cycle and the damaging consequences that this entails, the proposed baseline instrument (characterized by a spectral range extending from 925 to 975 cm-1 and a resolution of 0.625 cm-1) comes at a substantial cost.
In this paper, we explore hypothetical spectrometers measuring infrared spectra at a lower spectral resolution or with a limited number of channels, and we investigate to what extent these can be used to effectively measure NH3. By compromising on spectral resolution, imagers monitoring NH3 at high spatial resolution could be developed, offering significant advantages in terms of weight, size, cost, and development time. We begin with a brief description of the data used for this study, including IASI satellite measurements and Telops Hyper-Cam airborne data (Sect. ). Following this, we discuss ways to quantify the NH3 retrieval uncertainty. We also provide a concise overview of the matched filter technique used to detect and identify NH3 features in infrared measurements, as well as the metrics used to assess the resulting distributions. In Sect. , we evaluate the performance of hypothetical instruments for measuring NH3. We first analyze simulated spectra to characterize the effects of spectral range and resolution. After that, a more comprehensive evaluation is performed using the remotely measured spectra. We evaluate the native performance of these instruments and progressively downgrade their spectra by averaging channels, allowing the analysis of instruments with coarser spectral resolution. We investigate the performance not only for instruments with continuous spectral coverage and fixed sampling, but also for instruments measuring a limited number of specific spectral bands of various widths. In the final section, we present our conclusions.
Measurements
The spaceborne data used in this study were acquired by the IASI/Metop-B instrument on 8 April 2020 (Fig. ). IASI is a passive sounder equipped with a Fourier-transform spectrometer, observing the Earth in the thermal infrared in nadir geometry. Operating in a sun-synchronous polar orbit, the satellite provides twice-daily global data, though only data from the morning overpass (around 09:30 am local time, LT) were used here. The instrument's field of view corresponds to a circular footprint of 12 km in diameter at nadir, extending elliptically up to 20×39km2 for larger viewing angles. The spectral range of IASI covers 645 to 2760 cm-1 but was limited here to 812–1126 cm-1 following the range used for the IASI NH3 retrieval algorithm . The IASI L1C data have an apodized spectral resolution of 0.5 cm-1 and are sampled at 0.25 cm-1.
We also use measurements from aerial surveys that were carried out in Italy in the spring of 2022 in the context of Nitrosat demonstration campaigns . The measurements were recorded by a Hyper-Cam LW on board a Cessna T207A aircraft. At an altitude of about 3 km, the ground instantaneous field of view for each individual pixel was about 5 m. The Hyper-Cam LW instrument, developed by Telops, is an advanced hyperspectral imaging camera employing Fourier-transform technology to deliver high-resolution spectra. Operating in the longwave infrared between 830 and 1270 cm-1, the spectrometer offers a spectral resolution ranging from 0.25 to 150 cm-1. Data from two flights are exploited here. The first one (Fig. ) measured a scene of approximately 6 by 14 km centered on the soda ash production plant in Rosignano. The production of soda ash is based on the well-known Solvay process that notably requires an input of NH3. Although a large amount is recycled in the process, a part of the NH3 is lost to the atmosphere . The NH3 emissions of the Rosignano plant were estimated to exceed 200 t in 2022 according to the European Pollutant Release and Transfer Register (E-PRTR; ). The area was surveyed on 19 May 2022, around noon. The second scene (Fig. ) was acquired on 30 June 2022 between 10:00 am and 05:00 pm LT and covered an area of 10 by 55 km between the cities of Trecasali and Vetto. The northern part of the scene is part of the Po Valley, which is Europe's largest NH3 hotspot due to intensive agricultural activities . Between 2020 and 2022, the E-PRTR listed 8 agricultural NH3 emission sources in the surveyed area. In this study, for each of the two flights, the observed pixels were averaged two by two to reduce the noise (see Appendix for the estimation of the noise), resulting in a reduction of the spatial resolution from 5 to 10 m. The native spectra are sampled at 1.3 cm−1.
Performance metrics and the matched filterMeasurement uncertainty
In nadir viewing geometry, the effect of atmospheric NH3 on observed radiances is linear for all but the largest columns . That is, the observed spectrum can be written as
y=y0+xK+ϵ,
with y0 the theoretical spectrum that would be observed in the absence of NH3 and instrumental noise ϵ, x the NH3 total column, and K=∂y∂x the Jacobian with respect to NH3. If we assume that, except for x and ϵ, we have perfect knowledge of all parameters affecting the spectrum (i.e., y0 and K are known), the generalized least-squares solution provides the following estimate for x:
x^=KTSϵ-1K-1KTSϵ-1(y-y0),
with Sϵ-1 the covariance matrix of the instrumental noise. This solution minimizes the (weighted) distance between the observed spectrum y and y0+xK in the presence of noise. The estimate x^ has an associated variance or measurement uncertainty ,
σnoise=KTSϵ-1K-1/2,
which is the propagation of the instrumental noise to x^.
In practice, the state of the atmosphere or the surface is not known perfectly. However, we can still write
y=yg+xK+g,
with now yg some reference spectrum with negligible NH3 and g a generalized noise vector, which includes both the contribution of the instrumental noise and spectral contributions related to the uncertain scene parameters. This includes, for example, unknown surface and air temperatures, or parameters that can directly interfere with the identification of the contribution of the NH3 signature in the spectrum, such as unknown water vapor abundance and surface emissivity variations. If we can estimate the covariance matrix Sg associated with yg and the Jacobian K, we can, as before, obtain a generalized least-squares estimate ,
x^=KTSg-1K-1KTSg-1(y-yg),
with uncertainty
σabs=KTSg-1K-1/2.
This solution minimizes the distance between y and yg+xK, but this time inversely weighted with a covariance matrix characterizing not only the instrumental noise but also spectral interferences. This least-squares solution can be shown to correspond to the maximum likelihood estimate in case g follows a multivariate normal distribution. Importantly, it can also be shown to be equivalent to the solution obtained by performing a simultaneous optimal estimation of the interfering spectral features . In the field of hyperspectral imaging, g is referred to as the background clutter . The approach is very suitable for short-lived trace gases like NH3, for which yg and Sg can easily be estimated from observations with background levels of NH3. More details on their construction will be provided in Sect. .
In the present study, we are interested in characterizing the instrumental performance for retrieving NH3 column abundances. σnoise and σabs constitute two suitable metrics. The former quantifies the propagation of the instrumental noise to the retrieval and is a firm lower bound to the total measurement uncertainty. The quantity is easy to calculate as it relies only on a Jacobian and an estimate of the noise covariance matrix. σabs, on the other hand, includes uncertainty related to spectral interferences, irrespective of whether they are explicitly taken into account through fitting in the retrieval procedure. The capability of differentiating such interferences from the NH3 spectral signature is directly related to the instrument. For example, at higher spectral resolution, slowly varying surface emissivity is expected to be more easily disentangled from the sharper NH3 spectral features. As such, this metric is fully representative of how the instrumental performances propagate to the retrieval uncertainty. It is the main metric used in this study.
There are two important notes to be made, both related to the fact that in the above we assumed that K is known. K inherently depends on the state of the surface and the atmosphere, and more particularly on the thermal contrast (TC), which is the temperature difference between the surface and the ambient temperature at the location where the bulk of the NH3 is located. TC is crucial in the infrared as it determines whether the spectral signature of the species is observed in absorption or emission, as well as the strength of this signal. We refer to and for a detailed discussion on TC.
The uncertainty on the scene results in an additional contribution σrel to the total retrieval uncertainty σtotal, with σtotal2=σabs2+σrel2.
The notations abs and rel refer to the fact that σabs is an absolute contribution to the uncertainty, independent of the column, while σrel is a relative contribution that varies linearly with the column CNH3. It was shown in that σrel is also, to a first order, inversely proportional to the TC:
σrel≈0.07+1.6KTCCNH3.
This formula was derived statistically assuming a Gaussian-distributed NH3 vertical profile peaking at the surface with width h and the TC defined as the difference between the surface temperature and that at an altitude of h/2. Uncertainties of the order of 1–2 K on both surface and air temperature were assumed. In what follows, we will assume that the input parameters used to calculate K, in particular the temperatures, are provided from an external source, like the output of a meteorological model, and are not retrieved from the measurement itself. Uncertainty on the TC is, in this case, not related to the instrument, so this source of uncertainty can be disregarded when comparing different hypothetical instruments. The design of an instrument that is simultaneously capable of retrieving temperatures and NH3 (like IASI) will not be studied here. That being said, for the instruments under investigation, surface temperature can always be estimated from measurements as we consider sounders measuring in the atmospheric window between 900 and 1000 cm−1.
The second note to be made is that both σnoise and σabs depend on the atmospheric state (and again mostly the TC) because K does. It is therefore important to specify the exact atmosphere under which these numbers are calculated. In the rest of the paper, K is calculated for a standard atmosphere , a Gaussian-distributed NH3 vertical profile with h=1.35km, and a surface temperature such that the TC is 10 K. For IASI observations, it was shown that σabs(TC)≈3.6×1016TCmolec.Kcm2.
For our IASI reference scene (see Fig. discussed in Sect. ), we obtained σabs≈3.6×1015molec.cm-2, which is consistent with this value for a TC of 10 K. These fixed scenario numbers allow for a direct comparison of instruments, as the value of the TC depends on the state of the scene, not the instrument. However, if desired, the retrieval uncertainty at another TC can be obtained by scaling σabs inversely proportional to the TC.
(a) Measurement uncertainty (σnoise) for an instrumental noise (ϵ) of 100 mK from data simulated at a spectral resolution of 0.3 cm-1 as a function of central wavenumber and range width. The NH3 Jacobian K for the full range is indicated on top (black line). The crosses indicate the ranges discussed in Table . (b) On the left axis, σnoise is drawn as a function of the spectral sampling/resolution for two different spectral ranges. On the right axis, ϵ is shown corresponding to a σnoise=3×1015molec.cm-2. The spectral samplings of some existing and planned spaceborne instruments are indicated, along with the sampling of the Hyper-Cam airborne measurements .
The matched filter (MF)
A quantity related to σabs is the signal-to-noise or signal-to-clutter ratio:
x^σabs=MF=KTSg-1(y-yg)KTSg-1K.
This quantity, known as the (adaptive) matched filter, is widely adopted in scientific domains involving signal processing. This includes hyperspectral imaging and satellite remote sensing , where it is sometimes referred to as the hyperspectral range index (HRI; ). By definition, the distribution of the MFs for the background spectra (the clutter) has a mean of 0 and a variance of 1. By imposing a threshold on its value, the MF can be used as a detection tool to identify the presence of the target signature in an observed spectrum. Even if the set of spectra from which the pair (Sg, yg) is estimated does not follow a multivariate normal distribution, the distribution of the MF values on the background spectra is in practice often near normal . This implies that an MF value above 2.5 in absolute value indicates that the observed spectrum contains a signature of the target species with a probability larger than 98.5 %. Conversely, it means that 98.5 % of the spectra that were used for the construction of Sg and yg have an MF value (in absolute value) below 2.5.
Key to the calculation of σabs and MF is the construction of Sg and yg. As mentioned above, they are most frequently estimated from a large collection of observed spectra. Ideally, these should contain no detectable signature of the target species, as this leads to a decrease in performance . and proposed an iterative approach where the detection itself is used to exclude spectra with detectable signatures of the target species. A first MF value is calculated from the pair (Sg, yg) obtained from all observed spectra in the spectral range of interest. Next, a new pair (Sg, yg) is estimated, but this time only for spectra with a low |MF| value. This process is repeated until convergence. As explained in , using a very low threshold increases the sensitivity of the NH3 detection but leads to larger values of MF over the background too. Therefore, MF is explicitly renormalized at each iteration to have a standard deviation of exactly 1 on a well-chosen area of the scene with low MF values. Finally, to prevent numerical problems associated with the very small eigenvalues of Sg, Sg-1 is calculated using the methodology presented in .
Signal-to-noise ratio (SNR) and false alarm rate (FAR)
The quantities σabs and MF convey similar information for comparing instrumental performance when the pair (Sg, yg), on which they both rely, represents a multivariate normal background distribution. Consistent with its interpretation as a signal-to-noise ratio, an MF value of 1 corresponds to an NH3 value of x=σabs (this can be seen by substituting y-yg=xK in Eq. ). Larger values of MF can be interpreted likewise in units of σabs. However, while σabs is a single number calculated from an ensemble of spectra, MF can be calculated on individual spectra and can be used to investigate possible departures from linearity or non-Gaussian statistics, which might be instrument-dependent. For this reason, we use two additional metrics based on MF in this study.
The first is the mean signal-to-noise ratio (SNR), calculated as the average MF value of a given set of spectra containing the target signature. In view of the above, the expected behavior of this SNR is inversely proportional to σabs.
Another common metric based on the MF is the false alarm rate (FAR; ). Rather than assessing the performance on spectra containing observable quantities of NH3, this metric evaluates how likely it is that noise or spectral interferences are misinterpreted as NH3. It is defined as the fraction of false detections over the total number of observations for a given set of NH3-free spectra.
σnoise for the spectral ranges marked with crosses in Fig. a and, in the last column, σnoise relative to the range used for the IASI NH3 retrieval. An instrumental noise of 100 mK is assumed.
In the first part of this section, we analyze the performance of hypothetical instruments with different spectral ranges and resolutions, focusing on the σnoise metric. Then we move to the other metrics (SNR, FAR, and σabs), for which we rely on manipulations of real data from IASI (Sect. ) and Hyper-Cam (Sect. ).
From simulated spectra
In this section, Fourier-transform-type instruments were assumed, with different maximum optical path differences (MOPDs) and spectral ranges. The MOPD determines both the spectral sampling (0.5/MOPD) and spectral resolution (0.60335/MOPD) . The instrumental noise was assumed to be constant across the spectrum with ϵ in radiance units corresponding to 100 mK for a reference blackbody at 288 K and 1000 cm−1. In this case, Sϵ is proportional to the identity matrix as Sϵ=ϵ2I and
σnoise=ϵKTK-1/2.
The line-by-line radiative transfer code Atmosphit was used as the forward model under the fixed standard atmospheric conditions specified in Sect. . We focus on the 800–1200 cm-1 range that contains most of the ν2 band of NH3, showing strong features around 931 and 967 cm-1, as can be seen from the Jacobian K displayed in Fig. a.
We first evaluate the effect of spectral range on the measurement uncertainty, for an instrument with an MOPD of 2 cm (sampled at 0.25 cm-1 and with a spectral resolution of 0.3 cm-1). Figure a shows σnoise as a function of both central wavenumber and range width. Table lists a series of selected spectral ranges of various widths (marked with crosses in Fig. a) along with their σnoise. The last column of Table expresses retrieval uncertainty relative to the one for the range used for the IASI NH3 retrieval (812–1126 cm-1).
As expected, we observe the smallest uncertainties for the largest range, with the 925–975 cm-1 interval contributing the most. Compared to the IASI retrieval range, we find that extending the range to 400 cm-1 improves the uncertainty by only 0.5 %. For range widths of 200 and 100 cm-1, σnoise increases by 7 % and 23 %, respectively. Increases greater than 60 % are observed for ranges shorter than 35 cm-1, as these contain only one of the two major features of the NH3 signature. The range focusing on the feature centered at 967 cm-1 is more sensitive to NH3 than the second one centered on 931 cm-1, as seen from the last two rows of Table .
The effect of spectral sampling is investigated for two ranges. The first is 200 cm-1 wide, extending from 925 to 1125 cm-1, and the second is 100 cm-1 wide between 900 and 1000 cm-1. Figure b shows σnoise (black curves) calculated for both ranges as a function of the spectral sampling, which varies from 0.1 to 10 cm-1 (the equivalent spectral resolution is indicated on top). For the 900–1000 cm-1 range, degrading the sampling from 0.1 to 1 cm-1 increases σnoise by a factor of 3.6. When the sampling is further degraded from 1 to 10 cm-1, σnoise increases by a further factor of 4.5. Consistent with what was observed above, σnoise is slightly larger for the shortest range. However, this difference is small, and the effect of the spectral sampling/resolution is clearly greater than that of the spectral range.
The right axis of the graph shows the required noise ϵ (in orange) to obtain a fixed value of σnoise=3×1015molec.cm-2. This was calculated by inversion of Eq. (). As can be seen from that relation, in principle, any desired retrieval uncertainty can be achieved as long as the instrumental noise is small enough. However, at very coarse resolution, the NH3 signature becomes difficult to distinguish from other spectral contributions. Hence the need to look at simulations involving real data and the σabs metric.
From IASI spaceborne dataUniformly spaced channels
Taking advantage of the high spectral resolution of the native IASI measurements, we degraded the original L1C spectra to characterize hypothetical sounders with lower resolution. The sampling was degraded to 1, 2, 5, and 10 cm-1 by block-averaging neighboring channels of the original spectra. In view of the results of the previous section, the spectral range was limited to the 900–1000 cm-1 region. Averaging multiple channels together reduces the single-channel noise, and to be able to fairly compare the different hypothetical instruments, artificial noise was added to each spectrum to match the noise level of the spectra degraded to 1 cm-1 sampling. It should be noted that the results presented here are specific to the assumed noise level, but the observed trends remain general, as further supported in the following section dealing with noisier data. The details of how the spectra were degraded and how the noise levels were estimated are explained in the Appendix . There, we also show that the spectra obtained in this way have a spectral resolution that matches very closely their spectral sampling, so both terms will be used interchangeably in this section.
MFIASI distribution calculated from the morning IASI overpass on 8 April 2020 from . The signal-to-noise ratio (SNR), the false alarm rate (FAR), and the uncertainty (σabs) are indicated on top. The “out” boxes correspond to the areas used to estimate the FAR.
As the basis for our analysis, we used all IASI morning observations of a single day (8 April 2020) between -65 and 65° latitude. The original MFIASI from is illustrated in Fig. over an area covering part of Europe, northern Africa, and western Asia. For clarity, we only show this region in the following. However, since we use all data between -65 and 65° latitude, the results that will be presented are based on and representative of global data (except for the poles). The pair (Sg, yg), the MF, and the four performance metrics were determined as follows:
(Sg, yg).
These were constructed from all degraded spectra with a corresponding |MFIASI|≤1.5.
MF.
MF was calculated from the degraded spectra with Eq. (), using (Sg, yg) defined above and K calculated from forward simulations as explained in Sect. , and block-averaged in a similar way as the spectra. For the reason explained in Sect. , the MF was renormalized to have a standard deviation of 1 over the area west of -140° W (remote Pacific Ocean).
SNR.
A mean SNR was calculated from the average MF for spectra with MFIASI>20. The SNR for MFIASI on this set is 22.2.
FAR.
The FAR was calculated as the fraction of observations for which |MF|>2.5 for observations inside the “out” boxes defined on Fig. . As mentioned above, when the MF follows a normal distribution, the expected value of the FAR is 1.5 % for this threshold (this is the case for MFIASI).
σabs.
σabs was straightforwardly calculated from Eq. () and estimated to 3.6 × 1015molec.cm-2 for MFIASI.
σnoise.
σnoise was calculated from Eq. (). While the single-channel noise is defined to be the same across all degradations, σnoise varies because of the different Jacobians and number of channels.
SNR, FAR, and σabs as a function of the number of channels for the degraded IASI (a) and the Hyper-Cam data over Rosignano (b) and around the Po Valley (c). The triangles show the results for continuous channels between 900 and 1000 cm-1, while the dots represent the well-chosen spectral bands of different widths, as indicated by their respective color for IASI/Hyper-Cam. The open triangles on σabs plots indicate σnoise.
The metrics are summarized in Fig. a (triangles) and Table , while the MF distributions are shown in Figs. a and a. Note that the color scale of each panel was adapted to show visually similar NH3 over India, enabling better comparison of the noise levels.
SNR and FAR (%), along with σabs (×1016molec.cm-2) and σnoise (×1016molec.cm-2) for downgraded IASI spectra with n continuous channels between 900 and 1000 cm-1, and with 5, 4, 3, and 2 bands of different width (see Table ).
Each panel shows an MF distribution calculated from degraded IASI spectra. They show distributions retrieved for an instrument with a sampling of 1 cm-1 (left column) and 2 cm-1 (right column). The first row (a) is for an instrument with continuous channels between 900 and 1000 cm-1, and the other rows are for spectra with (b) 5, (c) 4, (d) 3, and (e) 2 spectral bands, respectively. The SNR and the FAR (in %) are noted on the upper right of each panel along with σabs (in molec.cm-2).
Each panel shows an MF distribution calculated from degraded IASI spectra. They show distributions retrieved for an instrument with a sampling of 5 cm-1 (left column) and 10 cm-1 (right column). The first row (a) is for an instrument with continuous channels between 900 and 1000 cm-1, and the other rows are for spectra with (b) 5, (c) 4, (d) 3, and (e) 2 spectral bands, respectively. The SNR and the FAR (in %) are noted on the upper right of each panel along with σabs (in molec.cm-2).
The distributions from the spectra sampled at 1, 2, and 5 cm-1 visually match the original distribution closely (see Fig. ), demonstrating that high spectral resolution is not a requirement for reliable NH3 measurements. The main difference is in the level of observed noise, as witnessed by the progressively higher σabs and lower SNR numbers for coarser samplings. From 100 channels of 1 cm-1 to 20 channels of 5 cm-1, the noise increases by a factor of approximately 3.
The FARs are all relatively close to the theoretical value of 1.5 %, a consequence of the MF normalization and the Gaussian nature of the MF distribution. The configuration of 10 channels of 10 cm-1 sampling (top-right panel of Fig. ) has the highest FAR (2.8 %). While the main NH3 patterns of the original distribution are still visible with an SNR of 2.4, slightly negative values are seen over North Africa and the Middle East. These can be attributed to variations in surface emissivity, which apparently cannot be resolved with the given spectral resolution and which also explain the higher FAR.
As for σnoise (open triangles in Fig. ), the results are consistent with the theoretical simulations from Sect. , increasing by a factor of 4.5 between 1 and 10 cm-1 sampling. In all cases, σabs is larger than σnoise as expected. We also see that at 1 cm-1 resolution, there is hardly any difference between the σabs and σnoise. However, as the resolution gets coarser, the difference becomes progressively larger. This is a consequence of the fact that at coarser resolution it becomes increasingly difficult to unambiguously distinguish NH3 from other interfering physical parameters. At 10 cm-1, the contribution of these spectral interferences is σabs2-σnoise2≈3×1016molec.cm-2, limiting inherently the unambiguous identification of columns of this magnitude, even for an instrument with a very small radiometric noise.
Well-chosen bands
Especially for the instruments with 5 and 10 cm−1 samplings, there are potentially better choices for the channel centers in relation to the absorption features of NH3. In this section, we explore again potential instruments with channels 1, 2, 5, and 10 cm-1 wide. However, instead of instruments with uniform sampling, we investigate instruments with fewer bands (2 to 5) and optimize their positions within the 900–1000 cm−1 interval. This could also potentially further reduce the complexity of a dedicated NH3 sounder. The locations of the bands reported here were determined as those that minimized the resulting σabs (calculated using the same procedure as before). For 2 bands, an exhaustive search was performed, while for 3, 4, and 5 bands, these were found with a stochastic hill climbing algorithm starting from 300 randomly chosen configurations. The optimal bands are summarized in Table and illustrated in Fig. .
Table summarizing the position of the optimal bands for observing atmospheric NH3 for the test data under consideration. Each value represents the center of the band in cm-1.
Illustration of the optimal spectral bands of various widths (from 1 to 10 cm-1) for observing atmospheric NH3 in the infrared. The NH3 Jacobian from Fig. is indicated as well in each subpanel (black line). Exact band positions are listed in Table .
As shown in the figure, for configurations with 2 or 3 bands, bands are always selected very close to each other, with 1 band targeting either the 931 or 967 cm-1NH3 feature, and 1 or 2 bands focusing on the baseline. When more bands are available, the two strong NH3 features are always targeted. For the configurations with more bands, bands are relatively close together as well and the full 900–1000 cm−1 range is never exploited. This likely helps in avoiding broadband variations in the baseline due to surface emissivity or clouds.
The associated MF distributions are shown in Figs. and , and the statistics are summarized in Fig. a (dots) and Table . All distributions resemble the original distribution, all reproducing the main NH3 enhancements over Europe, Russia, North Africa, India, and Myanmar. However, with an SNR of 1.5, the 2-band 10 cm-1 configuration is by far the noisiest, and with a measurement uncertainty of 6 × 1016molec.cm-2 such an instrument is only suitable for measuring very large NH3 columns. As expected, there is a clear general decrease in SNR and an increase in σabs for wider bands, with a factor of 3–4 between 1 and 10 cm-1 for a given number of bands. The number of bands also affects these two metrics, but to a lesser extent – about a factor of 2 between 2 and 5 bands. As a general observation, it is more efficient to observe NH3 using fewer bands at finer sampling than more bands at coarser sampling. For instance, in terms of SNR and σabs, we observe that even just 2 bands of 1 cm-1 perform similarly to 5 bands of 5 cm-1. Likewise, 2 bands of 2 cm-1 outperform 5 bands of 10 cm-1. We also see from the statistics in Table that for the coarsest spectral resolutions of 5–10 cm-1, the precise location of the bands is key and that the optimal choice provides a genuine gain in performance. For instance, 5 well-chosen bands of 10 cm-1 outperform 10 contiguous bands between 900–1000 cm-1. For the 10 cm-1 band configuration, even just 3 well-chosen bands match the performance of the latter.
The MF does a good job of minimizing the FAR, with most configurations having a FAR below 2 %. It is notable that the 5 well-chosen bands of 10 cm-1 have a much better FAR and performance over deserts than the 10 uniformly sampled bands of 10 cm-1. This demonstrates that the optimized choice of band centers not only helps increase the SNR but can also help mitigate false detections. In terms of FAR, besides the 10 bands of 10 cm-1, the configurations that perform the poorest are the 2 or 3 bands of 10 cm-1, with a FAR between 2 % and 2.6 % (see Figs. d, e and d, e). These are the same configurations that exhibit the largest negative values over the deserts in North Africa and the Middle East. For these, the information content of the measurement is not large enough to distinguish surface effects from the NH3 spectral signature. Related to this, we again observe that the difference between σabs and σnoise increases as the spectral resolution decreases (see Table ). Here, we additionally see that these differences increase as the number of bands decreases, showing that both the number of bands and their resolution affect the capability of an instrument to disentangle the NH3 signature from other spectral interferences.
Finally, to demonstrate the robustness of these findings, we repeated the same set of tests using IASI measurements acquired 6 months later, on 8 October 2020. In autumn, NH3 observation conditions are less favorable, resulting in generally lower MFs. However, since our analysis focuses on relative differences compared to the original IASI measurements, the performance metrics derived from downgraded data are in very good agreement with those obtained from the spring dataset (see Appendix ).
In terms of channel-selection methodology, our approach attempts to find the extremum over all channel combinations, whereas the traditional microwindow selection process as in uses an iterative approach, where 1 channel is added in turn, each time adding a maximum of information. This process is computationally more efficient (and thus suitable for a large number of channels) but is less likely to yield a global extremum than our approach.
From Hyper-Cam airborne measurementsUniformly spaced channels
As explained in Sect. , the Hyper-Cam data were spatially averaged to reduce noise. Even after averaging, the resulting resolution of 100 m2 is still 1000 times finer than IASI's (> 100 km2). At such a fine resolution, the measurements are expected to exhibit much stronger variations in surface emissivity due to features like rooftops, solar panels, crop fields, or bare soil. Such features are not seen individually by IASI and might affect NH3 measurements at low spectral resolution. Hence, in this section, we explore the effects of spectrally degrading the Hyper-Cam measurement data to verify whether the results from the previous section remain valid at smaller spatial scales.
From the two surveys (over Rosignano and around the Po Valley; see Sect. ), MF distributions were calculated from the observed spectra covering the spectral range from 870 to 1260 cm-1 at the native 1.3 cm-1 sampling. In both cases, the pair (Sg, yg) was built in 8 iterations, each time filtering out pixels with |MF|>1.5. The MF distributions were renormalized using the spectra measured over the areas referred to with “out” in Figs. and , defining the background. In the measurements over Rosignano, we observe an NH3 plume originating from the plant, extending over more than 2 km in the eastward direction; see Fig. . As can be seen from the zoomed-in view of the industrial complex shown in Fig. b of the figure, both positive and negative MF values are observed. The sign is related to the sign of the TC, which determines whether the spectral signature is observed in absorption or emission . The MF distribution for the scene in and around the Po Valley is shown on the left side of Fig. . Various hotspots of NH3 can be observed over farms, some of which are shown in close-ups on the right side of the figure. The agricultural sources listed in the E-PRTR between 2020 and 2022 are indicated by black dots, most of which are visible in the MF distribution.
For the evaluation of the results, we followed as much as possible the approach applied to the IASI spectra. The spectral range was as before limited to 900–1000 cm-1, and spectra were degraded by block-averaging neighboring channels of the original measurements. Given the initial sampling of 1.3 cm-1, this procedure results in spectra sampled at 2.6, 5.2, and 10.4 cm-1, which is close to the 2, 5, and 10 cm-1 studied earlier. For the same reasons as above, Gaussian noise was added to each spectrum to match the native unapodized noise of the 1.3 cm-1 spectra, estimated at 4.43×10-4W(m2srcm-1)-1 (see Appendix ). For each configuration, (Sg, yg) were calculated based on the pixels for which |MF|<1.5 of the original spectra. The SNR was calculated from the 500 pixels presenting the highest MFs located in the “in” boxes defined in Figs. and . The FAR was calculated as the fraction of spectra with |MF|>2.5 within the “out” boxes defined in Figs. and .
Figure a–d show a close-up of the resulting MF distributions over Rosignano. As before, the color scale was adapted so that the NH3 plume appears similar in each panel. The SNR, FAR, and σabs are indicated on the bottom left of each panel and are also shown in Fig. b (triangles). As expected, the NH3 signal gradually fades into the noise when the sampling deteriorates, resulting in an SNR decrease from 8.0 to 2.1 and a σabs increase from 2.2×1016 to 10.3×1016molec.cm-2. By means of illustration, the insets of Fig. show the average of the 500 spectra measured inside the plume and used to calculate the SNR (blue) at different spectral resolutions. In red, a scaled Jacobian is shown with the signature of NH3, illustrating that while the contribution of NH3 to the average is easily seen at fine resolution, it becomes increasingly hard to identify NH3 at coarser spectral resolution. As before, the FARs are all close to the theoretical value of 1.5 % for the given threshold of MF. Yet, there are certain small features that are apparent in MF distributions, especially at coarser resolution. One of these is indicated with an arrow in Fig. . The associated spectra have a large positive slope in the baseline between 900–1000 cm−1. Inspection of visual imagery shows that this particular feature is related to a large rooftop. So even though the overall FAR statistics are favorable, localized false detections related to surface features are to be expected at small spatial scales.
MF distributions calculated from Hyper-Cam measurements in Rosignano downgraded to a spectral sampling of (a) 1.3, (b) 2.6, (c) 5.2, and (d) 10.4 cm-1 between 900 and 1000 cm-1. Panel (e) corresponds to the distribution obtained from spectra computed in 5 well-chosen bands of 1.3 cm-1 width. The arrows indicate a false signal of NH3. The SNR, FAR (in %), and σabs (in molec.cm-2) are indicated on the bottom left of each panel. The bottom right shows the average of the 500 downsampled spectra observed over the plume used to calculate the SNR (in blue) and the NH3 Jacobian (in red).
The results related to the spectra measured over the Po Valley show the same tendencies, as summarized in the third column of Fig. . Overall, these statistics are again fully consistent with those from IASI, when taking into account the larger noise of the Hyper-Cam measurements (4.43×10-4W(m2srcm-1)-1, Fig. ) compared to that of the IASI instrument averaged in blocks of 1 cm−1 (1.73×10-4W(m2srcm-1)-1).
Well-chosen bands
As with the IASI spectra, we also degraded the Hyper-Cam spectra to just a few bands. The bands were selected as close as possible to the optimal ones found for IASI. The results are summarized in Fig. . Generally, we observe that all metrics are remarkably close to each other for both campaigns, demonstrating that these are largely scene independent. Taking into account the larger noise of the Hyper-Cam measurements, the statistics follow closely those from IASI. In particular, we observe the general trend that the SNR and σabs improve when the channels become narrower or when the number of channels increases. The only exception is for the case of 4 bands of 10.4 cm-1, which performs slightly better than the 5 bands of 10.4 cm-1 over the Po Valley. This is likely related to the slight shifts in the positions of the bands. The FARs are all around the theoretical value of 1.5 %.
We also observe again that configurations with few bands at higher resolution can perform just as well as a uniformly sampled instrument, supporting again the possibility of drastically reducing the number of spectral measurements to monitor NH3. For instance, for the Rosignano measurements, we see that the SNR and the σabs of the 5-band 1.3 cm-1 configuration are similar and even slightly better than the 40 continuous channels of 2.6 cm-1. Both distributions are compared in Fig. b and e and indeed have a visually similar appearance. However, the FAR, at 1.6 %, is slightly larger for the 5-band configuration, and there are also a few additional surface artifacts in the distribution with fewer channels. Somewhat surprisingly, we observe that generally the FAR for the campaign data does not vary as much as for IASI. This is likely due to the absence of sandy surfaces with large and variable surface emissivity variations, posing particular difficulties for the MFs.
Figure illustrates MF distributions obtained from spectra measured over the Po Valley sampled at 1.3 cm-1 and computed as continuous (Fig. a) and individual well-defined bands (Fig. b to d). The gradual increase in noise is visible, but the main NH3 hotspots are clearly identifiable in all distributions, as well as the broad gradients across the map, confirming that NH3 can be effectively observed with just a few channels, also at small spatial scales.
Conclusions
One of the crucial challenges in designing a satellite sounder is balancing the quality of the observations with the complexity and cost of a mission. For measuring atmospheric compounds, the key observational requirements are the spatial resolution and the retrieval uncertainty, which are intricately linked with the spectral range, resolution, and radiometric noise of the instrument. Current sounders capable of measuring NH3 offer excellent spectral and radiometric qualities but lack the spatial resolution for quantifying its many small-scale emission sources. While a hyperspatial high-resolution infrared sounder is technologically feasible, it has until now not yet been investigated whether the high spectral resolution offered by current sounders is required for effectively observing NH3. In this study, we explored the feasibility of measuring NH3 with instruments having a reduced spectral coverage and resolution compared to current and planned operational sounders. This objective is driven by the urgent need for effective monitoring of atmospheric NH3 at high spatial resolution, especially in the context of excessive agricultural and industrial emissions that significantly affect air quality and the environment.
A first general conclusion is that the 900–1000 cm-1 (or even the 925–975 cm-1) range is by far the most sensitive spectral range for infrared measurements of NH3 and that from a pure retrieval uncertainty perspective, there is no large benefit of extending beyond. When it comes to instruments providing full spectral coverage with uniformly spaced channels, it was found that even a spectral resolution of 10 cm-1 can be adequate for monitoring NH3, depending on the radiometric noise and the targeted retrieval uncertainty. However, at such a resolution, spectral interferences start becoming increasingly important in the retrieval uncertainty budget, limiting inherently the retrieval to high columns only. For a general purpose NH3 sounder of low-resolution and uniform sampling, we therefore would recommend a spectral resolution finer than 5 cm−1, noting that it is more efficient to observe NH3 using fewer bands at finer sampling rather than more bands at coarser sampling.
The possibility of using a few dedicated broadband channels for measuring atmospheric gases has been demonstrated before. for instance retrieved methane (CH4) column concentrations from two 10 nm wide bands in the shortwave infrared of the Sentinel-2 MultiSpectral Instrument. We have shown that especially for sounders with a resolution of 5–10 cm−1, the location of the spectral bands is key, and if the instrumental design permits, 3–5 carefully chosen located bands can provide significant benefits on the retrieval uncertainty. For instruments with higher resolution (1–2 cm-1), 2 or 3 carefully chosen microchannels can already faithfully reproduce NH3 distributions and outperform instruments with broader spectral bands.
Further validation was conducted using airborne Hyper-Cam measurements. The analysis of these spectra, measured at fine spatial resolution, confirmed the results obtained with IASI and demonstrated the applicability of a sounder with reduced spectral resolution for measuring NH3 at small spatial scales, whether from industry or agriculture.
While it is clear that high spectral resolution offers significant benefits, it should be emphasized that all the results reported here assume uniform noise, which in practice will not be the case when comparing different engineered designs. For example, it is generally much easier to achieve a required noise level at low spectral resolution than at high. If a medium- to low-spectral-resolution instrument were to be designed, the analysis should carefully take into account the estimated instrumental noise budgets that each of the potential designs could offer. The methodology developed and presented in this paper allows this and can be easily generalized to variable noise levels. Indeed, for the case of uniform noise presented here, there are a plethora of well-chosen bands that theoretically have a very similar performance. Some of these alternative options are likely to perform better with a specific non-uniform noise profile.
Downgrading spectra and total noise estimate
In this study, spectra were downgraded by averaging neighboring channels in blocks of different sizes n. For IASI, values of n=4, 8, 20, and 40 were used, resulting in spectra sampled at 1, 2, 5, and 10 cm-1. Block-averaging a spectrum is equivalent to convolving the original spectrum with a normalized boxcar function of width n and selecting 1 out of n channels of the resulting spectrum. The spectral resolution of this spectrum can be estimated from the full width at half maximum (FWHM) of the instrumental line shape of IASI (approximately Gaussian with a FWHM of 0.5 cm-1) convolved with this boxcar. Numerically, it was found to be very close to the sampling rate; see Table .
The first part of the table compares the sampling and the equivalent spectral resolution from original IASI measurements and downsampled spectra. The second part lists the median of σ between 900 and 1000 cm-1 for both diagonal and off-diagonal elements (in W(m2srcm-1)-1). The bottom part shows the median values of the unapodized noise, the added noise, and the total noise, provided in radiance units and converted into brightness temperatures for a reference temperature of 288 K.
To compare these hypothetical instruments fairly, it is important to equalize their noise levels, and so Gaussian noise was added to spectra to match the noise level of the spectra with the smallest sampling, as these have the largest noise. Noise covariance matrices were estimated from a principal component analysis . For IASI, as its spectra are quite strongly apodized, these matrices are found to have non-negligible off-diagonal elements, indicating correlated noise across nearby channels . Reversible apodization does not affect the total noise in the spectrum but does make it more difficult to compare noise levels. Below, we show that the uncorrelated noise, i.e., the diagonal noise before apodization, can be recovered by simply summing up the columns of the correlated noise covariance matrix.
Table summarizes, for both original and downgraded IASI spectra, the apodized noise (diagonal and off-diagonal elements of the noise covariance matrix) and total unapodized noise. It also tabulates for each choice of n how much Gaussian noise was added and the resulting total noise, both in radiance units and brightness temperatures. Figure shows the original IASI apodized and unapodized noise between 900 and 1000 cm-1.
Radiometric noise estimated from native IASI and two-by-two averaged Hyper-Cam measurements between 900 and 1000 cm-1.
The same procedure was applied to the Hyper-Cam data. Spectra were downgraded by block-averaging neighboring channels (n=1, 2, 4, and 8), resulting in spectra sampled at 1.3, 2.6, 5.2, and 10.4 cm-1. Gaussian noise was added to these spectra to match the unconvoluted noise level of the original measurements, estimated at around 300 mK from the noise covariance matrix. The apodized and unapodized noise calculated from the original data measured over Rosignano are shown in Fig. (in green).
We end this section with a proof of the relation between the apodized and unapodized noise covariance matrix. Let Sϵ be a diagonal noise covariance, with σ the square root of its diagonal. We now investigate how this covariance matrix is altered by convolution or apodization. We write the convolution as w-n, w-n+1, …, wn-1, wn, with ∑kwk=1. We assume the convolution only spreads a few elements wide (much smaller than the length of the spectrum). The convolution has the following effect on a given spectral noise ϵ:
ϵ̃j=∑kwk-jϵk.
This can be written in matrix notation as
ϵ̃=w⋆ϵ=Wϵ,
with Wjk=wk-j. Using the propagation of uncertainty formula, the noise covariance matrix of the convoluted spectra takes the form S̃ϵ=WSϵWT
or
S̃ϵ,ij=∑klWikSϵ,klWjl=∑kWikσk2Wjk,
where we have used the fact that Sϵ is assumed diagonal. This equation gives the relation between the apodized and unapodized covariance matrix. Let us now evaluate the vector obtained by summing the rows of S̃ϵ,ij:
∑iS̃ϵ,ij=∑ikWikσk2Wjk=∑kσk2Wjk∑iWik.
Using the fact that the sum of all rows of W equals an all-one vector (disregarding edge effects), we find
∑iS̃ϵ,ij=∑kσk2Wjk.
Assuming a small kernel, slowly varying noise (σk≈σj), and again away from end points, we find that
∑iS̃ϵ,ij=σj2.
We can therefore recover the unconvoluted noise σ2 by simply adding up the columns of the noise covariance matrix.
Degradation of IASI data measured in autumn
The tests described in Sect. were also applied to IASI data collected on 8 October 2020 to assess the robustness of our conclusions under less favorable observation conditions. Figure presents the original MF distribution, illustrating that the overall MF levels are lower than in April. Following the same methodology as for the spring dataset, we evaluated the NH3 detection with the four performance metrics introduced in Sect. . To ensure that the SNR of the initial distribution is comparable to the SNR calculated from the spring dataset, the mean SNR was calculated from a tuned set of spectra, i.e., as the average MF for spectra with MFIASI>14.2. The FAR was calculated as before as the fraction of observations for which |MF|>2.5 inside the “out” boxes defined in Fig. . The values σabs and σnoise were calculated as before with Eqs. () and (), with (Sg, yg) constructed from all spectra with |MFIASI|≤1.5.
The measurements were then downgraded as previously described and assessed using these performance metrics. Figures , , and summarize the results, showing that they are almost identical to those derived from the spring dataset. The largest differences are observed in the FARs, which is expected due to random nature of these. Overall, these results confirm the consistency of the conclusions drawn from spring measurements and highlight the robustness of the performance metrics.
MFIASI distribution calculated from the morning IASI overpass on 8 October 2020 from . The signal-to-noise ratio (SNR), the false alarm rate (FAR), and the uncertainty (σabs) are indicated on top. The “out” boxes correspond to the areas used to estimate the FAR.
(a) SNR, (b) FAR, and (c)σabs as a function of the number of channels for the degraded IASI measurements (8 October 2020). The triangles show the results for continuous channels between 900 and 1000 cm-1, while the dots represent the well-chosen spectral bands of different widths, as indicated by their respective color. The open triangles on σabs plots indicate σnoise.
Each panel shows an MF distribution calculated from degraded IASI spectra (8 October 2020). They show distributions retrieved for an instrument with a sampling of 1 cm-1 (left column) and 2 cm-1 (right column). The first row (a) is for an instrument with continuous channels between 900 and 1000 cm-1, and the other rows are for spectra with (b) 5, (c) 4, (d) 3, and (e) 2 spectral bands, respectively. The SNR and the FAR (in %) are noted on the upper right of each panel along with σabs (in molec.cm-2).
Each panel shows an MF distribution calculated from degraded IASI spectra (8 October 2020). They show distributions retrieved for an instrument with a sampling of 5 cm-1 (left column) and 10 cm-1 (right column). The first row (a) is for an instrument with continuous channels between 900 and 1000 cm-1, and the other rows are for spectra with (b) 5, (c) 4, (d) 3, and (e) 2 spectral bands, respectively. The SNR and the FAR (in %) are noted on the upper right of each panel along with σabs (in molec.cm-2).
Code availability
Code is available upon request by contacting the corresponding author (lara.noppen@ulb.be).
Data availability
Data are available upon request by contacting the corresponding author (lara.noppen@ulb.be).
Author contributions
LN and LC conceptualized the research, analyzed and interpreted the results, prepared the figures, and wrote the first version of the manuscript. TR organized the campaigns and carried out the measurements. All authors took part in the campaign planning, in the discussions, and in the revisions of the manuscript.
Competing interests
At least one of the (co-)authors is a member of the editorial board of Atmospheric Measurement Techniques. The peer-review process was guided by an independent editor, and the authors also have no other competing interests to declare.
Disclaimer
Publisher's note: Copernicus Publications remains neutral with regard to jurisdictional claims made in the text, published maps, institutional affiliations, or any other geographical representation in this paper. While Copernicus Publications makes every effort to include appropriate place names, the final responsibility lies with the authors.
Acknowledgements
The authors gratefully acknowledge the GFZ German Research Centre for Geosciences and Freie Universität Berlin (FUB) for the use of the Hyper-Cam instrument and for their support and cooperation during the campaign. The authors also thank Tim Hultberg and Jean Vander Auwera for discussions on principal component analysis and spectral resolution.
Financial support
This research has been supported by the European Space Agency (ESA; grant no. 4000133881/20/NL/FF/ab), which provided funding for the airborne campaigns. Lara Noppen has been supported by the French Community of Belgium in the framework of a FRIA grant (grant no. 40021763). Lieven Clarisse is a senior research associate supported by the Belgian F.R.S.-FNRS.
Review statement
This paper was edited by Daniela Famulari and reviewed by two anonymous referees.
ReferencesApte, J. S., Brauer, M., Cohen, A. J., Ezzati, M., and Pope, C. A.: Ambient PM2.5 reduces global and regional life expectancy, Environ. Sci. Tech. Let., 5, 546–551, 10.1021/acs.estlett.8b00360, 2018.Atkinson, N. C., Hilton, F. I., Illingworth, S. M., Eyre, J. R., and Hultberg, T.: Potential for the use of reconstructed IASI radiances in the detection of atmospheric trace gases, Atmos. Meas. Tech., 3, 991–1003, 10.5194/amt-3-991-2010, 2010.Barret, B., Hurtmans, D., Carleer, M. R., De Mazière, M., Mahieu, E., and Coheur, P.-F.: Line narrowing effect on the retrieval of HF and HCl vertical profiles from ground-based FTIR measurements, J. Quant. Spectrosc. Ra., 95, 499–519, 10.1016/j.jqsrt.2004.12.005, 2005.Bauduin, S., Clarisse, L., Theunissen, M., George, M., Hurtmans, D., Clerbaux, C., and Coheur, P.-F.: IASI's sensitivity to near-surface carbon monoxide (CO): Theoretical analyses and retrievals on test cases, J. Quant. Spectrosc. Ra., 189, 428–440, 10.1016/j.jqsrt.2016.12.022, 2017.Clarisse, L., Clerbaux, C., Dentener, F., Hurtmans, D., and Coheur, P.-F.: Global ammonia distribution derived from infrared satellite observations, Nat. Geosci., 2, 479–483, 10.1038/ngeo551, 2009.Clarisse, L., Coheur, P.-F., Prata, F., Hadji-Lazaro, J., Hurtmans, D., and Clerbaux, C.: A unified approach to infrared aerosol remote sensing and type specification, Atmos. Chem. Phys., 13, 2195–2221, 10.5194/acp-13-2195-2013, 2013.Clarisse, L., Van Damme, M., Clerbaux, C., and Coheur, P.-F.: Tracking down global NH3 point sources with wind-adjusted superresolution, Atmos. Meas. Tech., 12, 5457–5473, 10.5194/amt-12-5457-2019, 2019.Clarisse, L., Franco, B., Van Damme, M., Di Gioacchino, T., Hadji-Lazaro, J., Whitburn, S., Noppen, L., Hurtmans, D., Clerbaux, C., and Coheur, P.: The IASI NH3 version 4 product: averaging kernels and improved consistency, Atmos. Meas. Tech., 16, 5009–5028, 10.5194/amt-16-5009-2023, 2023.Clerbaux, C., Boynard, A., Clarisse, L., George, M., Hadji-Lazaro, J., Herbin, H., Hurtmans, D., Pommier, M., Razavi, A., Turquety, S., Wespes, C., and Coheur, P.-F.: Monitoring of atmospheric composition using the thermal infrared IASI/MetOp sounder, Atmos. Chem. Phys., 9, 6041–6054, 10.5194/acp-9-6041-2009, 2009.Coheur, P.-F., Barret, B., Turquety, S., Hurtmans, D., Hadji-Lazaro, J., and Clerbaux, C.: Retrieval and characterization of ozone vertical profiles from a thermal infrared nadir sounder, J. Geophys. Res., 110, 10.1029/2005jd005845, 2005.Crevoisier, C., Clerbaux, C., Guidard, V., Phulpin, T., Armante, R., Barret, B., Camy-Peyret, C., Chaboureau, J.-P., Coheur, P.-F., Crépeau, L., Dufour, G., Labonnote, L., Lavanant, L., Hadji-Lazaro, J., Herbin, H., Jacquinet-Husson, N., Payan, S., Péquignot, E., Pierangelo, C., Sellitto, P., and Stubenrauch, C.: Towards IASI-New Generation (IASI-NG): impact of improved spectral resolution and radiometric noise on the retrieval of thermodynamic, chemistry and climate variables, Atmos. Meas. Tech., 7, 4367–4385, 10.5194/amt-7-4367-2014, 2014. Davis, S. P., Abrams, M. C., and Brault, J. W.: Fourier Transform Spectrometry, Academic Press, 2nd edn., ISBN 9780120425105, 2005.de Vries, W., Posch, M., Simpson, D., de Leeuw, F., van Grinsven, H., Schulte-Uebbing, L., Sutton, M., and Ros, G.: Trends and geographic variation in adverse impacts of nitrogen use in Europe on human health, climate, and ecosystems: A review, Earth-Sci. Rev., 253, 104789, 10.1016/j.earscirev.2024.104789, 2024.Di Gioacchino, T., Clarisse, L., Noppen, L., Van Damme, M., Bauduin, S., and Coheur, P.: Spatial and temporal variations of thermal contrast in the planetary boundary layer, J. Remote Sens., 10.34133/remotesensing.0142, 2024.ESA: Report for Assessment: Earth Explorer 11 candidate mission Nitrosat, Tech. rep., European SpaceAgency, Noordwijk, the Netherlands, ESA-EOPSM-NITR-RP-4373, 127 pp., https://esamultimedia.esa.int/docs/EarthObservation/EE11_Nitrosat_Report_for_Assessment_v1.0_15Sept23.pdf (last access: 6 November 2024), 2023.European Commission: Best available techniques for the manufacture of large volume inorganic chemicals, Tech. rep., European Commission, https://bureau-industrial-transformation.jrc.ec.europa.eu/sites/default/files/2019-11/lvic-s_bref_0907.pdf, 2007.European Environment Agency: Industrial reporting under the industrial emissions directive 2010/75/EU and European pollutant release and transfer register regulation (EC) No. 166/2006, https://industry.eea.europa.eu/industrial-site/environmental-information?siteInspireId=IT.CAED/570161001.SITE&siteName=SOLVAY CHIMICA ITALIA S.P.A. ROSIGNANO&siteReportingYear=2020, (last access: 24 September 2024), 2022.Franco, B., Clarisse, L., Stavrakou, T., Müller, J.-F., Van Damme, M., Whitburn, S., Hadji-Lazaro, J., Hurtmans, D., Taraborrelli, D., Clerbaux, C., and Coheur, P.-F.: A general framework for global retrievals of trace gases from IASI: application to methanol, formic acid, and PAN, J. Geophys. Res.-Atmos., 123, 10.1029/2018jd029633, 2018.Glumb, R., Williams, F., Funk, N., Chateauneuf, F., Roney, A., and Allard, R.: Cross-track Infrared Sounder (CrIS) development status, in: Infrared Spaceborne Remote Sensing XI, SPIE, vol. 5152, 10.1117/12.508544, 2003.Holmlund, K., Grandell, J., Schmetz, J., Stuhlmann, R., Bojkov, B., Munro, R., Lekouara, M., Coppens, D., Viticchie, B., August, T., Theodore, B., Watts, P., Dobber, M., Fowler, G., Bojinski, S., Schmid, A., Salonen, K., Tjemkes, S., Aminou, D., and Blythe, P.: Meteosat Third Generation (MTG): Continuation and innovation of observations from geostationary orbit, B. Am. Meteorol. Soc., 102, E990–E1015, 10.1175/bams-d-19-0304.1, 2021.Kim, K.-E., Lee, S.-S., and Baik, H.-S.: Iterative matched filtering for detection of non-rare target materials in hyperspectral imagery, in: Image and Signal Processing for Remote Sensing XXII, International Society for Optics and Photonics, SPIE, vol. 10004, 100040E, 10.1117/12.2240638, 2016.Kneizys, F., Abreu, L., Anderson, G., Chetwynd, J., Shettle, E., Berk, A., Bernstein, L., Robertson, D., Acharya, P., Rothman, L., Selby, J., Gallery, W., and Clough, S.: The MODTRAN 2/3 Report and LOWTRAN 7 MODEL, Tech. rep., https://web.gps.caltech.edu/~vijay/pdf/modrept.pdf, 1996.Lagueux, P., Farley, V., Rolland, M., Chamberland, M., Puckrin, E., Turcotte, C., Lahaie, P., and Dube, D.: Airborne measurements in the infrared using FTIR-based imaging hyperspectral sensors, in: First Workshop on Hyperspectral Image and Signal Processing: Evolution in Remote Sensing, IEEE, 10.1109/whispers.2009.5289060, 2009a.Lagueux, P., Farleya, V., Chamberland, M., Villemaire, A., Turcotte, C., and Puckrinb, E.: Design and performance of the Hyper-Cam, an infrared hyperspectral imaging sensor, Tech. rep., Telops inc. Quebec, QC, Canada, https://apps.dtic.mil/sti/tr/pdf/ADA568314.pdf, 2009b.Lonati, G. and Cernuschi, S.: Temporal and spatial variability of atmospheric ammonia in the Lombardy region (Northern Italy), Atmos. Pollut. Res., 11, 2154–2163, 10.1016/j.apr.2020.06.004, 2020.Manolakis, D., Truslow, E., Pieper, M., Cooley, T., and Brueggeman, M.: Detection algorithms in hyperspectral imaging systems: An overview of practical algorithms, IEEE Signal Proc. Mag., 31, 24–33, 10.1109/msp.2013.2278915, 2014. Manolakis, D., Lockwood, R., and Cooley, T.: Hyperspectral Imaging Remote Sensing: Physics, Sensors, and Algorithms, Cambridge University Press, ISBN 9781316017876, 2016.Montembeault, Y., Lagueux, P., Farley, V., Villemaire, A., and Gross, K.: Hyper-Cam: Hyperspectral IR imaging applications in defence innovative research, in: 2nd Workshop on Hyperspectral Image and Signal Processing: Evolution in Remote Sensing, IEEE, 10.1109/whispers.2010.5594890, 2010.Noppen, L., Clarisse, L., Tack, F., Ruhtz, T., Merlaud, A., Van Damme, M., Van Roozendael, M., Schuettemeyer, D., and Coheur, P.: Constraining industrial ammonia emissions using hyperspectral infrared imaging, Remote Sens. Environ., 291, 113559, 10.1016/j.rse.2023.113559, 2023.Rodgers, C. D.: Information content and optimisation of high spectral resolution remote measurements, Adv. Space Res., 21, 361–367, 10.1016/s0273-1177(97)00915-0, 1998. Russell, S. J. and Norvig, P.: Artificial Intelligence: A Modern Approach, Prentice Hall, ISBN 978-0136042594, 2010.Schaum, A.: A uniformly most powerful detector of gas plumes against a cluttered background, Remote Sens. Environ., 260, 112443, 10.1016/j.rse.2021.112443, 2021.Serio, C., Liuzzi, G., Masiello, G., and Venafra, S.: Assessing the impact of incorrect observational covariance matrix over retrieval: Methods and application to IASI data, in: The 2014 EUMETSAT Meteorological Satellite Conference, Geneve, Switzerland, 10.13140/2.1.1417.8088, 2014.Serio, C., Masiello, G., Camy-Peyret, C., Jacquette, E., Vandermarcq, O., Bermudo, F., Coppens, D., and Tobin, D.: PCA determination of the radiometric noise of high spectral resolution infrared observations from spectral residuals: Application to IASI, J. Quant. Spectrosc. Ra., 206, 8–21, 10.1016/j.jqsrt.2017.10.022, 2018.Shephard, M. W. and Cady-Pereira, K. E.: Cross-track Infrared Sounder (CrIS) satellite observations of tropospheric ammonia, Atmos. Meas. Tech., 8, 1323–1336, 10.5194/amt-8-1323-2015, 2015.Sutton, M., Reis, S., Riddick, S., Dragosits, U., Nemitz, E., Theobald, M., Tang, Y. S., Braban, C., Vieno, M., Dore, A., Mitchell, R., Wanless, S., Daunt, F., Fowler, D., Blackall, T., Milford, C., Flechard, C., Loubet, B., Massad, R., Cellier, P., Personne, E., Coheur, P., Clarisse, L., Van Damme, M., Ngadi, Y., Clerbaux, C., Skjoth, C., Geels, C., Hertel, O., Kruit, R., Pinder, R., Bash, J., Walker, J., Simpson, D., Horvath, L., Misselbrook, T., Bleeker, A., Dentener, F., and de Vries, W.: Towards a climate-dependent paradigm of ammonia emission and deposition, Philos. T. Roy. Soc. B., 368, 10.1098/rstb.2013.0166, 2013.Tellinghuisen, J.: Statistical Error Propagation, J. Phys. Chem. A, 105, 3917–3921, 10.1021/jp003484u, 2001.Van Damme, M., Clarisse, L., Heald, C. L., Hurtmans, D., Ngadi, Y., Clerbaux, C., Dolman, A. J., Erisman, J. W., and Coheur, P. F.: Global distributions, time series and error characterization of atmospheric ammonia (NH3) from IASI satellite observations, Atmos. Chem. Phys., 14, 2905–2922, 10.5194/acp-14-2905-2014, 2014.Van Damme, M., Clarisse, L., Whitburn, S., Hadji-Lazaro, J., Hurtmans, D., Clerbaux, C., and Coheur, P.: Industrial and agricultural ammonia point sources exposed, Nature, 564, 99–103, 10.1038/s41586-018-0747-1, 2018.Van Damme, M., Clarisse, L., Stavrakou, T., Wichink Kruit, R., Sellekaerts, L., Viatte, C., Clerbaux, C., and Coheur, P.: On the weekly cycle of atmospheric ammonia over European agricultural hotspots, Sci. Rep., 12, 10.1038/s41598-022-15836-w, 2022.Varon, D. J., Jervis, D., McKeever, J., Spence, I., Gains, D., and Jacob, D. J.: High-frequency monitoring of anomalous methane point sources with multispectral Sentinel-2 satellite observations, Atmos. Meas. Tech., 14, 2771–2785, 10.5194/amt-14-2771-2021, 2021. von Clarmann, T., Grabowski, U., and Kiefer, M.: On the role of non-random errors in inverse problems in radiative transfer and other applications, J. Quant. Spectrosc. Ra., 71, 39–46, 10.1016/s0022-4073(01)00010-3, 2001.Walker, J. C., Dudhia, A., and Carboni, E.: An effective method for the detection of trace species demonstrated using the MetOp Infrared Atmospheric Sounding Interferometer, Atmos. Meas. Tech., 4, 1567–1580, 10.5194/amt-4-1567-2011, 2011.Wyer, K., Kelleghan, D., Blanes-Vidal, V., Schauberger, G., and Curran, T.: Ammonia emissions from agriculture and their contribution to fine particulate matter: A review of implications for human health, J. Environ. Manage., 323, 116285, 10.1016/j.jenvman.2022.116285, 2022.