Development and Evaluation of a Fluctuating Plume Model for Odor Impact Assessment

For environmental odor nuisance, it is extremely important to identify the instantaneous concentration statistics. In this work, a Fluctuating Plume Model for different statistical moments is proposed. It provides data in terms of mean concentrations, variance, and intensity of concentration. The 90th percentile peak-to-mean factor, R90, was tested here by comparing it with the experimental results (Uttenweiler field experiment), considering different Probability Distribution Functions (PDFs): Gamma and the Modified Weibull. Seventy-two percent of the simulated mean concentration values fell within a factor 2 compared to the experimental ones: the model was judged acceptable. Both the modelled results for standard deviation, σC, and concentration intensity, Ic, overestimate the experimental data. This evidence can be due to the non-ideality of the measurement system. The propagation of those errors to the estimation of R90 is complex, but the ranges covered are quite repeatable: the obtained values are 1–3 for the Gamma, 1.5–4 for Modified Weibull PDF, and experimental ones from 1.4 to 3.6.


Introduction
Odor is a property of a mixture of substances able to stimulate the olfactory sense. In the human nose, there are millions of receptors and the smell perception arises from the combination of the reactions of the nasal receptors to a wide range of odorous gases (H 2 S, NH 3 , VOCs, and more) [1,2]. Therefore, the main sources of environmental odors are the emissions of those odorous gases into the Planetary Boundary Layer (PBL) from industrial and agricultural activities [3][4][5]. Due to the proximity of residential centers to industrial areas, odor is one of the main causes of complaint to authorities [6,7].
In the PBL, like any other meteorological variable, the instantaneous concentration of odorous gases, more or less fluctuates, in time and space around to the local mean value, depending on the turbulence level of the atmosphere [8,9]. This is the reason why fluid dynamics researchers attribute to each PBL variable, and therefore also to the concentration of a passive scalar, the character of a stochastic variable completely defined by an appropriate Probability Density Function (PDF) [10][11][12]. Therefore, in order to completely know the statistics of the instantaneous concentration of a gas, it would be necessary to know its PDF or, equivalently, its infinite statistical moments, for each of which, it is theoretically possible to write an appropriate partial differential equation describing its budget [8,9,12,13].

•
C p = C m + σ, where C m is the hourly mean value and σ its standard deviation [22] • C p equal to the maximum value of the instantaneous concentration in the considered averaging period [23] • As an appropriate p -th percentile of the instantaneous concentration at each point of the spatial domain [24] A historical scientific challenge was the objectification of the subjective sensation of odor [25]. For this reason, the measurement of odors requires specific methods [26,27]. There are many regulations for Air Pollution, but olfactory pollution is typically treated differently. As previously mentioned, the trend in space and time of the instantaneous concentration of a gaseous species is very irregular. For instance, the sensation of smell is perceived mostly in hours when the PBL turbulence is low and therefore the atmospheric stability is high, i.e., at evening and early morning [17,28]. In these situations, the use of an atmospheric dispersion model appears to be crucial [29][30][31]. As a matter of fact, the majority of environmental odor legislations around the world lean upon models [32,33]. The outputs of the dispersion models used in Air Pollution assessment and forecast are usually the hourly-mean concentrations C m , but this information is not sufficient to describe completely the nature of an odor nuisance process [34,35]. To consider the variability of the ambient odor concentration within the period of 1 hour, a constant peak-to-mean factor C p /C m (also P/M) is usually provided by authorities [36][37][38]. As an example, the German legislation prescribes that all olfactory considerations of a modelling type, "Must be made considering an appropriate peak concentration". The Standard requires that the hourly average concentration obtained from the model is simply multiplied by a constant numerical factor equal to 4 [36,37]. Differently, all the regional guidelines present in Italy, suggest the value of 2.3 [38][39][40]. Unluckily, the experimental data show that a huge amount of physical phenomena have an effect on concentration fluctuations, demonstrating that the choice of a constant parameter is a very simplified approach [41]. Different simple methods for the calculation of this "peak-to-mean" factor can be found in literature; it is worth mentioning the constant peak-to-mean [36], the peak-to-mean variable only depending on atmospheric stability [42] and the one variable with stability and distance downwind the emission source [43,44]. Obtaining the sub-hourly percentile (and so the peak concentration) of a passive substance via dispersion model is not a trivial challenge. An alternative approach, available for Gaussian models is the consideration of recalculated lateral dispersion coefficients, in order to make them able to estimate ambient concentrations with averaging times shorter that 10 min [45,46].
However, the use of new models able to assess the mean concentration and variance, based on the physical laws describing the transport and dispersion in air of a substance, treated as a stochastic variable, appears the most recently debated methodology for the identification of peak concentrations (however defined, but linked to the statistical characteristics of the instantaneous concentration). In   [47] an updated and exhaustive review of the modelling methods that can be used for odor modelling has been presented, and the most suitable methods to represent real situations seem to be those based on a Lagrangian framework. The most used philosophy to solve the problem of estimating a sub-hourly percentile is to hypothesize a priori a realistic PDF for the passive concentration. Experimental evidences show that, for this purpose, it is sufficient to consider a two-parameter PDF that asymptotically reduces to an exponential distribution near the source and a Log-Normal distribution at great downwind distances [44]. Weibull distribution and especially Gamma distribution own these adaptability features. Since a two-parameter distribution is completely known once the mean value and the variance are obtained, this closure hypothesis means that, to describe the concentration fluctuations, and therefore to determine the desired percentile, it is sufficient to reconstruct the mean and the concentration variance.
One of the most interesting model is the Fluctuating (or Meandering) Plume model, originally proposed in qualitative terms by Gifford (1959) [48]. In Luhar et al. (2000) [49], the logical evolution of this modelling philosophy over the years is shown and a version based on Lagrangian Particle Modelling is described in detail. Further works have been published about this topic [50][51][52][53]. Within these studies, a Lagrangian version of the Fluctuating Plume is proposed, which provides extremely realistic reconstructions of the instantaneous concentration statistics. Unlucky, the complexity of the models proposed hinders their application for regulatory or screening evaluations.
The work of Marro et al. (2015) [54], instead, studies the Fluctuating Plume in situations that can be modelled by a Gaussian Plume Model for the average concentration (horizontal homogeneity of meteorological and micrometeorological variables and flat and horizontally homogeneous soil). In fact, these conditions are rather artificial, but can be considered realistic when the ground is flat, and the meteorological conditions are horizontally homogeneous and stationary. Primary focus of that work was to verify how much such a model was able to reproduce the extensive set of experimental measurements obtained by Nironi et al. (2015) [55] in a wind tunnel in substantially neutral turbulence. The important result reached is a semi-analytical expression for the different moments (uncentered) of the instantaneous concentration that reproduces with good approximation the measurements obtained in Nironi et al. (2015).
Our work starts from the general conclusions reached by Marro et al. (2015), in order to obtain a Gaussian Plume Model for the average concentration and its variance, totally algebraic and simple enough to be useful for design purposes. Based on the knowledge of the values representing the mean and variance, the parameters defining the two-parameter PDF are known, with which it is possible to estimate the peak concentration, defined as an appropriate percentile, at every point in time and space of the considered simulation domain. In order to evaluate the performance of the proposed model, a comparison with the Uttenweiler field dispersion test was conducted [56]. The simplicity of this model makes it useful at least for screening purposes and, in situations with flat and horizontally homogeneous terrain and with horizontally homogeneous meteorology, also for regulatory purposes. Its limitation consists in considering only one active emitting source.
In Section 2, the Lagrangian theory of the Fluctuating Plume is initially presented, and from it a new stationary Gaussian Plume formulation is obtained for the average concentration of a generic odorous substance and for its variance, as well as the methodology to be used to obtain the peak concentration. Section 3 briefly presents the Uttenweiler experimental campaign specifically dedicated to the measurement of the average concentration and variance, which was used to verify the behavior of the Gaussian Stationary Fluctuating Plume model here developed. In Section 4, the results obtained using the model developed to reconstruct the Uttenweiler experimental campaign are presented and discussed. Section 5 presents some conclusions.
The Gaussian stationary formulation obtained holds only if one emission source is active, but its use in situations of practical interest would require its multisource extension and this is not straightforward. If, in fact, for the average concentration the superposition of the effects holds, so it is not a priori for the variance and for the percentiles, since the turbulence of the PBL somehow correlates the different emission sources. This topic is currently still an open challenge and the Supplementary Material presents some considerations and possible practical solutions.
The purpose of the work described in this paper is to obtain a prototypal implementation of the theoretical model presented. Our aim is to obtain a preliminary test of the reliability and the usability of a simple and analytical model to estimate ambient peak concentrations, crucial for odor assessments. Only after a widespread experimental verification, the model will be worthy of a proper operative development, including an official implementation, releases, user's manual, and public distribution.

Conceptual Bases of the Fluctuating Plume Model
When a passive scalar, like a tracer or odorous gas, from a point source is emitted, in reality, many instantaneous plumes are generated in sequence, each different from the other and irregularly shaped. Only considering their average, they make up the usual regular plume characterized by a progressive enlargement in downwind direction, proportional to the turbulence present in the PBL. If we focus our attention on a single instantaneous plume, we can clearly see that in the first phase of dispersion, near the source, the plume is coherent, narrow and meandering, mainly horizontally and, to a lesser extent, also vertically. The plume meandering, more accentuated near the source, progressively reduces downwind until it disappears: the meandering extent is inversely proportional to the plume's characteristic dimension. From this phenomenological evidence, the famous Fluctuating Plume Model proposed by Gifford (1959) was inspired, which was originally formulated more as a conceptual tool than a quantitative model. It should be pointed out that, in this context, the term meandering refers to the slow oscillation of a plume due to the eddies characterized by a length scale greater than the plume length scale and not to the slow horizontal oscillations of the mesoscale motion (the "submeso" motions) practically always present in the PBL and very evident in high stability [57][58][59][60][61].
Let us put a point source in position (0, 0, z s ) and a coordinate system centered in it (x along the direction towards the mean wind is blowing, the y horizontal and transverse to x and with the vertical z-axis) [48,62], and an averaging time of the order of the spectral gap (therefore of the order of the hour [8]). What we can see is a regular plume growing progressively with the distance downwind to the emission point, initially in linearly and subsequently in parabolic manner. Basically, in homogeneous and stationary turbulence, the average plume can be seen as a succession of slices (spreading disk), adjacent to each other in x direction, having flat surfaces in (y, z) and thickness dx = Udt, where U is the mean wind speed at the emission point and dt is an appropriate small time interval. The distribution of the average concentration in the plane (y, z), at least in first approximation, can be considered Gaussian and centered at points y s = 0 and z s (plume centroid).
If, instead, we subdivide the averaging time into a succession of shorter time steps, it is easy to imagine that the average plume is the result of the superimposition of ideally infinite instantaneous irregular plumes, whose barycenters no longer coincide with the x-axis, but meander around it. Further, in this case, the (instantaneous) plume can be seen as a series of slices placed one next to the other, but in each slice the concentration distribution, always Gaussian in the y and z directions, is centered around a new centroid placed now at the transversal distance y m and the vertical distance z m . Gifford (1959) used this idea to propose a simple conceptual model of a stationary Gaussian Meandering Plume. In Gifford's model, the concentration distribution within the instantaneous plume is strictly deterministic, being described in both y and z by a Gaussian distribution. This distribution is instead a stochastic variable, since the coordinates of the position of the centroid y m and z m are really stochastic variables due to the nature of the turbulent eddies in the PBL. However, Gifford's model does not account, neither directly nor explicitly, for the action of turbulent eddies of smaller dimensions than the plume. This dispersion, not considered by the Gifford's model, is named "relative dispersion" or "internal plume dispersion". In practice, if we were to sample at the point (x, y, z) at high frequency (i.e., at successive instants very close to each other), what we would obtain would be a sequence of instantaneous concentration c i , each corresponding to a possible position of the centroid (y m , z m ). These statistical realizations will be different from each other and, on average, they will give the average concentration C, which corresponds to the visible and overall result of an absolute dispersion process. Figure 1 reports a graphical example of the average and the instantaneous plume dispersion.
Appl. Sci. 2021, 11, x FOR PEER REVIEW 5 of 29 Gifford (1959) used this idea to propose a simple conceptual model of a stationary Gaussian Meandering Plume. In Gifford's model, the concentration distribution within the instantaneous plume is strictly deterministic, being described in both y and z by a Gaussian distribution. This distribution is instead a stochastic variable, since the coordinates of the position of the centroid ym and zm are really stochastic variables due to the nature of the turbulent eddies in the PBL. However, Gifford's model does not account, neither directly nor explicitly, for the action of turbulent eddies of smaller dimensions than the plume. This dispersion, not considered by the Gifford's model, is named "relative dispersion" or "internal plume dispersion". In practice, if we were to sample at the point (x, y, z) at high frequency (i.e., at successive instants very close to each other), what we would obtain would be a sequence of instantaneous concentration ci, each corresponding to a possible position of the centroid (ym, zm). These statistical realizations will be different from each other and, on average, they will give the average concentration C, which corresponds to the visible and overall result of an absolute dispersion process. Figure 1 reports a graphical example of the average and the instantaneous plume dispersion. Despite being very simplified, the Gifford's Fluctuating Plume model captures in an immediate fashion the phenomenology of the instantaneous dispersion of a passive substance in the PBL. Despite the fact that the ground reflections of instantaneous plumes in the original model are neglected, the biggest restriction of the model in its original formulation is that it assumes the transverse and vertical distribution of the concentration in an instantaneous plume to be deterministic (described by a Gaussian distribution) and not a stochastic process as the experimental evidence has confirmed. Further studies [63][64][65], more than 30 years after the model was proposed, extended Gifford's model to include fluctuations within the instantaneous plume. However, even though Gifford's Fluctuating Plume model was formulated on a predominantly phenomenological basis, in Yee and Wilson (2000) [65] it was shown to be theoretically justified, describing in a simple and immediate way the fact that the absolute (average) total dispersion of a passive substance in the turbulent PBL is the result of two different and practically independent stochastic processes: a dispersion due to the meandering of the plume centroid and a relative dispersion of the centroid itself. This conceptual model has been the key to a number of experimental campaigns aimed at highlighting the absolute dispersion of the plume, the relative dispersion, and the meandering of the centroid. In this regard it is worth referring to the works of Ma et al. (2005), Peterson et al. (1999), Lamb (1995, 1992), and E.   [66][67][68][69][70]. Despite being very simplified, the Gifford's Fluctuating Plume model captures in an immediate fashion the phenomenology of the instantaneous dispersion of a passive substance in the PBL. Despite the fact that the ground reflections of instantaneous plumes in the original model are neglected, the biggest restriction of the model in its original formulation is that it assumes the transverse and vertical distribution of the concentration in an instantaneous plume to be deterministic (described by a Gaussian distribution) and not a stochastic process as the experimental evidence has confirmed. Further studies [63][64][65], more than 30 years after the model was proposed, extended Gifford's model to include fluctuations within the instantaneous plume. However, even though Gifford's Fluctuating Plume model was formulated on a predominantly phenomenological basis, in Yee and Wilson (2000) [65] it was shown to be theoretically justified, describing in a simple and immediate way the fact that the absolute (average) total dispersion of a passive substance in the turbulent PBL is the result of two different and practically independent stochastic processes: a dispersion due to the meandering of the plume centroid and a relative dispersion of the centroid itself. This conceptual model has been the key to a number of experimental campaigns aimed at highlighting the absolute dispersion of the plume, the relative dispersion, and the meandering of the centroid. In this regard it is worth referring to the works of Ma et al. (2005), Peterson et al. (1999), Lamb (1995, 1992), and E.   [66][67][68][69][70].

General Lagrangian Theory of the Fluctuating Plume Model
Let us consider a steady-state PBL of vertical extension z i , one point source at (x s ,y s ,z s ) with constant emission rate Q and a horizontally homogeneous spatial domain. In these conditions, the fluctuating plume model can be reformulated more realistically in a purely Lagrangian framework [49][50][51][52]. The instantaneous concentration c(x,y,z), if considering a continuous point source (with characteristic physical dimension σ 0 ) with position (x s ,y s ,z s ), is statistically described by the probability density function p(x,y,z). Adopting the Fluctuat-ing Plume philosophy, the dispersion can be considered as the combination (convolution) of two independent contributions (the floating part and the relative diffusion part). This distribution can be expressed by the convolution integral: where p cr (c; x, y, z, y m , z m ) is the probability density function describing at the downwind distance x the dispersion of the generic passive with respect to the centroid of an instantaneous plume located at (y m , z m ) (the relative dispersion) and p m (x, y m , z m ) is the probability density function that at x the centroid of the instantaneous plume has exactly those coordinates. Known the two probability density functions, we can calculate any n -th moment of the instantaneous concentration. As a matter of fact, in a Lagrangian framework, a generic (uncentered) moment of order n will be expressed as For example, the average concentration and the variance are expressed as and the concentration intensity as Unlike Gifford (1959) and supported by experimental evidence [65,70], here it is assumed that the fluctuations inside the instantaneous plume can be statistically described using a predefined PDF p cr (c; x, y, z, y m , z m ). Although Franzese (2003) [51] assumes this distribution as Log-Normal, Cassiani, and Giostra (2002), Luhar et al. (2000) and Mortarini et al. (2009) [51,52,54] hypothesize more realistically that the PDF is a Gamma distribution of the type: where c r is the mean concentration relevant to the instantaneous plume centroid, c the instantaneous concentration, and λ is defined as λ = 1/i 2 cr , where i cr is the ratio of the standard deviation of the relative concentration σ r to the mean relative concentration (see Section 2.6). On the other hand, the instantaneous plume centroid in x meanders stochastically [65] and this can be described by a probability density function p m (x, y m , z m ) associated to the coordinates y m and z m . We can suppose the statistical independence of the transverse meandering from the vertical one, previously postulated by Gifford (1959), thus giving: There are no theoretical considerations supporting this hypothesis; however, it is justified by the need to keep the model relatively simple, and it is not contradicted by any other experimental evidence. lence are nearly steady-state and horizontally homogeneous, the horizontal meandering of the plume centroid can be described using a Gaussian PDF: Indeed, in the vertical direction this homogeneity cannot exist, due to the action of the soil as a lower bound to dispersion and, in convective conditions, for the action of the PBL top z i as upper bound. However, the simplest PDF that describes a realistic vertical meandering motion of the centroid of the instantaneous plume (principally in near neutral conditions) considers only the interaction with the ground, and therefore: where y s and z s are the emission point coordinates. In these equations, σ ym and σ zm are the meandering dispersion parameters in horizontal and vertical direction and will be described in Section 2.6. For a generic instantaneous plume with the centroid in position (y m , z m ), described by PDF (8) and (9), the relative average concentration, C r , of the instant plume is where U m is the mean wind velocity at the height z m and Q is the constant emission rate. For the quantification of C r , the explicit forms of the PDFs, statistically describing the relative transverse and vertical dispersion, are needed. The relative dispersion is fully represented by the following two relationships: Further, in this case, a completely Gaussian relative transversal dispersion has been assumed, given the lack, in the hypotheses considered, of lateral barriers to the plume. Regarding the vertical relative dispersion, only the soil-bound has been considered. In order to make these PDFs effectively calculable, the standard deviations σ yr and σ zr must be known. Detailed explanation will be given in Section 2.6.
Taking all this into account and assuming an instantaneous concentration fluctuating according to a Gamma distribution, the n -th moment of the concentration is obtained by placing the (1), (6), (7), (8), (9), and (10) in (2). The result is the complex relation (13), which cannot be solved analytically due to the presence of some integrals, which quantifies both the average value and any n -th moment of the concentration. In order to effectively calculate the average concentration and the variance, which are indispensable parameters for the quantification of olfactory annoyance, it is first necessary to know the analytical relations that express the different variances present (those relevant to the meandering movement and those relevant to the relative dispersion) and the parameter i 2 cr necessary for the complete definition of the Gamma distribution (see Equation (6)).
This is the main result obtained by Marro et al. (2015), but also the starting point for the development of our Steady State Gaussian Fluctuating Plume.

New Operational Gaussian Fluctuating Plume Model
The estimation of the olfactory annoyance requires to quantify the odorants peak concentration defined as an appropriate percentile C p of the instantaneous concentrations collected within one hour: this can be achieved from a PDF able to describe the instantaneous concentration. If this PDF is a two-parameter distribution (such as a Log-Normal, a Weibull, or a Gamma), then the knowledge of the hourly spatial distribution of the mean concentration and the variance of the concentrations are sufficient to obtain the peak.
Our objective is, firstly, to obtain, from relation (13), for a generic n -th moment (uncentered), the appropriate relations for the average concentration C and for the variance of concentrations σ 2 C and, secondly, to simplify these relations by making them suitable for screening and regulatory use.
Equation (13), obtained by Marro et al. (2015), is totally general if the assumptions of applicability of a plume model are valid. Its practical applicability, however, is not straightforward, since it contains some integrals requiring a numerical solution. However, assuming the simple hypothesis that i cr depends only on the downwind distance x [54], it is possible to analytically solve the integrals in (13) and finally obtain a totally algebraic relationship, even if rather complex, for the generic n -th moment (uncentered) of the instantaneous concentration: where n k is the binomial coefficient n! k!(n−1)! . Considering (n = 1), we obtain the Gaussian relationship for the spatial distribution of the mean concentration for a Gaussian plume: Remembering the property of Euler's Gamma function Γ(1 + λ) = λ · Γ(λ) and that 1 k = 1 for k = 0, 1 the relation (15) is reduced to: i.e., the usual steady-state Gaussian relation for the mean concentration when only the ground reflection of a steady-state plume is considered. In this relation, the parameters σ y and σ z of the absolute dispersion are set equal to σ 2 y = σ 2 ym + σ 2 yr and σ 2 z = σ 2 zm + σ 2 zr , respectively. The λ parameter is not present in this equation, so C does not depend on the PDF: it depends only on parameters of the absolute dispersion.
Proceeding the analysis and setting n = 2, it is then possible to obtain the spatial distribution for the Gaussian plume uncentered second concentration moment: zr , the second uncentered moment assumes the following analytical form: Differently from the mean concentration, the second uncentered moment explicitly depends on the PDF parameter λ, which statistically describes the fluctuations of the instantaneous plume, and depends both explicitly and separately on the horizontal and vertical parameters that characterize the relative dispersion and meandering of the plume centroid.
Finally, the steady-state Gaussian Fluctuating Plume Model thus obtained consists of the following two equations: Equation (16) for the mean concentration and Equation (18) for its second moment. The concentration variance is equal to the second uncentered order moment minus the square of the mean concentration (see Equation (4)). Then, the standard deviation of the concentration is the root square of the concentration variance. This is the general form of the new steady-state Fluctuating Gaussian Plume Model used in the following.

Peak Concentration
Obtaining direct information about the concentration PDF is currently only possible by using extremely complex modelling techniques such as DNS (Direct Numerical Simulation) [71,72] and LES (Large Eddy Simulation) [73,74] modelling. However, these techniques, together with the complex techniques known as PDF methods [11], can only be applied to limited spatial domains and time intervals, far from the needs of applications of practical interest. When, therefore, one needs to tackle the olfactory annoyance generated by an industrial source to the surrounding population over a whole year, it is necessary to choose different methods.
As it is well-known, full knowledge of the instantaneous concentration PDF would be achievable if its infinite relative statistical moments were all known. Realistically, only the budget equations for some of the statistical moments can be written and (numerically) integrated, and therefore it is necessary to introduce some empirical elements in the PDF identification process. In the Eulerian budget equation for a generic n -th moment (e.g., the second one) there are terms dependent on the n + 1 -th moment [8], and therefore also simple integration of this equation needs the introduction of appropriate closures that parameterize these terms. Normally, when the interest is on the PDF of instantaneous concentrations c, as primary closure the hypothesis of a known a priori PDF, statistically describing c, is introduced. For example, if the PDF is a two-parameter distribution, it will be sufficient to know the field of the mean value and the concentration variance at each point of the calculation domain and at each moment.
Different studies [41,44,63,70,[75][76][77][78] tackled the problem of identifying the type of PDF on the basis of various experimental measurements carried out in laboratory studies and in the atmosphere, but without reaching a decisive conclusion. The most common are the exponential, the clipped normal, Log-normal, Gamma, and Weibull. The Log-Normal is simple, but it is the stiffest [79]. In other works [80,81], exponential and clipped normal PDF are also supported. Currently, two of the most considered PDFs were used to calculate the peak concentration: the Gamma [24] and the Modified Weibull [82,83]. The PDF Gamma [84] is very complex, but it is the most adaptable: due to this, it is probably the most suitable for dealing with the statistics of concentration fluctuations. Anyway, what emerges is that the actual PDF tends to be exponential near the emission source, while at great distances downwind its shape is much more symmetrical, therefore similar to a Log-Normal. Interesting are the observations made by Nironi et al. (2015) [55] analyzing the numerous measurements obtained in the wind tunnel. Authors state, "these findings clearly support the existence of a universal function for the PDF of the concentration." Moreover, they show how the measures suggest the adoption, at least in first approximation, of a Gamma PDF type, precisely for its adaptability. It is worthy to remark, however, that also the Weibull distribution has similar characteristics.
Known at (x,y) the mean concentration C, its variance σ 2 c and so the concentration intensity i c , adopting as PDF a Gamma distribution or a Weibull distribution, it is then possible to obtain the n -th percentile concentration C n . According to the German legislation [36], the percentile of interest is the 90th: in this way, the 90th percentile of the sub-hourly concentration, C 90 , can be considered as the peak concentration, C p . Accordingly, the peak-to-mean can be defined as R 90 = C p C . Even though the Gamma distribution seems to be the most realistic distribution, the fact that it does not allow the obtainment of the R 90 in analytical form makes its practical use complex. Nevertheless, in the present study, Gamma PDF is considered as well, by setting a zeroing cycle for the calculation of the Gamma's R 90 .
Much simpler is the use of the Weibull distribution. The two-parameter modified Weibull distribution is described as [83]: where the scale parameter λ and the shape parameter k are given by and Γ( . . . ) is the Gamma Function. After substitution, for calculating the R 90 we used: The interesting result obtained is represented by (21), which expresses the R 90 ratio between the peak concentration C p and the average concentration C, dependent on i C .
Both when the intensity of concentration tends to zero and when it tends to infinity the value of R 90 is finite and limited, and this implies that there is a value for i C for which R p is maximum. Numerically, we can see that for p equal to 90

Mean Concentration
The first result obtained from the model is the average concentration, obtained with Equation (16). Cm values were calculated for each sampling position of each crossbar, for each trial. A total of 132 values were collected from the model. These values were com-  B T2P4  C T1P5  C T2P4  D T1P3  D T2P3  E T1P3  E T2P2  F T1P2  F T2P2  G T1P2  G T2P2  H T1P4  H T2P3  I T1P4  I T1P9  J T1P4  J T1P8  K T1P4  K T1P9  L T1P4  L T1P9  Mean Concentration 90° Percentile Maximum Concentration

Dispersion Parameters and Relative Concentration Intensity
According to the hypotheses on which the Fluctuating Plume is based, the relationships between the parameters describing the absolute dispersion of the plume (y, z), those that describe its relative dispersion (y r , z r ) and the parameters that describe the meandering of the centroid of the instant plume (y m , z m ) are where T Lv = 2σ 2 v C 0 ε and T Lw = 2σ 2 w C 0 ε are the Lagrangian decorrelation time scales, σ 0 is the characteristic source dimension (σ 0 is calculated as σ 0 = D 2.15 [86], where D is the internal diameter of the stack), C 0 = 4.5 is the Kolmogorov constant and, finally, ε is the mean turbulent kinetic energy dissipation rate.
• the longitudinal and vertical dispersion parameters for the relative dispersion can be expressed from the following relationships: with the characteristic times T my = αT Lv and T mz = αT Lw considering a constant value of α equal to two. Taking the expression for σ 2 yr as example, it must respect two asymptotic conditions [51,87]. The first one holds when t→0; in this case, σ yr takes the asymptotic form: where C r is the Richardson-Obukhov constant equal to 0.8 and t s is the time necessary for the plume to expand until it reaches dimension σ 0 , so t s = σ 2 0 /(C r ε) 1

/3 (Monin and
Yaglom, 2007). The second one holds when t→∞ and in this case: The intensity of the relative concentration i cr is a key parameter to fully define the Gamma probability distribution that characterizes the relative dispersion of the instanta-neous plume, and therefore to actually obtain the various moments (including the average) through the relationship (14). However, this parameter has rarely been measured experimentally or numerically. Only few works available on the subject [55,88]. Given the scarce knowledge on the subject, a 1D model has normally been adopted for the estimation of i cr relating this parameter only to the downwind distance. Marro et al. (2015) considered for i cr both a 1D model and a 3D model; however, they have shown how only with a 1D model the relationship (14) can be analytically integrated. Since our goal is to obtain a plume model easy to use and suitable for carrying out preliminary impact assessments, supported also by the observations that a 1D model for i cr leads to reasonably correct results [54], only the 1D models according to which i cr = i cr (x) will be considered below.
Analysis [49] of experimental measurements [89,90] did not allow to univocally identify a relation for i cr and operationally the cited work hypothesized to place i cr = 1, so λ = 1. This assumption, not contradicted by the experimental evidence, implies the representation of the concentration fluctuations of the instantaneous plume as an Exponential distribution because a Gamma distribution is reduced to it when α = 1. In practice, this means that at great distances from the emission all concentration fluctuations depend on the internal fluctuations of the instantaneous plume and meandering is negligible. In the light of the experimental evidence considered, this assumption for i cr while being realistic was not completely satisfactory, although from the analyses made in the work cited this simple model for i cr leads to a reasonably limited error.
Crucial at this regard are the measurements made inside a wind tunnel in near-neutral conditions [55]. Based on them, the authors developed a new 1D model that makes i cr depend on the normalized downwind distance ξ = x/z i , (z i is the PBL top) according to where the coefficients p 1 , p 2 , p 3 , q 1 , q 2 , q 3 depend on the height of the source, its characteristic dimension σ 0 and the vertical extension of the PBL. The experimental measurements of refer to three different types of sources [55]. In applications related to olfactory annoyance it is recurring to consider low source without buoyancy. Accordingly, it would seem appropriate to use the lower-level source (LLS) coefficients in the model here developed. The values of the coefficients are indicated in Table 1.

Software Implementation
The model here presented has been implemented in Matlab R2019b. The use of a Matlab code was due to a fast implementation of this prototypal approach.
The code was divided into the following different sections: • Meteorological and micrometeorological input data • Emission source data • Calculation of average concentration • Calculation of concentration standard deviation and concentration intensity • Peak percentile calculation (with a PDF-dependent choice, Gamma, or Modified-Weibull).
The calculation domain was fixed as a square of 800 m × 800 m dimension, with a mesh grid of 10 m.
For the calculations, a laptop computer with 4 parallel processors, 1.8 GHz CPU and 16 GB RAM was used. The computational time needed of each trial was dependent on the chosen PDF: for the Modified Weibull it was about 1 s, while for Gamma, which needs a zeroing for the calculation of R 90 , it was 5 s.

Uttenweiler Field Experiment
In this paragraph, we only provide a short description of the field dispersion experiment, with the aim to make the understanding of the results easier. Further details regarding the experimental campaign (e.g., chemical analysis) are extensively described in the field test report [56]. The campaign was conducted in a pre-existing pig farm in three different days: 12 and 13 December 2000 and 31 October 2001. The farm is located outside the small village Uttenweiler, 20 km west of the city of Bielberach (48.136 • N, 9.652 • E) in Germany. The surrounding area is mostly flat and has only slight elevations and nearly congruent with the validity hypotheses of a Gaussian Plume Model. This farm consists of the pig barn and the feed processing room. These are two buildings with a height of 7.7 and 10.6 m, respectively. The gas tracer, sulphur hexafluoride (SF 6 ) were continuously emitted by a single point source on the smaller building. It was at 8.5 m above the ground level, and it was connected to the internal ventilation system. The column was the union of three shafts (338 cm × 107 cm) guided into one of area 1.2 m 2 . 14 trials were performed, named in alphabetical order from B to O: the experiment A was an attempt. In the lee of the building, one (experiments I to L) or two receptor transepts (experiments A to H) were arranged, perpendicular to the direction of wind. Five to six measurement point are posed on each of these crossbars; each test site had an air sampler to record the SF 6 concentrations averaged over the measurement period of 10 min. Fast-response concentration measurements of SF 6 were also taken. They were carried out with a sampling rate of 0.1 Hz at two receptors, and then analyzed by gas chromatography. In the south-southwest region under consideration, at 150 m from the source and a height of 3.5 m, an ultrasonic anemometer (USAT) was placed. It was operated with a frequency of 10 Hz. The ultrasonic anemometer/thermometer data were analyzed and averaged over 30 min according to methodology normally used by Eddy Covariance [91]. Wind direction and wind speed were also recorded by means of a cup anemometer placed at 10 m above the ground level. During the experiments of 31 October 2001 the meteorological column broke down, so the measurements were carried out on an auxiliary shaft at a height of 2 m. The measurement points are identified using an acronym: T for "Traverse" that represents the crossbar, and P for "Proband" that represents the subject that occupies the point where the measurements take place; T and P are followed by a number that indicates which of the two crossbars and which of the twelve positions on the crossbars.

Meteorological Data Setting
Eleven experiments have been considered, B-L: shortcomings in the acquirement of sonic input data for the trials M, N, and O made the evaluation for these datasets not reliable. Particular attention, by the authors of the test, was paid to carry out the field trials with a stable/neutral atmosphere. In these conditions, the horizontal meandering effect can cause problems to describe the intermittency naturally present at the transversal limits of the plume [46]. Moreover, Gaussian models are not able to consider in an efficient way the horizontal meandering naturally present in nature. As evidence of this phenomenon, there is a large range of angles of wind direction measured by the sonic anemometer during every trial (Table 2). In order to overcome two possible problems, it was decided to do a data tuning for the wind direction. The first reason was that the mean concentration data, for this field experiment, are available on the average time of ten minutes and not of an hour (which is the standard averaging time for a simple Gaussian model). The second and most important reason is that the aim of this work was not the test of the mean concentration, but to provide a simple way to assess of σ c , I c and R 90 . Therefore, it was necessary to obtain mean concentration values as much consistent as possible.

Performance Evaluation
In order to evaluate the reliability of the model, in a simplified and analytical way, it was decided to calculate some statistical indicators [92][93][94][95]:, mean bias (MB), normalized mean bias (NMB), root mean squared error (RMSE), normalized mean squared error (NMSE), index of agreement (IOA) and the fraction of predictions within a factor or two (FAC2). The following equations report the calculation methods: where M i is the single modelled value and O i is the single observed value. All these parameters have ideal values: MB = 0, NMB = 0, RMSE = 0; FAC2 = 1; IOA = 1. We also used regression lined scatter and quantile-quantile plots [96].

Raw Data Processing
The first step was the elaboration of input data. The meteorological conditions, micrometeorological data and emission rates, the considered trials, and the meteorological conditions for each trial, are reported in Table 2. Due to the considerations reported in Section 3.3, the penultimate column of Table 2 shows the wind direction that has been used for the simulations. As reported, the chosen values are fully within the range of wind directions measured over the 10 minutes of each trial.
The second step was to elaborate the fast-response ambient concentration data (Table 3). R 90 was calculated from the ratio of the 90th percentile (C 90 ) of the fast-response concentrations and the mean concentration. The 90th percentile was obtained considering the extremes of the series. To make the elaboration of the raw data reported in Table 3, a graph is presented (Figure 2). In this graph it is possible to compare the values of C m (blue bar), 90th percentile (brown bar) and C max (yellow bar) reported in (µg/m 3 ) for every fastresponse concentration point of measurement. The colored columns show the relationship between the three variables. For B T1P5, D T1P3, and D T2P3, the values are very low compared to the scale of the other points. Their values are anyway readable in Table 3. Table 3. For every fast-response point of measurement, mean concentration, peak concentration, standard deviation of concentration, intensity of concentration, 90th percentile concentration and R 90 are reported. The receptors are indicated as TP, where T is the crossbar and P represents the subject which occupies the point where the measurements take place. The numbers indicate which of the two transvers and which of the twelve positions.

Trial
Receptor

Mean Concentration
The first result obtained from the model is the average concentration, obtained with Equation (16). C m values were calculated for each sampling position of each crossbar, for each trial. A total of 132 values were collected from the model. These values were compared with experimental 10-min data measurements. As mentioned in the field experiment document [56], measurements taken from deflated bag were considered unreliable and were removed from the comparison. To evaluate the quality of the model, performance parameters and some graphs are presented. Table 4 shows the results obtained from the performance evaluation: it is worth to remark that 72% of the values lies within a factor of 2 of the observations (FAC2). Moreover, parameters like MB and NMB are very close to the ideal zero value. A scatter plot was then drawn to help the reading of the results (Figure 3): it reports the simulated values (y-axis) of C m , plotted towards the field data (x-axis). The bisector (1:1), representing a perfect model, and the two lines of FAC2 (1:0.5, 1:2) representing a factor of two from the perfect value, have been highlighted. The linear trendline was added, obtaining an angular coefficient of 0.7778 (showing a slight underestimation of the average concentration values by the model), an intercept of 1.066 (exhibiting fairly low bias) and a R 2 = 0.6054 (denoting a low dispersion of the data). This agreement between the average concentrations data was considered better than acceptable.

Trials
MB NMB RMSE NMSE IOA FAC2 All cases (B-L) 5.6 -0.2 -0.03 4.5 0.7 0.88 72% A scatter plot was then drawn to help the reading of the results (Figure 3): it reports the simulated values (y-axis) of Cm, plotted towards the field data (x-axis). The bisector (1:1), representing a perfect model, and the two lines of FAC2 (1:0.5, 1:2) representing a factor of two from the perfect value, have been highlighted. The linear trendline was added, obtaining an angular coefficient of 0.7778 (showing a slight underestimation of the average concentration values by the model), an intercept of 1.066 (exhibiting fairly low bias) and a R 2 = 0.6054 (denoting a low dispersion of the data). This agreement between the average concentrations data was considered better than acceptable.

Standard Deviation of Concentration,
The results obtained from the model for the standard deviation of the concentration are shown in Figure 4. The Figure reports the simulated values (y-axis) of σc, plotted towards the field data (x-axis). It should be reported that, in certain experiments, the modelled values at the fast-response detector locations of the mean concentration are equal to 0. For this reason, the standard deviation is forced to 0 by the model. In the graph of Figure  3, only nonzero values are shown. The bisector line 1:1, the 1:0.5, and the 1:2 lines are also graphed. It is possible to note that 60% of all the points are within the FAC2 range. The

Standard Deviation of Concentration, σ c
The results obtained from the model for the standard deviation of the concentration are shown in Figure 4. The Figure reports the simulated values (y-axis) of σ c , plotted towards the field data (x-axis). It should be reported that, in certain experiments, the modelled values at the fast-response detector locations of the mean concentration are equal to 0. For this reason, the standard deviation is forced to 0 by the model. In the graph of Figure 3, only nonzero values are shown. The bisector line 1:1, the 1:0.5, and the 1:2 lines are also graphed. It is possible to note that 60% of all the points are within the FAC2 range. The linear trendline was added, obtaining an angular coefficient of 3.14 (showing a relevant overestimation of the standard deviation by the model), an intercept of −6.19 (exhibiting negative bias) and a R 2 = 0.3 (denoting a moderate linear relationship). the measurement tool. For this reason, it suffers two kind of data losses: low frequency losses due to the finite mediation time and high frequency losses due to the analyzer's response time. The measured standard deviation of the concentration is forced to decrease. The overestimation of the model presented is therefore someway expected.
Despite these "Signal theory" dissertations, considering the simplicity of the model, the modelled data are considered acceptable. It is important to make some considerations regarding this comparison. The modelled standard deviation of concentration theoretically represents the standard deviation of the instantaneous sequence of concentration data. On the contrary, the experimental standard deviation, brought as a comparison to the model, is far from instantaneousness. This is the result of a not-instantaneous data sampling time (10 s) and the non-ideality of the measurement tool. For this reason, it suffers two kind of data losses: low frequency losses due to the finite mediation time and high frequency losses due to the analyzer's response time. The measured standard deviation of the concentration is forced to decrease. The overestimation of the model presented is therefore someway expected.
Despite these "Signal theory" dissertations, considering the simplicity of the model, the modelled data are considered acceptable. Figure 5 reports the simulated values (y-axis) of I c , graphed towards the field data (x-axis). For the reason mentioned above, also in this graph the comparative points are reported only for the not-null calculated concentration intensity. The bisector line 1:1, the 1:0.5, and the 1:2 lines are also reported. It is possible to see that 40% of the value is within the range of the FAC2. Then, the linear trendline was added, obtaining an angular coefficient of 0.71, an intercept of 1.87 and a R 2 = 0.11. The correlation coefficient of 0.33 indicates a moderate linear relationship. Figure 5 reports the simulated values (y-axis) of Ic, graphed towards the field data (xaxis). For the reason mentioned above, also in this graph the comparative points are reported only for the not-null calculated concentration intensity. The bisector line 1:1, the 1:0.5, and the 1:2 lines are also reported. It is possible to see that 40% of the value is within the range of the FAC2. Then, the linear trendline was added, obtaining an angular coefficient of 0.71, an intercept of 1.87 and a R 2 = 0.11. The correlation coefficient of 0.33 indicates a moderate linear relationship.

Intensity of Concentration, I c
Remembering that the intensity of concentration is the ratio between the standard deviation of concentration and the mean concentration (see Equation (5)), it is possible to highlight that the biased behavior of overestimation of the standard deviation propagates to intensity of concentration.
It appears that the model does not perfectly describe the physical phenomenon, but the value of FAC2 is not poor considering the simplification of the model.

Peak-to-Mean Factor, R90
The R90 was calculated considering both the Gamma and the Modified Weibull [83] as representative PDF for the instantaneous ambient concentration. In Figure 6 Remembering that the intensity of concentration is the ratio between the standard deviation of concentration and the mean concentration (see Equation (5)), it is possible to highlight that the biased behavior of overestimation of the standard deviation propagates to intensity of concentration.
It appears that the model does not perfectly describe the physical phenomenon, but the value of FAC2 is not poor considering the simplification of the model.

Peak-to-Mean Factor, R 90
The R 90 was calculated considering both the Gamma and the Modified Weibull [83] as representative PDF for the instantaneous ambient concentration. In Figure 6, the results for the peak-to-mean factor are reported. The orange results refer to the Gamma PDF and the blue ones to the Modified Weibull. It is possible to see the simulated values (y-axis) of R 90 plotted in ordinate towards the field data (x-axis). On Figure 6a Table 5. Because of the presence of the factor 1.5 (see Equation (21)), present in the Modified Weibull, the results for this PDF show higher values. On Figure 6b a q-q plot is reported. The results do not lay strictly on the bisector, but very similar trends can be seen for both PDFs: the obtained data seem to be diverse only for a static translation, probably due to the presence of the "safety factor" 1.5 [97].  Table 5. Because of the presence of the factor 1.5 (see Equation (21)), present in the Modified Weibull, the results for this PDF show higher values. On Figure 6b a q-q plot is reported. The results do not lay strictly on the bisector, but very similar trends can be seen for both PDFs: the obtained data seem to be diverse only for a static translation, probably due to the presence of the "safety factor" 1.5 [97].   Figure 7, the predicted R90 contour plots calculated testing the Gamma PDF are shown for all considered trials, while in Figure 8 the predicted R90 contour plots calculated testing the Modified Weibull. Even in these graphs, it is clear that the values calculated using the Modified Weibull are higher than those obtained with the Gamma PDF as a reference. Figures 7 and 8 provide further information with respect to the scatter plot and   Figure 7, the predicted R 90 contour plots calculated testing the Gamma PDF are shown for all considered trials, while in Figure 8 the predicted R 90 contour plots calculated testing the Modified Weibull. Even in these graphs, it is clear that the values calculated using the Modified Weibull are higher than those obtained with the Gamma PDF as a reference. Figures 7 and 8 provide further information with respect to the scatter plot and q-q plot. It is possible to see that the values of R 90 vary along the plumes. Not precisely at the emission source (located in the domain center) but in the strict proximity, there are higher R 90 values (yellow-orange areas). This result depicts a different trend with respect to the one proposed by empirical peak-to-mean literature [17,22]. They proposed a monotonic trend for the peak-to-mean value, maximum at the emission and decreasing with the downwind distance. Here-obtained results depict a non-monotonous R 90 trend, with a peak near the source but not at the emission, then decreasing with the downwind distance, as proposed by [17,22]. This model shows a greater complexity, due to the non-unique dependence on the distance. Another observation evident from Figures 7 and 8 is that R 90 increases with distance from the plume centerline. This evidence is in accordance with the theory of Best [98]. Referring to the cited paper, the dependency of the peak-to-mean factor from y is exponential and R 90 increases by getting closer to the extremes of the plume, according also to experimental evidences [44,77]. Reaching the edges of the domain, the colors of the figures indicate decreasing values with distance. A characteristic shape, in certain experiments V-shape, in others Y-shape, is formed because of these dependences on x and y (lighter yellow). All these considerations are valid for both the Gamma and the Modified Weibull PDFs. It is important to note that the obtained values fall between 1 and 4, in particular 1-3 for the Gamma PDF and 1.5-4 for the Modified Weibull. More in detail, the dispersion of the points in the scatter plot for both the PDFs is evident. This can be explained by considering that the physics of the model is not completely satisfactory: there is not a monotonic trend between the simulated values of R 90 and the experimental ones. Similar tendency of dispersion is evident also in [99], where the authors tested a new approach: the use of Lagrangian Particle Model LASAT coupled with the implementation of the concentration-variance transport and the Modified Weibull [83].
On the other hand, the q-q plot shows a tendency to the overestimation of the model with respect to the experimental values. In particular, it appears that, for both the considered PDFs, the model often provides upper limit values, which are equal to three and four for the Gamma and the Modified Weibull PDF, respectively [41]. This tendency to an asymptotic value is due to the choice to define the sub-hourly peak as the 90th percentile of the instantaneous concentration value. In fact, as mentioned in Section 2.5, the trend of R 90 as function of I c shows an upper limit value. As mentioned above, the obtained upper limit value depends on the hypothesized representative PDF.
Another observation can be made on the obtained peak-to-mean range: all the results fall between 1 and 4. In particular, overall-sample average peak-to-mean values have been calculated: the mean value corresponding to the Gamma PDF is 2.7; the mean value for the Modified Weibull is 3.2. Even though this represents a very rough estimation, it can be useful in order to compare it with the laws in-force.
Moreover, these values are comparable to the values obtained by using the concentrationvariance transport implemented in GRAL [41,97]. In a recent paper by the authors [82], the overall time and space value for the R 90 turned out to be equal to 2.5, which is comparable with the data here presented. Despite the points of the scatter plot (Figure 6a) exhibit quite dispersed data, it is important to note that the range of obtained R 90 appears reasonably narrow.
As reported diffusely in the scientific literature [41,100,101], the German constant peakto-mean value, set equal to 4 [36], appears to be rather conservative: this value represents the upper limit value for the R 90 obtained by considering the Modified Weibull PDF. With regard to the most recently investigated value [82] used in Italian regulations, equal to 2.3 [38][39][40], this shows a more halfway behaviour, laying amid the obtained calculated and experimental value.

Experimental Underestimation of Peak-to-Mean
It is necessary to compare the modelling outputs with the experimental evidence reported in the literature. This comparison hides a tricky problem. The measurements obtained experimentally consist of concentration measurements produced by the various analyzers with a generic "high-frequency", whose dynamic characteristics are not usually reported in a clear and exhaustive way. From these data, the concentration intensities and P/M ratios are deduced. It would therefore seem that, with few exception [44], concentration intensities and P/M ignore any possible correction that takes into account the filtering effect of the other frequencies. These measurements are produced by an analyzer, which in general, follows a first order linear system with characteristic time τ [102]. Due to this, as shown in the micrometeorological and agrometeorological literature [91,[103][104][105][106], also the sample variance produced by the analyzers at the basis of the sample estimation of concentration intensity and P/M is a clear underestimation of the real variance, theoretically obtainable with an ideal concentration measurement tool (i.e., with a null response time). The ratio between the two variances (sample and real) in stable situations can reach very high values. Therefore, the sample variance, produced by analyzers, far from truly being "fast", is an underestimation of the real variance. From this, the intensity of concentration is also an underestimation of reality. This problem also has consequences in the calculation of P/M. The experimental evidence and the PDFs taken as a model of the statistics of a passive gas in the Surface Layer clearly show that there is a relationship between concentration intensity and P/M. It presents a maximum and this prevents us from saying a priori whether the spectral losses accumulated in the estimation of the variance eventually lead to an underestimation or an overestimation of the P/M. Therefore, regarding the values of P/M found in the literature, there is an associated an intrinsic positive or negative uncertainty that is difficult to be quantified, in the light of the few or non-existent information related to the analyzers used by various authors. This makes it difficult to make a comparison with the modelling outputs that, if the physical and theoretical basis are correct and complete, can only produce estimations to which no-intrinsic uncertainty can be associated.

Conclusions
Atmospheric dispersion modelling has a key role in the study of environmental odors. Unlike the study of macro-pollutants, for odor impact assessment, the calculation of the short-term peak odor concentrations is fundamental. For this purpose, in this article a simplified and analytical Fluctuating Plume Model [54] is tested. It is fundamental to point out the merits of this model: it is very simple, and the equations of the mean and variance concentration can be worked out analytically. This model was here used to verify if it can provide reliable data, not only for the mean concentration, but also for σ C , I c and R 90 . Moreover, for the calculation of the peaks, PDFs are necessary: Gamma and Modified Weibull PDFs were tested here. Different conclusions can be drawn from the present work.
The difficultly of Gaussian models to consider the horizontal meandering that is naturally present in nature was corroborated. For the scope of this work, wind direction data were tuned in order to fit the plume transversal limits. Seventy-two percent of the simulated mean concentration values fell within the range of the FAC2 with respect to the experimental ones. Good results are also obtained looking at the linear regression line. Moreover, the model here presented and developed, has the aim to calculate concentration variance, in order to use it for the estimation of the peak-to-mean factor R 90 . Both the results for σ C and I c provide an overestimation of the experimental data. This result is strictly linked with the data losses due to the non-ideality of the measurement system: the non-theoretically instantaneous sampling (0.1 Hz) and the response time τ contribute to the flattening of the instant concentration data and so cause a decrease of the sample variance.
The propagation of the errors from I c data to R 90 is very complex due to the introduction of the relationships of the chosen PDF. Nonetheless, the obtained data for R 90 show a dispersed behavior with respect to the experiment, but the ranges covered are quite repeatable: the P/M obtained values are 1-3 for the Gamma PDF and 1.5-4 for the Modified Weibull PDF, with experimental values ranging from 1.4 to 3.6. This finding can be linked to the R 90 trend with respect to I c : depending on the PDF, different maximum values are reached: three and four for the Gamma and the Modified Weibull, respectively.
The obtained results highlight the variability of ambient odor concentration fluctuations, which cause great confusion in complaints from citizens close to industrial activities. The model here presented is theoretically designed for neutral/slightly stable situations: in this work, the comparison was made only in neutral conditions. A future perspective could be the use of different atmospheric stability situation to test this kind of analytical models. One goal is to make it usable even in less ideal conditions. On the other hand, a limitation of the work presented here, is its inapplicability in calm wind conditions: unfortunately in these conditions the Gaussian plume models are not applicable due to the mathematical formulation that requires the presence of the wind speed term in the denominator. A further crucial point that has to be taken into consideration when "high-frequency" concentration data are used: spectral losses are implicit when using non-ideal sensors. Unluckily these considerations are very scarce in the odor nuisance research field: the considerations made in this paper could be a first step for further reflections for the development of future experimental field campaigns.
In the most advanced models, the PDFs need to be evaluated in a consistent statistical way. For this reason, it is also crucial to deepen the scientific knowledge on probability density functions, which can well describe the ambient instantaneous concentration. All these adjustments for the calculation of fluctuations will allow to modify odor legislations accordingly, with the final aim of improve the quality of life of population.