1. Introduction
The filtration of solutes and suspended particles through porous media is a fundamental process across a broad spectrum of industrial and natural systems, ranging from groundwater remediation and reactive decontamination (Luckins et al. Reference Luckins, Breward, Griffiths and Please2024) to the applications in pharmacology (Khanafer & Vafai Reference Khanafer and Vafai2006) and the complex drying processes in capillary media (Luckins Reference Luckins2025). In high-performance applications, such as membrane science and microfluidic sorting, filters are increasingly engineered with spatially variable textures – known as graded filters – to optimise the trade-off between separation efficiency and hydraulic resistance. To design such devices effectively, a rigorous understanding of how microstructural heterogeneity governs macroscopic transport, phase change and adsorption is essential (Battiato et al. Reference Battiato, Ferrero, P., O’Malley, Miller, Takhar, Valdés-Parada and Wood2019). However, the multi-scale nature of these media often renders direct numerical simulation (DNS) of the full Navier–Stokes and advection–diffusion equations computationally prohibitive for design optimisation.
Asymptotic homogenisation (namely the method of multiple scales) provides a powerful framework for bridging these scales, allowing the derivation of effective macroscopic equations that retain the influence of the underlying micro-geometry (Mei & Vernescu Reference Mei and Vernescu2010). Traditionally, these methods rely on the assumption of a locally periodic microstructure. While highly successful for uniform media, standard homogenisation is inherently limited when addressing graded filters where porosity gradients are explicitly introduced to enhance performance. Recent extensions have addressed near-periodic domains, for instance, through curvilinear coordinate transformations in biological tissues (Richardson & Chapman Reference Richardson and Chapman2011; Penta et al. Reference Penta, Ambrosi and Shipley2014, Reference Penta, Ambrosi and Quarteroni2015) or through the assumption of slowly varying properties. A significant advancement in this direction was made by Bruna & Chapman (Reference Bruna and Chapman2015), who derived homogenised equations for transport through obstacles with slowly varying radii. This framework was subsequently applied by Dalwadi et al. (Reference Dalwadi, Griffiths and Bruna2015) to analyse how porosity gradients influence filtration efficiency, and later extended to account for varying obstacle spacing (Auton et al. Reference Auton, Pramanik, Dalwadi, MacMinn and Griffiths2022), the influence of microstructure and clogging (Dalwadi et al. Reference Dalwadi, Bruna and Griffiths2016; Printsypar et al. Reference Printsypar, Bruna and Griffiths2019), and dispersive transport and sorption in heterogeneous porous media (Auton et al. Reference Auton, Dalwadi and Griffiths2025). Recent work has also examined adsorption and sieving in graded pore networks (Gu et al. Reference Gu, Sanaei, Kondic and Cummings2026); although based on a network rather than a homogenised continuum model, it further illustrates the strong dependence of filter performance on the chosen grading and fouling mechanisms.
There are two related formal descriptions of slowly varying microstructure in the multiple-scales literature. In one, the physical interface is constructed by a two-scale level set and its normal is expanded consistently with that construction, as was performed by Bruna & Chapman (Reference Bruna and Chapman2015) and Klika & Gaffney (Reference Klika and Gaffney2023). In the more traditional parametrised-cell formulation, the normal is retained as a prescribed field of both slow and fast variables; applying transport identities then produces additional geometric terms (Burridge & Keller Reference Burridge and Keller1981; Holmes Reference Holmes2013; Penta et al. Reference Penta, Ambrosi and Shipley2014, Reference Penta, Ambrosi and Quarteroni2015). We use the former construction because the present geometry is specified explicitly by obstacles with slowly varying radius. To the best of our knowledge, the two descriptions have not been proved to be equivalent in general. Our derivation is a formal locally periodic expansion for the specified level-set geometry.
Despite these advances, most existing macroscopic filtration models assume that the fluid velocity field is solenoidal (
$\boldsymbol{\nabla }\boldsymbol{\cdot }\boldsymbol{u} = 0$
). While appropriate in certain situations (which we clarify later), this assumption may break down in systems where significant solute–solvent interactions or local volume changes occur during the adsorption process. In this work, we generalise the modelling framework of Dalwadi et al. (Reference Dalwadi, Griffiths and Bruna2015) by incorporating a non-zero divergence in the fluid velocity, derived from the principles of non-equilibrium thermodynamics and mixture theory (De Groot & Mazur Reference De Groot and Mazur2013; Klika Reference Klika2014; Klika et al. Reference Klika, Whiteley, Brown and Gaffney2019; Klika Reference Klika2021, Reference Klika2022). This modification introduces a fundamental coupling between the chemical species transport and the momentum balance, leading to the (mixture) velocity being non-solenoidal.
The paper is organised as follows. In § 2, we start by deriving the governing equations from non-equilibrum thermodynamics, namely from balance laws for a mixture of
$n$
components. Then, we formulate the microscopic model for a filter composed of a graded array of obstacles. We describe the transport of solute via advection and diffusion, with adsorption modelled as a flux condition on the obstacle surfaces and the mixture velocity non-solenoid. The governing equations are upscaled in § 3 to yield an effective macroscopic system where microscale heterogeneities are encapsulated in effective coefficients determined by local cell problems. Next, in § 4, we simplify the geometry to a unidirectionally graded filter, derive the corresponding boundary conditions at the filter boundaries and gain analytical insight again using asymptotic methods. Finally, in § 5, we solve the resulting equations for the simplified unidirectionally graded filter and examine the impact of the porosity gradient and the mixture coupling parameter on various efficiency metrics, comparing our findings with the classical solenoidal results to highlight the significance of realistic mixture dynamics in filter optimisation.
2. Filtration in a mixture of incompressible solute and solvent
We consider a filtration model consisting of solid obstacles in a domain
$\varOmega \subset \mathbb{R}^d$
, where
$d\in \{2,3\}$
denotes the spatial dimension. These obstacles may have a rather general geometry and the approach used here does not depend on their specific shape. However, to illustrate the general description, we assume that the filter is composed of
$d$
-dimensional balls arranged in a square (for
$d=2$
) or cubic (for
$d=3$
) lattice with spacing
$\delta l$
. The parameter
$\delta \in \mathbb{R}^+$
is assumed to be small and positive, and will later serve as the small parameter in asymptotic expansions as
$\delta \to 0$
. The length
$l$
represents the overall size of the filter.
We further assume that the radius of the balls varies with position throughout the filter, representing spatial inhomogeneity of the porous medium. The radius is described by the function
$\delta l R(\tilde {\boldsymbol{x}})$
, which defines the ball radius as a function of the spatial coordinate
$\tilde {\boldsymbol{x}}\in \varOmega$
. The function
$R(\tilde {\boldsymbol{x}})$
is assumed to be dimensionless. We denote the part of the space occupied by the balls as the solid domain
$\varOmega _s\subset \varOmega$
, representing the impermeable part of the filter.
We consider a mixture of fluid and solute flowing through the filter, where the solute represents the contaminant being removed. The region accessible to the fluid is denoted by the fluid domain
$\varOmega _{\kern-1pt f}=\varOmega \setminus \varOmega _s$
. To track the degree of contamination of the fluid, we introduce the (dimensional) solute concentration
$\tilde {c}(\tilde {\boldsymbol{x}},\tilde {t})$
, which depends on the spatial coordinate
$\tilde {\boldsymbol{x}}$
and time
$\tilde {t}$
. For convenience, we extend the definition of the concentration to the entire domain by assuming
$\tilde {c}(\tilde {\boldsymbol{x}},\tilde {t})=0$
for
$\tilde {\boldsymbol{x}}\in \varOmega _s$
.
The final key feature of the model is the ability of the filter to capture solute particles representing the contaminant. This process is modelled as adsorption of solute particles onto the surfaces of the balls. For simplicity, we neglect clogging effects and assume that the geometry and volume of the solid domain
$\varOmega _s$
remain unchanged during the filtration process.
2.1. Diffusion of incompressible mixture
Let us consider a mixture of
$n$
components. We start from general laws of physics, and finally move on to the above-mentioned specified mixture of the fluid and the solute.
For each component
$k$
of the mixture, the following balance of mass holds (De Groot & Mazur Reference De Groot and Mazur2013; Klika Reference Klika2014, Reference Klika2021, Reference Klika2022):
where
$\rho _k$
is the density of the kth component and
$\boldsymbol{u}_k$
is its velocity. The right-hand side of (2.1) can include a source term
$\hat {\rho }_{k}$
(Klika Reference Klika2014, Reference Klika2021, Reference Klika2022), but which we assume to be zero in our closed system, as we consider no reactions among the components. Thus, the density changes over time only due to material transport described by the term
$\rho _k\boldsymbol{u}_k$
.
The level of description that we choose is for a mixture of components whose movement cannot be tracked individually, but whose concentrations
$\tilde {c}$
can be measured for any
$k$
, time and space. Therefore, we consider the following state variables defining the mentioned level of description: the density of components
$\rho _{k}$
and the centre of mass velocity of the mixture
$\boldsymbol{u}$
as
\begin{align} \boldsymbol{u}=\sum _{k=1}^{n}\frac {\rho _k}{\rho }\boldsymbol{u}_k. \end{align}
We also define the total mixture density
$\rho$
and the diffusion flow of the
$k$
th component of the mixture as
\begin{align} \rho &=\sum _{k=1}^{n}\rho _k, \\[-12pt] \nonumber \end{align}
Therefore, the diffusion flow
$\boldsymbol{J}_k$
represents the momentum of the
$k$
th component relative to the mixture’s centre of mass. Summing
$\boldsymbol{J}_k$
over all components yields
\begin{align} \sum _{k=1}^{n}\boldsymbol{J}_k=\sum _{k=1}^{n}\rho _k\left (\boldsymbol{u}_k-\boldsymbol{u}\right )=\sum _{k=1}^{n}\rho _k\boldsymbol{u}_k-\sum _{k=1}^{n}\rho _k\boldsymbol{u}=0, \end{align}
meaning that only
$n-1$
of the flows are independent. As a result, we can replace the
$n$
inaccessible partial velocities
$\boldsymbol{u}_k$
with one state variable, the barycentric velocity
$\boldsymbol{u}$
, and
$n-1$
independent diffusion fluxes
$\boldsymbol{J}_k$
. For the unknown diffusion fluxes
$\boldsymbol{J}_k$
, we shall seek closures in terms of the state variables
$\rho _{k},\,\boldsymbol{u}$
.
We now rewrite the partial velocities
$\boldsymbol{u}_k$
in terms of the state variable
$\boldsymbol{u}$
and the yet unknown diffusion fluxes
$\boldsymbol{J}_k$
. By expressing the velocities
$\boldsymbol{u}_k$
from (2.3) and substituting them into (2.1), we obtain
By the virtue of the second law of thermodynamics, one can identify a suitable closure for the diffusion fluxes
$\boldsymbol{J}_k$
in terms of the chosen state variables. Because the fluxes obey
$\sum _k\boldsymbol{J}_k=0$
, only
$n-1$
constitutive relations are independent. For the binary mixture used later, we prescribe Fick’s law for the solute (index
$u$
),
and set
$\boldsymbol{J}_v=-\boldsymbol{J}_u$
for the solvent (index
$v$
). This is the simplest binary closure consistent with (2.5) (Lebon et al. Reference Lebon, Jou and Casas-Vázquez2008; De Groot & Mazur Reference De Groot and Mazur2013; Klika Reference Klika2021). The solute mass balance therefore takes the form
which is a standard advection–diffusion equation.
2.1.1. Fluid incompressibility
Let us now inspect the fluid incompressibility assumption and use it in the governing equations.
We first define a volume fraction
$\varphi _k$
, which simply represents the fraction of the volume occupied by the
$k$
th component with respect to the total volume. From the definition, the sum of all volume fractions satisfies the condition
\begin{align} \sum _{k=1}^{n}\varphi _k=1. \end{align}
We can now rewrite the density
$\rho _k$
as
where
$\rho _k^T$
is the so-called true density of the
$k$
th component of the mixture. The true density is defined as a density of the stand-alone component, that is, if it were not included in a mixture. Then, the incompressibility of a given component
$k$
means that
$\rho _k^T$
constant. Crucially, considering both the solvent and solute in our filtration problem to be incompressible does not result into the mixture being divergence free. That is because individual components in a mixture can rearrange in space; hence, their volume fraction volumes can change (Klika et al. Reference Klika, Whiteley, Brown and Gaffney2019). Consequently, rewriting the partial mass balances in terms of volume fractions, we obtain
The incompressibility of all the components of the mixture entails
\begin{align} 0={\boldsymbol{\nabla }} \,{\boldsymbol{\cdot }}\,\left (\sum _{k=1}^{n}\varphi _k\boldsymbol{u}_k\right )\!, \end{align}
by virtue of (2.9), but which is different from vanishing divergence of (barycentric) velocity.
Rewriting partial velocities
$\boldsymbol{u}_k$
in terms of diffusion fluxes
$\boldsymbol{J}_k$
, we get after some algebra that the incompressibility condition (2.12) can be expressed as
\begin{align} {\boldsymbol{\nabla }} \,{\boldsymbol{\cdot }}\,\boldsymbol{u}=-\sum _{k=1}^{n}\frac {{\boldsymbol{\nabla }} \,{\boldsymbol{\cdot }}\,\boldsymbol{J}_k}{\rho _k^T}. \end{align}
With the description of a mixture of incompressible components ready, we move to the description of the filtration problem.
2.2. Governing equations for filter
We identify the dimensional solute concentration with its partial mass density,
$\tilde {c}(\tilde {\boldsymbol{x}},\tilde {t}):=\rho _u(\tilde {\boldsymbol{x}},\tilde {t})$
, and denote the barycentric mixture velocity by
$\tilde {\boldsymbol{u}}$
. Thus,
$\boldsymbol{J}_u=-D\tilde {{\boldsymbol{\nabla }}}\tilde c$
and the solute balance becomes
where
$\tilde {{\boldsymbol{\nabla }}}$
denotes derivative with respect to the coordinate
$\tilde {\boldsymbol{x}}$
. Let
$\varGamma _s=\partial \varOmega _s\cap \varOmega$
denote the internal solid–fluid interface, excluding the external inlet and outlet boundaries. We represent adsorption of solute at this interface by
where
$\gamma \geq 0$
is an adsorption coefficient and
$\boldsymbol{n}$
is the unit normal pointing out of the fluid and into the solid. The advective contribution vanishes at
$\varGamma _s$
by the boundary condition on
$\tilde {\boldsymbol{u}}$
stated later; writing (2.14b
) directly as a diffusive flux avoids suggesting otherwise.
For simplicity, we neglect any changes to the filter geometry (clogging) due to the sedimentation of the solute on the surface
$\partial \varOmega _s$
.
2.2.1. Creeping flow of the mixture
We assume steady creeping flow of a Newtonian binary mixture, so inertia is neglected. This assumption concerns the momentum balance and does not impose
$\tilde {{\boldsymbol{\nabla }}}\boldsymbol{\cdot }\tilde {\boldsymbol{u}}=0$
. Indeed, for constant shear and dilatational viscosities, the Newtonian stress may be written as
Its divergence contains the gradient
$(\lambda +\mu )\tilde {{\boldsymbol{\nabla }}}(\tilde {{\boldsymbol{\nabla }}}\boldsymbol{\cdot }\tilde {\boldsymbol{u}})$
, which can be absorbed into a modified pressure
$\tilde p=\pi -(\lambda +\mu )\tilde {{\boldsymbol{\nabla }}}\boldsymbol{\cdot }\tilde {\boldsymbol{u}}$
. The steady momentum balance therefore has the familiar Stokes form even though the barycentric velocity need not be solenoidal:
Here,
$\tilde {p}(\tilde {\boldsymbol{x}},\tilde {t})$
stands for the pressure of the fluid and the constant
$\mu$
is its viscosity. We replace the fluid mass balance equation with the derived incompressibility condition (2.13). Rewriting it for a two-component mixture using our new notation, we obtain
where we used
$\boldsymbol{J}_v=-\boldsymbol{J}_u$
as a result of (2.5) for
$n=2$
. The index
$v$
denotes the fluid (solvent) and the index
$u$
denotes the solute. By substituting the assumed diffusion flux closure (2.7), we obtain the final form of the incompressibility condition as
It is important to note that the right-hand side of (2.16c
) is generally non-zero because we assume
$\rho _u^T\neq \rho _v^T$
for two different substances. As pointed out earlier, this non-zero term results from the observation that for an incompressible fluid, only the true densities
$\rho _k^T$
are constant. However, if we assumed incompressibility simply as the constancy of the overall densities
$\rho _k$
, the right-hand side of (2.16c
) would be zero, derived directly from the diffusion equation (2.8). Thus, our approach can be viewed as a generalisation of a special case with
$\tilde {{\boldsymbol{\nabla }}}\boldsymbol{\cdot }\tilde {\boldsymbol{u}}=0$
, corresponding to
$\rho _u^T=\rho _v^T$
, used for example by Dalwadi et al. (Reference Dalwadi, Griffiths and Bruna2015). We aim to explore in depth the effects of this non-solenoidal mixture velocity field. The final missing element is the boundary condition at the stationary, rigid, impermeable solid skeleton. We impose both no slip and no penetration of the barycentric advective velocity,
This does not suppress adsorption: solute mass crosses the interface through the diffusive flux in (2.14b ), while the mixture has no advective transport through the stationary solid.
2.2.2. Microscopic governing equations
The final forms of the detailed governing equations are obtained after non-dimensionalisation, see Appendix A for more details. Here,
$\delta$
is the ratio of the pore spacing to the macroscopic filter length, introduced at the beginning of § 2; throughout,
$0\lt \delta \ll 1$
. The equations describing diffusion of the solute are
and flow of the solvent
We introduced a dimensionless parameter,
$A= [(1/\rho _u^T)- (1/\rho _v^T )]c_\infty$
, with
$c_\infty$
being a characteristic solute concentration outside of the filter. Note that the ratio
$A/Pe$
measures the deviation from the classical incompressibility condition for a single component fluid, which would lead to a zero right-hand side of (A11b
), as described in § 2.2.1.
3. Effective macroscopic equations
Instead of solving the microscopic governing equations, (2.17) and (2.18), in a complicated microscopic geometry, we seek to find effective governing equations at a macroscopic level, where the details of the geometry are acting via the macroscopic coefficients.
To be able to derive a homogenised form of these microscopic equations, we follow the approach outlined by Bruna & Chapman (Reference Bruna and Chapman2015), Dalwadi et al. (Reference Dalwadi, Griffiths and Bruna2015) and Klika & Gaffney (Reference Klika and Gaffney2023), which allows the geometry to be almost periodic with mild spatial heterogeneity by the virtue of the method of multiple scales. Our purpose is a formal asymptotic derivation of the effective fluid and transport model, under smooth slow variation of the cell geometry and a clear separation of scales; we do not claim a rigorous convergence theorem for the present coupled problem. For rigorous tools applicable to related periodic problems, we refer the reader to two-scale convergence approaches (Allaire Reference Allaire1992; Allaire et al. Reference Allaire, Brizzi, Mikelić and Piatnitski2010; Allaire Reference Allaire2012).
Diagram of the filtration model for a two-dimensional square lattice, corresponding to the model description in § 3.1. (a) The physical graded filter is not globally periodic: its porosity varies on the macroscopic scale. (b) For each fixed macroscopic position
$\boldsymbol{x}$
,
$\omega (\boldsymbol{x})$
is the locally periodic reference cell on which the fast-variable corrector problems are posed. Cells at different values of
$\boldsymbol{x}$
need not be identical. Adapted from Dalwadi et al. (Reference Dalwadi, Griffiths and Bruna2015).

3.1. Multiple-scale analysis
We continue to use the variable
$\boldsymbol{x}$
for the description of the filter as a whole, to which we refer as the macroscale. However, we introduce a new variable
$\boldsymbol{y}= ({\boldsymbol{x}}/{\delta })$
defined locally in a unit cell
$\omega (\boldsymbol{x})$
, which will serve as a description for the microscale, see figure 1. The notation
$\omega (\boldsymbol{x})$
denotes a family of cells parametrised by the slow coordinate; it is not a single unit cell repeated unchanged throughout the physical filter. Similarly to the previous notation, we denote a solid part of the unit cell as
$\omega _s(\boldsymbol{x})$
and the rest of the cell accessible to the fluid as
$\omega _{\kern-1pt f}(\boldsymbol{x})=\omega (\boldsymbol{x})\setminus \omega _s(\boldsymbol{x})$
. We also denote the interface of these two regions as
$\partial \omega _s(\boldsymbol{x})$
and the boundary of the whole unit cell as
$\partial \omega (\boldsymbol{x})$
. The multiple-scale analysis requires that the solution is periodic in
$\boldsymbol{y}$
, while the variables
$\boldsymbol{x}$
and
$\boldsymbol{y}$
are considered independent (Bender & Orszag Reference Bender and Orszag1999). More precisely, the lifted fields and their correctors are
$\boldsymbol{y}$
-periodic for every fixed
$\boldsymbol{x}$
. The reconstructed physical field, for example,
$c^\delta (\boldsymbol{x},t)=c(\boldsymbol{x},\boldsymbol{x}/\delta ,t)$
, is generally not periodic because its cell geometry and slow dependence vary with
$\boldsymbol{x}$
.
Hence, we shall consider the unknowns
$\boldsymbol{u},c,p$
as functions of both
$\boldsymbol{x}$
and
$\boldsymbol{y}$
. The goal now is to switch from these variables dependent on the microscale
$\boldsymbol{y}$
to new effective variables dependent explicitly only on the macroscale
$\boldsymbol{x}$
. We define them by averaging over the unit cell
$\omega (\boldsymbol{x})$
as
where we applied that
$|\omega (\boldsymbol{x})|=1$
and
$c(\boldsymbol{x},\boldsymbol{y},t)=\boldsymbol{u}(\boldsymbol{x},\boldsymbol{y},t)=0$
for
$\boldsymbol{y}\in \omega _s(\boldsymbol{x})$
. We also introduce a porosity
$\phi$
indicating the local ratio of the available space to the total space as
Further, we also introduce the fluid-volume averaged quantities,
This choice seems more natural from the physical perspective as then, both fields are always expressed with respect to the fluid region (and, hence, the presence of a filter does not change their meaning) and thus, both unknowns are continuous even when porosity changes abruptly (as when entering or exiting the filter). Nevertheless, one can rewrite one in terms of the other,
$C=\phi C^{\kern-1pt f}$
and
$\boldsymbol{U}=\phi \boldsymbol{U}^{\kern-1pt f}$
, and for a direct comparability with the existing literature, and in particular with Dalwadi et al. (Reference Dalwadi, Griffiths and Bruna2015), we use the former definition of the macroscopic fields in (3.1).
3.1.1. Transformation of derivatives
As is standard, we replace the spatial gradients as
Hence, for the fluid system (2.18), we obtain after a multiplication by a suitable power of
$\delta$
(so that the lowest power of
$\delta$
is equal to
$\delta ^{0}$
),
For the diffusion system (2.17), we proceed analogously, however, the inhomogeneous boundary condition requires further care. We need to first describe the normal vector
$\boldsymbol{n}$
, perpendicular to the interface, and depending on both
$\boldsymbol{x}$
and
$\boldsymbol{y}$
. We now introduce a level set function describing the location of the interface,
$\chi (\boldsymbol{x},\boldsymbol{y})=R(\boldsymbol{x})-\|\boldsymbol{y}\|$
(hence, a geometry more general than a ball is admissible), while the interface is simply
$\chi (\boldsymbol{x},\boldsymbol{y})=0$
. Now, we just need to realise that the normal vector to the boundary points in the direction as follows (Klika & Gaffney Reference Klika and Gaffney2023):
where we defined a new unit vector on the microscale
$\boldsymbol{n}_y=-({\boldsymbol{y}}/{\|\boldsymbol{y}\|})$
. The normal vector
$\boldsymbol{n}$
can be then in line with previous reasoning redefined as
This normal follows from the total gradient of the particular physical level set
$\chi (\boldsymbol{x},\boldsymbol{x}/\delta )$
. It is therefore not an additional assumption that
$\boldsymbol n$
decouples into unrelated slow and fast fields. Alternative parametrised-cell approaches retain a general
$\boldsymbol n(\boldsymbol{x},\boldsymbol{y})$
and generate extra geometric terms when transport identities are applied (Burridge & Keller Reference Burridge and Keller1981; Holmes Reference Holmes2013; Penta et al. Reference Penta, Ambrosi and Shipley2014, Reference Penta, Ambrosi and Quarteroni2015). Those formulations address a broader geometry, while here we restrict to the level-set construction of Bruna & Chapman (Reference Bruna and Chapman2015) and Klika & Gaffney (Reference Klika and Gaffney2023). A rigorous comparison of the two formal limits is beyond the scope of the present fluid-mechanical model.
We may now transform the diffusion problem into the multiple-scales form, which reads (after a multiplication by a suitable power of
$\delta$
)
where we also multiplied (3.9b
) by the term
$\|\boldsymbol{n}_y+\delta {\boldsymbol{\nabla }}_{x} R(\boldsymbol{x})\|$
.
3.1.2. Multiple-scale expansion
We now expand the state variables in
$\delta$
into regular asymptotic expansions:
which finally gives the following form of the governing equations (3.6) and (3.9):
and
\begin{align} \delta ^2\frac {\partial {c_0}}{\partial {t}} & =\left (\delta {\boldsymbol{\nabla }}_{x}+{\boldsymbol{\nabla }}_{y}\right )\boldsymbol{\cdot }\left (\frac {1}{{Pe}}\left (\delta {\boldsymbol{\nabla }}_{x}+{\boldsymbol{\nabla }}_{y}\right )\big (c_0+\delta c_1+\delta ^2 c_2\big ) \right. \nonumber \\& \quad \left. -\delta \left (\boldsymbol{u}_0+\delta \boldsymbol{u}_1\right ) \vphantom{\frac{1}{2}}\left (c_0+\delta c_1\right )\right )\!, \hspace {10pt} \boldsymbol{y}\in \omega _{\kern-1pt f}(\boldsymbol{x}), \\[-10pt] \nonumber \end{align}
where we kept only terms up to the power of
$\delta ^2$
. Now, we put together all terms with the same power of
$\delta$
, which gets us equations for the leading order solutions
$c_0,\boldsymbol{u}_0,p_0$
and corrections
$c_i,\boldsymbol{u}_i,p_i, \hspace {3pt} i\in \mathbb{N}$
.
3.1.3. Order-by-order solutions
First, let us assume that
$A/{Pe}=\textit {O}(\delta ^{0})$
. Further, note that the no-slip fluid flow condition translates for all
$i\in \mathbb{N}_0$
into the same condition
Collecting the leading order problem
$\textit {O}(\delta ^{0})$
in the equations in (3.13) and (3.14), we obtain
The solution of (3.16) is
$c_0=c_0(\boldsymbol{x},t)$
, meaning that
$c_0$
is independent of
$\boldsymbol{y}$
. The homogeneous Neumann problem determines only that the fast-variable dependence is constant; that constant is the macroscopic field
$c_0(\boldsymbol{x},t)$
.
In the same manner, we obtain the leading-order equations for (3.13) as
Equation (3.17b
) is already satisfied by the solution
$c_0=c_0(\boldsymbol{x},t)$
of (3.16) and (3.17a
) is fulfilled by
$p_0=p_0(\boldsymbol{x},t)$
being independent of
$\boldsymbol{y}$
. Both
$c$
and
$p$
are therefore independent of the microscale
$\boldsymbol{y}$
in the leading order.
We now proceed to the first-order subleading problem, that is,
$\textit {O}(\delta )$
. Collecting terms with
$\delta ^1$
in (3.13), and utilising
$c_0=c_0(\boldsymbol{x},t)$
, yields
Similarly, the first subleading problem for solute transport reads
where we used the boundary condition (3.15) and the independence of
$c_{0}$
on
$y$
.
We substitute
${\boldsymbol{\nabla }}_{y}\boldsymbol{\cdot }\boldsymbol{u}_0= (A/{Pe}){\boldsymbol{\nabla }}_{y}^2 c_1$
from (3.18b
) into (3.19a
) and get
Note that the factor
$ (1-Ac_0 )$
is non-zero. Recalling definitions
$A= [(1/\rho _2^T)- (1/\rho _1^T )]c_\infty$
and
$\tilde {c}_0=c_\infty c_0$
entails
\begin{align} 1-Ac_0=1-\left (\frac {1}{\rho _2^T}-\frac {1}{\rho _1^T}\right )c_\infty c_0=1-\frac {\tilde {c}_0}{\rho _2^T}+\frac {\tilde {c}_0}{\rho _1^T}. \end{align}
If
$\tilde {c}_0=0$
, then also
$c_0=0$
and we simply obtain
$1-Ac_0=1$
. Now, let us assume that
$\tilde {c}_0\gt 0$
. From the definition of the true density, we have that
$\rho _1^T\gt 0$
and
$\rho _2^T\geq \tilde {c}_0$
, and thus,
$1- (\tilde {c}_0/\rho _2^T)\geq 0$
. All together, then
Hence, we may simplify the first subleading diffusion problem into
Equations (3.23) are linear in
$c_1$
and uncoupled from fluid flow equations (3.18). Their general solution contains a
$\boldsymbol{y}$
-independent first-order mean,
where
${\varGamma }(\boldsymbol{x},\boldsymbol{y})$
is a vector satisfying
Here, notation
$n_{y,i}$
denotes the ith component of the vector
$\boldsymbol{n}_y$
.
The last condition fixes the additive constant in the Neumann cell problem. Correspondingly, we choose the standard corrector gauge
$\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}c_1\,\,\mathrm{d}\boldsymbol{y}=0$
, which sets
$\bar c_1=0$
. This gauge leaves the leading-order macroscopic equations unchanged; retaining
$\bar c_1$
would only alter the
$O(\delta )$
reconstruction. Hence, the formula used in the following is (3.24) with
$\bar c_1=0$
.
The above-mentioned set of equations is called the cell problem and its solution
${\varGamma }$
is given directly by the geometry of our model. Also, let us note that in (3.25), the coordinate
$\boldsymbol{x}$
appears only through the choice of the unit cell
$\omega (\boldsymbol{x})$
. This means we can find the function
${\varGamma }$
for all cells simultaneously, where
$x$
acts as a parameter. For further theoretical evaluation, we consider the function
${\varGamma }$
as already known.
Now, returning to the flow problem, the right-hand side of (3.18b
) vanishes as
${\boldsymbol{\nabla }}_{y}^2 c_1=0$
. Thus, together with the boundary condition (3.15), we obtain
Equations (3.26) are again linear in
$p_1$
and
$\boldsymbol{u}_0$
, therefore, we can also factorise the solution as
where
$\unicode{x1D646}(\boldsymbol{x},\boldsymbol{y},t)$
is a matrix and
${\varPi }(\boldsymbol{x},\boldsymbol{y},t)$
a vector satisfying
The final condition fixes the arbitrary additive constant in the pressure corrector
${\varPi }$
; the velocity corrector
$\unicode{x1D646}$
is already fixed by its no-slip boundary condition. Here,
$\unicode{x1D644}_d$
denotes the identity matrix for the corresponding spatial dimension
$d$
, and the terms
${\boldsymbol{\nabla }}_{y}{\varPi },{\boldsymbol{\nabla }}_{y}^2\unicode{x1D646}$
represent matrices and
${\boldsymbol{\nabla }}_{y}\boldsymbol{\cdot }\unicode{x1D646}$
a vector defined for
$i,j\in \{1,{\cdots} \hspace {-0.7pt},d\}$
as follows:
\begin{align} \left ({\boldsymbol{\nabla }}_{y}{\varPi }\right )_{\bullet j}&={\boldsymbol{\nabla }}_{y}{\varPi }_j, \nonumber \\ \left ({\boldsymbol{\nabla }}_{y}^2\unicode{x1D646}\right )_{ij}&={\boldsymbol{\nabla }}_{y}^2\unicode{x1D646}_{ij}, \nonumber \\ \left ({\boldsymbol{\nabla }}_{y}\boldsymbol{\cdot }\unicode{x1D646}\right )_i&={\boldsymbol{\nabla }}_{y}\boldsymbol{\cdot }\unicode{x1D646}_{\bullet i}. \end{align}
As in the diffusion problem, by the factorisation, we managed to split the dependence on
$\boldsymbol{x}$
and
$\boldsymbol{y}$
. Functions
$\unicode{x1D646}$
and
${\varPi }$
are again dependent on
$\boldsymbol{x}$
only through the change of the boundary
$\partial \omega _s(\boldsymbol{x})$
and we can evaluate them for all cells
$\omega (\boldsymbol{x})$
at once. As with the function
${\varGamma }$
, we, for further progress, assume that the functions
$\unicode{x1D646}$
and
${\varPi }$
are known solutions to (3.28).
3.2. Macroscopic equations
In the next step, we derive governing equations for the macroscopic quantities
$C$
and
$\boldsymbol{U}$
by inspecting a solvability condition for the second subleading problem.
3.2.1. Diffusion
For the diffusion system (3.14), we continue with the asymptotic expansion to the second order in
$\delta$
:
\begin{align} \frac {\partial {c_0}}{\partial {t}} &={\boldsymbol{\nabla }}_{y}\boldsymbol{\cdot }\left (\frac {1}{{Pe}}\left ({\boldsymbol{\nabla }}_{x} c_1+{\boldsymbol{\nabla }}_{y} c_2\right )-\boldsymbol{u}_0 c_1-\boldsymbol{u}_1 c_0\right )\qquad \nonumber \\& \quad +{\boldsymbol{\nabla }}_{x}\boldsymbol{\cdot }\left (\frac {1}{{Pe}}\left ({\boldsymbol{\nabla }}_{x} c_0+{\boldsymbol{\nabla }}_{y} c_1\right )-\boldsymbol{u}_0 c_0\right ), \hspace {10pt} \boldsymbol{y}\in \omega _{\kern-1pt f}(\boldsymbol{x}), \\[-12pt] \nonumber \end{align}
\begin{align} -kc_0 & =\boldsymbol{n}_y\boldsymbol{\cdot }\frac {1}{{Pe}}\left ({\boldsymbol{\nabla }}_{x} c_1+{\boldsymbol{\nabla }}_{y} c_2\right )+\qquad \nonumber \\& \quad +{\boldsymbol{\nabla }}_{x} R(\boldsymbol{x})\boldsymbol{\cdot }\frac {1}{{Pe}}\left ({\boldsymbol{\nabla }}_{x} c_0+{\boldsymbol{\nabla }}_{y} c_1\right ), \hspace {10pt} \boldsymbol{y}\in \partial \omega _s(\boldsymbol{x}), \\[10pt] \nonumber \end{align}
Next, we integrate (3.30a
) over the fluid volume
$\omega _{\kern-1pt f}(\boldsymbol{x})$
as
\begin{align} \int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\frac {\partial {c_0}}{\partial {t}}\,\mathrm{d}\boldsymbol{y} &= \nonumber \\& ={\boldsymbol{\nabla }}_{x}\boldsymbol{\cdot }\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\left (\frac {1}{{Pe}}\left ({\boldsymbol{\nabla }}_{x} c_0+{\boldsymbol{\nabla }}_{y} c_1\right )-\boldsymbol{u}_0 c_0\right )\,\mathrm{d}\boldsymbol{y}-\int _{\partial \omega _s(\boldsymbol{x})}\hspace {-12pt}kc_0\,{\mathrm ds}, \end{align}
where we used the divergence theorem, the boundary condition (3.30b ) and the Reynolds transport theorem (Dalwadi et al. Reference Dalwadi, Griffiths and Bruna2015; Klika & Gaffney Reference Klika and Gaffney2023)
When the
$\boldsymbol{y}$
-divergence theorem is applied on
$\omega _{\kern-1pt f}(\boldsymbol{x})$
, its boundary consists of the solid interface and the outer faces of the reference cell. The integrals on each pair of opposite outer faces cancel because the correctors and their fluxes have matching periodic boundary values in
$\boldsymbol{y}$
. The remaining solid-interface integral is combined with the boundary condition and with the transport identity (3.32). The latter is associated with the level-set cell family chosen previously.
Note that (3.31) give the same result as the Fredholm alternative theorem (Allaire et al. Reference Allaire, Brizzi, Mikelić and Piatnitski2010), which states that the system (3.30) for the unknown
$c_2$
has a solution only if a condition given by (3.31) is satisfied.
Now, given
$c_0(\boldsymbol{x},t)$
is independent of
$\boldsymbol{y}$
and that
$\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\,\mathrm{d}\boldsymbol{y}=|\omega _{\kern-1pt f}(\boldsymbol{x})|=\phi (\boldsymbol{x})$
, (3.31) then simplifies to
\begin{align} \phi (\boldsymbol{x})\frac {\partial {c_0}}{\partial {t}}={\boldsymbol{\nabla }}_{x}\boldsymbol{\cdot }\left (\frac {1}{{Pe}}\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\left ({\boldsymbol{\nabla }}_{x} c_0+{\boldsymbol{\nabla }}_{y} c_1\right )\,\mathrm{d}\boldsymbol{y}-c_0\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\boldsymbol{u}_0\,\mathrm{d}\boldsymbol{y}\right )-kc_0|\partial \omega _s(\boldsymbol{x})|. \end{align}
If we define the Jacobi matrix
$ (\unicode{x1D645}_\varGamma )_{ij}= \partial {\varGamma _i}/\partial {y_j}, \hspace {3pt} i,j\in \{1,{\cdots} \hspace {-0.7pt},d\}$
, we can, using (3.24), write
\begin{align} {\boldsymbol{\nabla }}_{y} c_1={\boldsymbol{\nabla }}_{y}\left (-{\boldsymbol{\nabla }}_{x} c_0\boldsymbol{\cdot }{\varGamma }\right )={\boldsymbol{\nabla }}_{y}\left (-\sum _{i}\varGamma _i\frac {\partial {c_0}}{\partial {x_i}}\right )=-\sum _{i}\left ({\boldsymbol{\nabla }}_{y}\varGamma _i\right )\frac {\partial {c_0}}{\partial {x_i}}=-\unicode{x1D645}_\varGamma ^T\boldsymbol{\cdot }{\boldsymbol{\nabla }}_{x} c_0. \end{align}
Therefore, we have another form of (3.33) given only in terms of
$c_{0}$
:
\begin{align} \phi (\boldsymbol{x})\frac {\partial {c_0}}{\partial {t}}&={\boldsymbol{\nabla }}_{x}\boldsymbol{\cdot }\left (\frac {1}{{Pe}}\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\left (\unicode{x1D644}_d-\unicode{x1D645}_\varGamma ^T\right )\boldsymbol{\cdot }{\boldsymbol{\nabla }}_{x} c_0\,\mathrm{d}\boldsymbol{y}-c_0\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\boldsymbol{u}_0\,\mathrm{d}\boldsymbol{y}\right )-kc_0|\partial \omega _s(\boldsymbol{x})| \nonumber \\[5pt]&={\boldsymbol{\nabla }}_{x}\boldsymbol{\cdot }\left (\frac {1}{{Pe}}\left (\phi (\boldsymbol{x})\unicode{x1D644}_d-\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\unicode{x1D645}_\varGamma ^T\,\mathrm{d}\boldsymbol{y}\right )\boldsymbol{\cdot }{\boldsymbol{\nabla }}_{x} c_0-c_0\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\boldsymbol{u}_0\,\mathrm{d}\boldsymbol{y}\right ) \nonumber \\[4pt]& \quad -kc_0|\partial \omega _s(\boldsymbol{x})|. \end{align}
Noting that
$C(\boldsymbol{x},t)\sim \phi (\boldsymbol{x})c_0(\boldsymbol{x},t)$
at the leading order, we can rewrite (3.35) into
where
$\tilde {D}$
is the effective diffusion coefficient and
$f$
the effective adsorption coefficient defined as
\begin{gather} \tilde {D}(\phi )=\frac {1}{{Pe}}\left (\unicode{x1D644}_d-\frac {1}{\phi }\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\unicode{x1D645}_\varGamma ^T\,\mathrm{d}\boldsymbol{y}\right )\!, \\[-28pt] \nonumber \end{gather}
Evaluation of the effective macroscopic transport coefficients as a function of porosity for a two-dimensional square lattice. (a) Diffusion coefficient. The numerical evaluation (dashed line) is obtained by solving the cell problem (3.25) for various porosity values within the range
$\phi \in [1-\pi /4,1]$
using the FlexPDE software. The results are then plugged into (3.37) to obtain the plotted values. The closed-form approximation (solid line) represents evaluated expression (4.59). (b) Numerical solution of the cell problem (3.28) yielding the effective permeability coefficient
$\unicode{x1D646}=K\unicode{x1D644}_d$
as a function of porosity. The numerical solution requires care and is described in Appendix B.

As an illustration, we consider spherical inclusions as a representation of filter geometry, that is, by a collection of
$d$
-dimensional balls. In such a case, we can explicitly rewrite the function
$f(\phi )$
as
\begin{align} f(\phi )=k\frac {d(1-\phi )}{\phi }\left (\frac {V_d}{1-\phi }\right )^{\tfrac {1}{d}}. \end{align}
It is a direct consequence of the observations
where
$V_d$
represents a volume of a unit ball in
$d$
dimensions.
We illustrate the values of
$\tilde {D}(\phi )$
for spherical inclusions (filter geometry) in two dimensions in figure 2. Note that analytical approximations for several two-dimensional (2-D) packing of circles is available due to Rayleigh, see § 4.3 for details.
3.2.2. Fluid flow
As the last step of the homogenisation process, we find macroscopic equations for the pressure
$p$
and the velocity
$\boldsymbol{U}$
. We obtain a relation between
$p$
and
$\boldsymbol{U}$
at the leading order by integrating (3.27a
):
\begin{align} \boldsymbol{U}(\boldsymbol{x},t)&\sim \int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\boldsymbol{u}_0(\boldsymbol{x},\boldsymbol{y},t)\,\mathrm{d}\boldsymbol{y}=-\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\unicode{x1D646}(\boldsymbol{x},\boldsymbol{y},t)\boldsymbol{\cdot }{\boldsymbol{\nabla }}_{x} p_0(\boldsymbol{x},t)\,\mathrm{d}\boldsymbol{y} \nonumber \\ &\quad =-\left (\int _{\omega _{\kern-1pt f}(\boldsymbol{x})}\unicode{x1D646}(\boldsymbol{x},\boldsymbol{y},t)\,\mathrm{d}\boldsymbol{y}\right )\boldsymbol{\cdot }{\boldsymbol{\nabla }}_{x} p_0(\boldsymbol{x},t)\sim -\unicode{x1D646}_{\textit{eff}}(\boldsymbol{x})\boldsymbol{\cdot }{\boldsymbol{\nabla }}_{x} p(\boldsymbol{x},t), \end{align}
where we define the effective permeability tensor as
For a general cell,
$\unicode{x1D646}_{\textit{eff}}$
is a symmetric positive-definite tensor, as follows from the reciprocal identity proved in Appendix B. Symmetry alone does not imply isotropy. For the centred circular/spherical obstacles in the square, cubic and hexagonal lattices considered in our computations, the reflection and rotational symmetries of the cell imply
$\unicode{x1D646}_{\textit{eff}}(\boldsymbol{x})=K(\phi )\unicode{x1D644}_d$
. Only in those geometries do we use the scalar notation
$K(\phi )$
in the following.
The macroscopic equation for the fluid flow is obtained in a similar way as the above-mentioned diffusion equation. We have
by the virtue of
${\boldsymbol{\nabla }}_{y} c_0=0$
and
${\boldsymbol{\nabla }}_{y}\boldsymbol{\cdot }\boldsymbol{u}_0=0$
. Next, we use the Reynolds transport theorem (3.32) and the boundary condition (3.15) to rewrite the left-hand side of (3.43),
and
$C(\boldsymbol{x},t)\sim c_0(\boldsymbol{x},t)\phi (\boldsymbol{x})$
to rewrite the right-hand side,
Finally, by combining both (3.44) and (3.45), we obtain the last macroscopic governing equation in the form
describing the fluid flow through the filter.
3.3. Summary
Using the method of multiple-scales, we obtained the following set of effective macroscopic equations for the filtration problem in terms of averaged quantities:
describing our filtration model at the leading order as
$\delta \to 0$
. The macroscopic transport parameters
$\tilde {D},\,K$
and the volumetric adsorption
$f$
are given in terms of the microscopic domain geometry, and can be evaluated separately (from the cell problem) providing an explicit link to the microscale.
For completeness, we also list the final governing equations for the fluid-volume averaged macroscale quantity
$C^{\kern-1pt f}$
and
$\boldsymbol{U}=\phi \boldsymbol{U}^{\kern-1pt f}$
(3.3):
\begin{align} &=\frac {1}{\phi }{\boldsymbol{\nabla }}_{x} \phi \boldsymbol{\cdot }\big (\tilde {D}\boldsymbol{\cdot }{\boldsymbol{\nabla }}_{x} C^f\big )+{\boldsymbol{\nabla }}_{x}\boldsymbol{\cdot }\big (\tilde {D}\boldsymbol{\cdot }{\boldsymbol{\nabla }}_{x} C^f-C^f\boldsymbol{U}\big )-f \, C^f, \nonumber \\ {\boldsymbol{\nabla }}_{x}\boldsymbol{\cdot }\boldsymbol{U}&= \frac {A}{{Pe}}{{\nabla }}_{x}^2C^f, \\[-12pt] \nonumber \end{align}
Note that in the above-mentioned derivation, we assumed that
$A/{Pe}$
is
$\textit {O}(\delta ^{1})$
. We leave it with the reader to check that the upscaled governing equations are in fact the same even when
$A/{Pe}$
is of lower order in
$\delta$
. In particular, the leading order problem is unaffected and so is the first subleading problem.
4. Qualitative insight – unidirectionally graded filter
In this section, we explore some of the consequences of the derived macroscopic governing equations (3.47) focusing on the non-zero term in the divergence of the mixture velocity.
To achieve this, we study a specific filter example with a porosity change in only one direction, which we choose to be the same as the direction of the fluid flow. This allows us to rewrite (3.47) only as a one-dimensional problem. We denote the only spatial dimension by variable
$x$
, where we assume the filter region to be
$x\in (0,1)$
in accordance with the above-mentioned multiple-scales asymptotics. We also assume two reservoirs, one before the filter for
$x\in (-\infty ,0)$
and one after the filter for
$x\in (1,+\infty )$
. The fluid flow is induced from
$x=-\infty$
to
$x=+\infty$
. As the last condition, we assume the system in the steady state, meaning
$\partial {C}/\partial {t}=0$
. Then, the governing equations (3.47) for the specified model simplify to
Because we are interested mostly in a concentration profile, we have for now omitted (3.47c
), which connects pressure and fluid velocity. Let us also recall that the effective coefficients
$\tilde {D}(\phi )$
and
$f(\phi )$
are both functions of the porosity
$\phi (x)$
, which, for now, is an arbitrary function of
$x$
, but will be specified in later analysis.
4.1. Boundary conditions
Our aim is to derive boundary conditions at the filter boundary and hence be able to solve the one-dimensional system (4.1) only within the filter (and not on the entire line) to obtain the desired concentration profile of the solute. To this end, we consider the filter to be located in
$x\in [0,1]$
and we seek proper boundary conditions at the filter boundary, that is, at
$x\in \{0,1\}$
. The system (4.1) consists of one second-order and one first-order differential equation, thus, we need to find three boundary conditions. We first introduce boundary conditions for the whole system, including the reservoirs. Second, we extend the system (4.1) to both reservoirs and use its solution to determine the required boundary conditions at
$x\in \{0,1\}$
.
In particular, we define the upstream concentration and fluid velocity for
$x\in (-\infty ,0)$
as
$C^{-}$
and
$U^{-}$
. Analogically, we denote the downstream concentration and fluid velocity for
$x\in (1,+\infty )$
as
$C^{+}$
and
$U^{+}$
. Two of the three boundary conditions can be defined as inlet values of concentration and fluid velocity
This choice of inlet values is possible due to the renormalisation in Appendix A, where we only need to take the characteristic concentration as the average concentration of the system. The same applies also to the fluid velocity. We take the last third boundary condition as
which represents an expectation that far behind the filter, the concentration settles at a constant value, as in the absence of the filter, there is no cause for heterogeneity. However, this final value is still unknown and must be determined as a part of the solution.
These boundary conditions correspond to experimentally controllable quantities, while the effective conditions at the filter boundary are determined by the system and cannot be imposed directly.
4.1.1. Upstream equations
Having the inlet and outlet conditions (4.2) and (4.3), we can extend the system (4.1) to both reservoirs and find its solution. We first proceed for the upstream variables
$C^{-},U^{-}$
. We apply limit
$\phi \to 1$
to the system (4.1), which yields
Both equations can be integrated directly, giving
where
$\alpha ^{-},\beta ^{-}$
are integration constants. Substituting (4.5b
) into (4.5a
), we obtain a first-order separable differential equation
with the implicit solution
where
$\gamma ^{-}$
is another integration constant. Now, we take the opposite direction and substitute (4.6) back into (4.5b
), which yields the expression for the fluid velocity
In deriving the solutions (4.7), we assumed that
$\alpha ^{-}\neq 0$
, which can be justified as follows. If we take
$\alpha ^{-}=0$
, then by integrating (4.6), we obtain a quadratic equation for
$C^{-}$
:
The solution to (4.8) is
where we have included all constants under
$\gamma '$
. Now, considering the limit
$x\to -\infty$
, the term
$(2A{Pe}\beta ^{-} x)$
diverges, which contradicts the assumption (4.2a
). Therefore, the only possible correction is to set
$\beta ^{-}=0$
, which reduces
$C^{-}$
to the constant
However, looking back at (4.5b
), the flow velocity
$U^{-}$
would be in that case zero for the whole upstream interval
$x\in (-\infty ,0)$
, which is also a contradiction to (4.2b
). Therefore, the constant
$\alpha ^{-}$
must be non-zero.
Moreover, we can determine the first two integration constants
$\alpha ^{-},\beta ^{-}$
from the inlet conditions (4.2). For the limit
$x\to -\infty$
, the left-hand side of (4.7a
) approaches
$\pm \infty$
, depending on the sign of
$\alpha ^{-}$
. However, on the right-hand side, the only term capable of going to infinity is
$\ln |\beta ^{-}+\alpha ^{-}C^{-}|$
. Therefore, to satisfy equality for
$x\to -\infty$
, the following limit must apply:
Then, from the inlet concentration value (4.2a ), we obtain
Applying the limit
$x\to -\infty$
also to the expression (4.7b
) yields
which together with the previously derived relation (4.12) gives
These values can be substituted back to the upstream solution (4.7), giving its final form
Let us note that this result holds only under the assumption that
$A\neq 1$
, which is always satisfied. In fact,
$A\lt 1$
. To see this, consider the definition of
$A$
, the condition
$A\lt 1$
is equivalent to
\begin{align} \left (\frac {1}{\rho _2^T}-\frac {1}{\rho _1^T}\right )c_\infty \lt 1. \end{align}
Provided that
$\rho _1^T,\rho _2^T,c_\infty \gt 0$
, (4.16) can be rewritten as
We remind that the true density
$\rho _2^T$
corresponds to the solute, as does the characteristic concentration
$c_\infty$
. The true density is defined only through the volume related to the solute, whereas the concentration is defined throughout the entire volume. Since we chose the
$c_\infty$
as the average concentration within the mixture, it must hold that
$c_\infty \lt \rho _2^T$
. Therefore, the entire left-hand side of (4.17) is negative and the inequality is always satisfied, meaning the assumption
$A\lt 1$
is justified. Finally note that in the limit
$x\to -\infty$
, the left-hand side of (4.15a
) also approaches
$-\infty$
. Therefore, the term
$ (1-A )\ln |C^{-}-1|$
must also approach minus infinity, which is satisfied as
$A\lt 1$
.
4.1.2. Downstream equations
So far, we have specified the constants
$\alpha ^{-}$
and
$\beta ^{-}$
of the solution (4.7). To specify the third yet undetermined constant
$\gamma ^{-}$
, we would need yet another inlet condition. However, as shown in the following, we do not need the value of
$\gamma ^{-}$
to determine the filter boundary conditions at
$x\in \{0,1\}$
to have a well-defined problem.
In the same manner as in the upstream case, we arrive at the downstream equations:
By integrating and combining them, we obtain
where
$\alpha ^{+}$
and
$\beta ^{+}$
are integration constants defined analogously to the upstream case. Assuming that
$(\mathrm{d}C^{+}/\mathrm{d}x)\neq 0$
, solution to this equation is again in the implicit form (and same as the upstream solution):
with
$\gamma ^{+}$
being the last integration constant. However, we show that this solution is not admissible for the upstream problem. To see this, we consider the limit
$x\to +\infty$
in (4.19). The first two terms on the left-hand side approach zero due to
$(\mathrm{d}C^{+}/\mathrm{d}x)\to 0$
, giving the limit value for
$C^{+}$
:
Also applying the limit to the implicit solution (4.20), we see that the left-hand side approaches
$+\infty$
. The positive sign is a result of the limit
which is a consequence of
$U^{+}= [(A/{Pe}) (\mathrm{d}C^{+}/{\mathrm{d}x})]+\alpha ^{+}$
and
$ {\mathrm{d}C^{+}}/{\mathrm{d}x}\to 0$
as
$x\to +\infty$
. Additionally, because
$U^{+}$
is the fluid velocity behind the filter, the value
$\alpha ^{+}$
must be positive. However, on the right-hand side of (4.20), the term
$\ln |\beta ^{+}+\alpha ^{+}C^{+}|$
approaches
$-\infty$
as
$x\to +\infty$
, due to (4.21). Therefore, we must consider
which can be rewritten as
Going back to the limit value of
$C^{+}$
, we have
where we used the previously derived condition
$A\lt 1$
. This means that the outlet concentration
$C^{+}$
is higher than the inlet concentration
$C^{-}$
, which is physically incorrect, considering we have no sources of matter within the filter. Thus, the implicit solution (4.20) for the downstream concentration
$C^{+}$
is indeed not admissible.
Note however that the inadmissible solution was derived based on the assumption
$ {\mathrm{d}C^{+}}/{\mathrm{d}x}\neq 0$
. Returning now to the omitted special case, we can see that (4.5) can be solved supposing that
$C^{+}$
and
$U^{+}$
are constants. To match the previous notation, we denote them as
However, since these constants are outgoing values of the concentration and fluid velocity from the filter, they remain unknown and must be determined as a part of the final solution to (4.1).
4.1.3. Final boundary conditions
We derived the solutions (4.7) and (4.26) for both reservoirs before and after the filter. Despite not having determined the constants
$\alpha ^{+},\beta ^{+},\gamma ^{\pm }$
, we can use the knowledge of solutions to derive the boundary conditions for the filter itself and, hence, simplify the problem. For this purpose, we need a condition at the filter boundary
$x\in \{0,1\}$
connecting the external variables
$C^{-},C^{+},U^{-},U^{+}$
with the internal variables
$C,U$
. For this, it is sufficient to take the following relations:
which guarantee the continuity of solute concentration and fluid velocity at the filter boundaries. From a physical point of view, we also need to impose the continuity conditions of concentration flux
which can be derived by comparing (4.1a ) with (4.4a ) or (4.18a ).
Using these relations, we can finally derive the filter boundary conditions for the set of equations (4.1). We take the concentration flux continuity condition (4.29), whose left-hand side is from (4.5a
) equal to
$\beta ^{-}$
. Knowing that
$\beta ^{-}=-1$
, we obtain the final condition on the left filter boundary:
Similarly for the right boundary condition, we start from (4.30). Considering that
$C^{+}$
is constant, we obtain
This can be further amended using (4.28), yielding the final boundary condition on the right side of the filter,
So far, we have derived two Robin boundary conditions for the solute concentration equation (4.1a ). To complete the system, we also need a boundary condition for the fluid velocity equation (4.1b ). It can be obtained directly from the expression (4.7b ), using the derived constants (4.14) together with the relations (4.27) as
\begin{align} U=\frac {1-A}{1-\frac {AC}{\phi }}, \hspace {10pt} x=0. \end{align}
That the above-mentioned boundary condition is well defined is clear from the definition of
$C$
in (3.1), which, considering the already derived observation (3.22), leaves the denominator non-zero.
To summarise, we obtained the three desired boundary conditions at the filter boundary
$x\in \{0,1\}$
, which completes the well-posed description of the unidirectionally graded filter (4.1). Moreover, this allows us to separate the filtering task from the entire region with reservoirs and limit ourselves to the solution inside the filter only.
4.2. Slowly varying porosity
We now employ asymptotic methods to approximate the solution to the unidirectional filter. To this end, we consider a slowly varying porosity profile on the macroscale,
where we introduced a small perturbation parameter
$\epsilon \ll 1$
.
Next, we consider regular expansions of
$C,\,U$
and
$\phi$
in parameter
$\epsilon \to 0$
to the first order as is usual in perturbation theory:
Here,
$\phi _0$
is the mean porosity and is constant due to the assumption of the small porosity gradient (4.32). Further, we also expand the effective coefficients
$\tilde {D}$
and
$f$
to the first order in
$\epsilon$
:
where the terms in expansions, including the observation that the leading orders
$\tilde {D}_{0}$
and
$f_{0}$
are independent of
$x$
, can be identified by the following direct calculation. We Taylor expand
$\tilde {D}$
and
$f$
at
$\phi _{0}$
:
Comparing with the assumed form of expansion (4.34), we get the desired expressions for the asymptotic terms:
4.2.1. Leading-order solution
We substitute the expansions (4.33) and (4.34) into the set of (4.1) with boundary conditions (4.31a
), (4.31c
) and (4.31d
), and solve order by order in
$\epsilon$
. For the leading order, we obtain the equations
with the respective boundary conditions
\begin{align} U_0=\frac {1-A}{1-\frac {A C_0}{\phi _0}}, \hspace {10pt} x=0, \\[-12pt] \nonumber \end{align}
After some algebra, the set of (4.39) leads to a second-order differential equation with polynomial coefficients. A solution to such an equation is in the form of hypergeometric functions and is therefore not suitable for our purpose to obtain a closed form solution, in which higher-order solutions are expressed in terms of the lower orders.
Therefore, to progress further, we resort to one further simplification, that is, the constant
$A$
is of order
$\textit {O}(\epsilon )$
, specifically
Note that as
$A= [({1}/{\rho _2^T})- ({1}/{\rho _1^T})]c_\infty$
, its smallness is justified, for example, when the solution is dilute, and/or the true concentrations of the solute and solvent are not different by orders of magnitude.
Equation (4.39b ) with boundary condition (4.40b ) then decouples into
with the simple solution
The rest of the equations then form a second separate system,
being a second-order differential equation with constant coefficients. Therefore, the leading-order solution reads
where
\begin{align} a=\frac {1}{2\tilde {D_0}\phi _0}, \hspace {5pt} b=\sqrt {1+\frac {f_0}{a^2 \tilde {D_0}}} \end{align}
and
4.2.2. First-order solution
The leading-order solution corresponds to the case when
$A=0$
due to our simplifying assumption
$A=\textit {O}(\epsilon )$
. Therefore, the first-order solution represents a correction due to the effect of mixture of two incompressible components.
Again, substituting the expansions (4.33) and (4.34) into the set (4.1) with boundary conditions (4.31a
), (4.31c
), (4.31d
) and equating terms of order
$\textit {O}(\epsilon )$
, we obtain
\begin{align} \tilde {D_0}\frac {\mathrm{d}^2 C_1}{\mathrm{d} x^2}-\frac {1}{\phi _0}\frac {\mathrm{d}C_1}{\mathrm{d}x}-f_0 C_1 & =-\frac {{d}}{\mathrm{d}x}\left (\tilde {D_1}\frac {\mathrm{d}C_0}{\mathrm{d}x}-\frac {C_0}{\phi _0}\left (U_1+\tilde {D_0}\frac {\mathrm{d}\phi _1}{\mathrm{d}x}-\frac {\phi _1}{\phi _0}\right )\right ) \nonumber \\[5pt] & \quad +f_1 C_0, \hspace {10pt} x\in (0,1), \\[-12pt] \nonumber \end{align}
The boundary conditions are then
The flow equation (4.48b ) can be directly integrated, giving the solution
where
$\theta$
follows from the boundary condition (4.49b
), yielding
We note that with the velocity
$U_1$
determined, all the terms on the right-hand side of (4.48a
) are explicit known functions of space
$x$
. Therefore, we are left with an inhomogeneous second-order differential equation with constant coefficients. The solution can be readily found using the method of variation of parameters and reads
\begin{align} C_1(x) & =\frac {e^{ax}}{2ab\tilde {D_0}}\left [\left (\int G(x)e^{-(a+ab)x}\,{\rm d}\textit{x}+\gamma _1\right )e^{abx} \right. \nonumber \\[5pt]& \quad \left. -\left (\int G(x)e^{-(a-ab)x}\,{\rm d}\textit{x}+\gamma _2\right )e^{-abx}\right ]\!, \end{align}
where
$G(x)$
is defined as the right-hand side of (4.48a
). Further, the constants satisfy
\begin{align} \gamma _1& =\frac {\alpha }{2}\left (-(b+1)^2 e^{ab}\left (\beta _1(1)-\beta _1(0)\right )-\frac {(b+1)^3}{b-1}e^{ab}\beta _2(0)+\left (b^2-1\right )e^{-ab}\beta _2(1) \right . \nonumber \\[5pt]&\quad \left . +2\alpha b\frac {b+1}{a}\frac {\mathrm{d}\phi _1}{\mathrm{d}x}\left (1\right )-2\frac {(b+1)^2}{b-1}\phi _0 e^{ab}N(0)\right )+\frac {b+1}{b-1}\beta _2(0)-\beta _1(0) \nonumber \\[5pt]& \quad +2\frac {\phi _0}{b-1}N(0), \\[-12pt] \nonumber \end{align}
\begin{align} \gamma _2& =\frac {\alpha }{2}\,\Bigg ({-}\big (b^2-1\big ) e^{ab}\left (\beta _1(1)-\beta _1(0)\right )-(b+1)^2e^{ab}\beta _2(0)+(b-1)^2e^{-ab}\beta _2(1) \nonumber \\[5pt]&\quad +2\alpha b\frac {b-1}{a}\frac {\mathrm{d}\phi _1}{\mathrm{d}x}\left (1\right )-2(b+1)\phi _0 e^{ab}N(0)\Bigg ), \\[10pt] \nonumber \end{align}
with
and where we denoted the function
$N(x)$
as the right-hand side of (4.49a
).
4.3. Numerical solution
In this section, we solve the system (4.1) with the derived boundary conditions (4.31) numerically. To this end, the governing equations were rewritten as a system of first-order ordinary differential equations by introducing auxiliary variables for the derivatives. The resulting nonlinear boundary value problem was solved in MATLAB using the built-in solver bvp4c. Parameter sweeps were carried out using continuation, with each converged solution used as the initial guess for the next parameter value.
For the solution, we use a family of linear porosity profile parametrised as
where
$\phi _0$
is the mean porosity within the filter and
$m$
represents the degree of the porosity gradient. For example, for
$m\lt 0$
, the porosity gradient is negative, meaning the filter obstacle size is smallest at the entrance of the filter and increases in size with increasing
$x$
. The value
$m=0$
then represents a uniform filter with constant porosity.
Finally, note that unless we want to assess pressure, there is no need to calculate the permeability coefficient
$K$
from the cell problem (3.28) as the unknown pressure field
$p$
decouples from the two macroscopic quantities
$\boldsymbol{U}, C$
, see (3.47).
4.3.1. Square lattice
To evaluate the solution, we also need to specify the effective coefficients
$\tilde {D}(\phi )$
and
$f(\phi )$
which, as pointed out earlier, are dependent on the filter microscale geometry. The adsorption coefficient
$f(\phi )$
is for spherical inclusions (as a filter geometry) in two dimensions from (3.39) equal to
For the diffusion coefficient
$\tilde {D}(\phi )$
, we start from the closed-form approximation for a square lattice derived by Jóhannesson & Halle (Reference Jóhannesson and Halle1996):
where the volume fraction value on the right indicates the values for which the approximation is valid. As shown in figure 2, the approximation provides very good results for porosity
$\phi \gt 0.3$
.
Numerically obtained (a) fluid-volume averaged solute concentration
$C^{\kern-1pt f}=C/\phi$
and (b) fluid velocity
$U=\phi U^{\kern-1pt f}$
for three gradients
$m=-0.3,0,0.3$
. The evaluation is performed for a two-dimensional square lattice with the parameters
$\phi _0=0.75,\, A=0.6,\, {Pe}=3$
and
$k=1$
. Note that for the special case of divergence free flow field,
$A=0$
, the solution is
$U=1$
and, hence, it can be viewed as a measure of the effect of the novel term, being a result of treating the filtration problem as a true mixture.

Using the relations for the effective macroscale coefficients, we evaluate the solutions
$C^{\kern-1pt f}$
and
$U$
for various values of parameters
$A,\,{Pe},\,k$
and
$m$
in figure 3. We opt for the fluid-volume averaged quantity
$C^{\kern-1pt f}$
, which needs to be monotonic and flatten out to zero derivative when leaving the filter. The fluid flow velocity, however, is chosen to be
$U=\phi U^{\kern-1pt f}$
as it allows a simple comparison to the special case
$A=0$
(fluid flow being divergence free), where the solution is known to be
$U=1$
, see the following. As expected, the concentration value decreases with increasing
$x$
, as the solute particles are being filtered out throughout the filter. We also observe that with increasing porosity gradient, the rate of concentration change decreases. This behaviour is also to be expected, because as the porosity gradient increases, more contaminant is filtered out towards the front of the filter, where the filter obstacle size is larger. Therefore, the concentration near the front should decrease faster. The same logic applies to the end of the filter, where thus, the overall concentration profile becomes more uniform. Note that such observations hold for
$C^{\kern-1pt f}$
, not
$C$
.
In addition, note that the solute concentration
$C^{\kern-1pt f}$
does not enter the filter with the (normalised) free-flow upstream value, that is,
$C^{\kern-1pt f}(x=0)\neq 1$
. The reason is that, as we have shown already in § 4.1, the experimentally controlled influx conditions at
$x=-\infty$
translate into non-trivial Robin boundary conditions at the entry to the filter
$x=0$
, (4.31a
). As can be seen from the boundary condition (4.31a
) and also from the numerical solutions in figure 3, the filter presence and geometry significantly affect the composition of the mixture even before (upstream) the filter and entails various entry values of the solute concentration.
Numerically obtained concentration profiles for linear porosity (4.57) for
$A=0$
and
$A=0.6$
, hence, highlighting the effect of the new term. The evaluation is performed for a two-dimensional square lattice with the parameters
$\phi _0=0.75,\, {Pe}=3,\, k=1$
and
$m=-0.3,0.3$
. The lower two curves (solid and dashed) correspond to positive porosity gradient
$m=0.3$
, while the upper two to a negative porosity gradient
$m=-0.3$
. Note that the inlet solute concentration is affected (being larger for
$A\neq 0$
) as well as the amount of the particles being filtered out (again, being larger for
$A\neq 0$
).

To examine the effect of the non-zero mixture velocity divergence, that is, the right-hand side of (4.1b
), we already mentioned that we plot
$U$
instead of
$U^{\kern-1pt f}$
in figure 3(b). The velocity profile is affected significantly, as for
$A=0$
, the solution from (4.1b
) to (4.31d
) is
$U=1$
, regardless of the used porosity profile. In addition, we calculate and plot the effect on the concentration profile, see figure 4. We observe that increasing
$A$
leads to a more pronounced concentration change during the filtration. Therefore, this represents the first major qualitatively different result of our filtration model.
4.3.2. Hexagonal lattice
Until now, we have only examined the filtration process in dependence on various porosity profiles
$\phi (x)$
and parameters
$A,{Pe},k$
. However, the effective coefficients
$D(\phi ),f(\phi )$
from their definitions (3.37), (3.38) depend not only on the porosity
$\phi$
, but also on the geometry of the filter. This can be seen from the cell problem (3.25) and constitutes one of the advantages of an asymptotic approach to deriving the macroscale equations, as the method provides a link between microscale and macroscale description. The solution to the cell problem explicitly reflects the geometry of the unit cell
$\omega$
. To demonstrate this effect and link to the microscale, we introduce a new filter layout in the form of a hexagonal lattice in two dimensions (with the same spherical inclusions). We represent the hexagonal lattice by unit cells
$\omega = [-3^{-1/4},3^{-1/4} ]\times [-3^{1/4},3^{1/4} ]$
with one solid disk placed in the centre and a quarter of a disk placed in each corner of the cell. By this definition, we achieve a uniform distribution of the disks, while keeping the cell size at
$|\omega |=1$
.
To evaluate the solution for such layout, we first need to modify the effective coefficients
$D,f$
for this specific geometry. Since every hexagonal cell contains two disks in total, we can rewrite the adsorption coefficient analogous to (3.39) as
where the index H denotes the hexagonal lattice. Next, we take the diffusion coefficient from Jóhannesson & Halle (Reference Jóhannesson and Halle1996) using the same steps as for the square lattice in (4.59), yielding
Having specified the above-mentioned coefficients, we evaluate concentration profiles for the linear porosity (4.57) in figure 5. As expected, we observe slightly different results for both lattices, despite using the same porosity values. Specifically, we see that the hexagonal layout causes higher solute adsorption at the front of the filter. This may be a consequence of a more uniform distribution of the balls (disks) within the filter, in comparison to the square lattice. However, to confirm this phenomenon, further analysis would be required.
Numerically obtained concentration profiles for linear porosity (4.57) for square and hexagonal lattices in two dimensions. The parameters used are
$\phi _0=0.75$
,
$A=0.6,\, {Pe}=3,\, k=1$
and
$m=-0.3,0.3$
. The effect of microscale geometry and the capability of the asymptotic method to reflect these effects in the derived macroscale model is apparent.

4.3.3. Asymptotic approximation
Taking the advantage of having both numerical and approximate solution, we check their validity by mutual comparison. In particular, we compare the asymptotic approximation of the solution for slowly varying porosity with the numerical results obtained here.
For this purpose, we once again use the liner porosity profile
$\phi (x)=\phi _0+m(x-0.5)$
. Comparing it with the asymptotic expansion (4.33c
), we require
We also need to specify the effective coefficients
$\tilde {D}_0,\tilde {D}_1$
and
$f_0,f_1$
. The adsorption coefficients
$f_0$
and
$f_1$
can be determined from prescription (4.38) using the previously derived value (4.58) as
In the same manner, we obtain the diffusion coefficients from (4.37) using (4.59) as
\begin{align} \tilde {D}_1(x)&=\frac {\phi _1(x)}{{Pe}\,\phi _0^2}\left (-1+\frac {2(1-\phi _0)}{2-\phi _0-0.3058(1-\phi _0)^4}+\frac {\left (2+1.8348(1-\phi _0)^4\right )\phi _0}{\left (2-\phi _0-0.3058(1-\phi _0)^4\right )^2}\right )\!. \\[0pt] \nonumber \end{align}
With specified effective coefficients, we evaluate the asymptotic solution in figure 6. We see that the first-order approximation gives very good results in comparison with the numerical solution. We note that the deviation is slightly larger for the steeper gradient
$m=-0.3$
in figure 6(a), as should be expected because
$\epsilon =m$
.
(a,b) Asymptotic and numerical concentration profiles for linear porosity given by (4.57). The evaluation is performed for a two-dimensional square lattice with the parameters
$\phi _0=0.75$
,
$A=0.6, \textit{Pe}=3,\, k=1,\, m=-0.3$
in panel (a) and
$m=-0.1$
in panel (b).

This close form solution allows further qualitative understanding of the filtration’s dynamics. In particular, we may inspect the effect of key model parameters:
$ \textit{Pe}$
,
$A$
or the effect of porosity (
$\phi _{0}$
or
$m=\epsilon$
), see § 6.
5. Filter efficiency
For a better understanding of the filtration efficiency, we analyse the obtained solutions a little further. We note that the optimisation question does not have a single goal as there might be several similar but distinct goals. For example, one might wish to minimise the contaminant concentration in the outflux from the filter or maximise the particle adsorption. However, as we have already discussed, these are distinct goals (and dependent on
$A$
, that is, the solute and solvent properties, filter gradient, fluid flow characteristics). Further one may wish to maximise the adsorption per unit time or per filter lifetime.
We introduce several quantities measuring efficiency in various ways. First, we define a local adsorption rate in the filter
$\lambda (x)$
as
Note that this measure
$\lambda$
has to be given in terms of the fluid-volume averaged concentration
$C^{\kern-1pt f}$
and not
$C=\phi C^{\kern-1pt f}$
, see (3.48). Indeed,
$f C^f$
is the concentration sink of the solute in a given fluid volume per unit time. In contrast,
$C$
depends the local amount of filter, via
$\phi (x)$
, and hence, does not serve as a suitable measure of local adsorption rate. Since
$\lambda$
is the right-hand side of (4.1a
), it represents the amount of filtered contaminant per unit area and unit time at the position
$x$
. The corresponding values of
$\lambda$
for the concentration profiles depicted in figure 3(a) are shown in figures 7(a) and 7(c). We see that for the positive gradient
$m=0.3$
, the particle adsorption is significantly higher near the inlet of the filter than near the outlet. However, with a decreasing porosity gradient, the particle adsorption distribution becomes more uniform. This is consistent with the concentration change behaviour, which we discussed in § 4.3.
Although it is useful to observe the particle adsorption distribution throughout the filter, it would be more appropriate to know the total adsorption rate by the whole filter per unit time. This can be achieved by integrating the function
$\lambda (x)$
, which we define as a new metric
$\varLambda$
:
In our simple model of the filtration process, we simplify the filtration by completely removing the filtered out particles from the filter geometry. This assumption prevents the filter geometry from changing during the filtration process, which greatly simplifies the description. However, it also eliminates the possibility of filter clogging, which is in practice a very important property. Therefore, to fully analyse the filter efficiency, we need to estimate the clogging in a different way. To achieve that, we introduce a new metric
\begin{align} \overline {T}=\int _{0}^{1}\left |\tau (x)-\int _{0}^{1}\tau (s)\,{\mathrm ds}\right |\,\mathrm{d}x, \quad \tau (x)=\phi (x)/\lambda (x). \end{align}
describing the uniformity (in space) of time to local blockage of the filter, noting that
$\tau$
is proportional to time to local blockage of the filter, see figures 7(b) and 7(d). A smaller value of
$\overline {T}$
means the more evenly the contaminant is adsorbed within the filter. If particle adsorption is non-uniform, the filter accumulates more of the contaminant in individual parts and the risk of clogging increases. In an ideal situation, we want the filter to clog all at once, rather than in a single location. Therefore, for the best efficiency when measured by the longevity of the filter, we seek the minimum value of
$\overline {T}$
.
We plot two key profiles for efficiency characteristics for the case which was shown in figure 3. In panel (a), we show the adsorption profile
$\lambda$
and in panel (b), the uniformity of time to local blockage of the filter for linear porosity (4.57). A total measure of the former is in terms of
$\varLambda$
, while for the latter, we introduced
$\overline {T}$
in the text. In panels (c) and (d), we show the same characteristics, but for hexagonal lattice, as in figure 5, where the square lattice is in black curves while the hexagonal lattice in grey.

As a final measure of filter efficiency, we suggest
being proportional to the filtration capacity per filter lifetime (the total amount of removed solute before clogging). This reflects the uniformity of adsorption (and hence filling up the pores), but with respect to fluid volume available. We do not aim to employ the detailed information about the microsctructure; hence, the proposed measure
$R$
is based on an estimate of fluid volume available via porosity.
We may now search for optimal designs of filter with linear gradients using these measures. However, note that further one needs to specify which filtration scenario one wishes to optimise: with a given (i) fixed flow through the filter or (ii) fixed pressure drop across the filter. The former simply uses the decoupled fields
$U$
,
$C^{\kern-1pt f}$
to evaluate the measures, while the latter requires to assess pressure drop
$\Delta p$
across the filter and rescale the model parameters so that the pressure drop remains fixed. Note that to calculate the decoupled pressure field, one needs to solve the cell problem for
$K$
, which requires a careful numerical approach, see figure 2 and Appendix B.
5.1. Fixed flow through the filter, case (i)
We start by showing how the values of total adsorption rate
$\varLambda$
depends on the filter design with linear gradient profile (4.57) for a two-dimensional square lattice in figure 8(a). For a fixed gradient, that is, value of
$m$
, the value of
$\varLambda$
increases with decreasing
$\phi _0$
. This is not surprising since a decreasing mean porosity
$\phi _0$
results in a denser filter, allowing more of the solute to be filtered out. However, when fixing
$\phi _0$
and varying the gradient
$m$
, we obtain more interesting results. First, the values of
$\varLambda$
are asymmetric around the point
$m=0$
, showing that a positive gradient
$m$
leads to a better filter efficiency in the sense of total particle removal per unit time. However, as shown in figure 8(a), the asymmetry seems to decrease with non-zero
$A$
(
$A=0.6$
; black curves), which, in addition, seems to be generally improving the
$\varLambda$
characteristic for
$m\lt 0$
, although the values for fixed
$m$
are within
$5\,\%$
difference. Note that the dependence of total adsorption rate
$\varLambda$
highly depends on
$\phi _{0}$
with lower values yielding more pronounced asymmetry and maximum being for largest positive slope
$m$
. Note however that there is an exception for large porosity (in particular, for
$\phi _{0}=0.9$
) where the best performance is for
$m=0.027$
, see figure 8(b) for more details and comparison with
$A=0$
.
Numerically obtained two-dimensional square lattice with
$A=0.6$
,
$ \textit{Pe}=3$
and
$k=1$
) filter efficiency metrics: (a,b) total adsorption rate per unit time
$\varLambda$
; (c) uniformity of time to local blockage
$\overline {T}$
; and (d) filtration capacity per filter lifetime
$R$
for linear porosity (4.57) as a function of the porosity gradient
$m$
. Each curve represents a different mean porosity value
$\phi _0$
, starting from
$\phi _0=0.7$
for the solid curve, up to
$\phi _0=0.9$
(long dashed curve) with steps of
$0.05$
. At the same time,
$m$
is continuously varied to observe the effect of filter design. Red curves correspond to
$A=0$
(divergence free case), while black curves represent
$A=0.6$
case. The variation in average porosity
$\phi _{0}$
is depicted using different types of curve styles as shown in the boxed legend in panel (c).

When we inspect the filter efficiency from the perspective of performance in time, we obtain quite different results. Namely, high values of total adsorption rate
$\varLambda$
are typically linked with a high degree of non-uniformity of removal within the filter as is illustrated by the
$\overline {T}$
plot in figure 8(c). In view of those results, the uniformity of removal is significantly (by an order of magnitude) higher for negative porosity gradient
$m$
.
Similarly, the measure of filtration capacity per filter lifetime
$R$
reaches maximal values for negative filter porosity gradients with optimal values similar but not the same as for the measure
$\overline {T}$
, see figure 8(d).
Note that both measures
$\overline {T}$
and
$R$
show monotonous dependence on the average porosity
$\phi _{0}$
. A higher average porosity means a higher filtration capacity per lifetime
$R$
, but only for porosity gradients
$m$
larger than the optimal value for a given averaged filter porosity
$\phi _{0}$
. For smaller
$m$
, there is an interval for
$m$
such that this monotonicity is lost. In figure 8(d), this corresponds to the abrupt change in the plots of
$R$
versus
$m$
, which occurs due to the change in location of the filtration bottleneck (where the clogging event is expected to occur first). The uniformity of time to local blockage
$\overline {T}$
also shows monotonic dependence on the average porosity
$\phi _{0}$
, but where there are essentially two regimes separated by
$m\approx 0$
. For a smaller
$m$
, a larger
$\phi _{0}$
means a smaller
$\overline {T}$
up to the optimal value (minimum of
$\overline {T}$
with respect to
$m$
; below this optimal
$m$
, the monotonic dependence is lost). For
$m\gt 0$
, we have the opposite, that is, a larger
$\phi _{0}$
means a larger
$\overline {T}$
.
In addition, we show the effect of non-zero velocity divergence (scaled by the value
$A$
) on these filter performance measures. Location of the optimal filter gradients is shifted in every studied case to lower values of
$m$
, higher negative porosity gradients, see figures 8(c) and 8(d).
5.2. Fixed pressure drop across the filter, case (ii)
First, note that the decoupled system for
$C,\,\boldsymbol{u}$
, that is, (3.47a
), (3.47b
), is invariant under the scaling
The decoupled equation for pressure, (3.47c
), is in turn used to find a suitable scaling of the velocity field (including the inlet boundary condition
$U(x=-\infty )$
for the unidirectionally graded filter) so that the pressure drop across the filter
$\Delta p$
is fixed.
To reformulate the fixed (dimensional) pressure condition into a condition for
$\chi$
, we first choose a reference point, that is,
$U_{\textit{ref}}$
with a reference porosity gradient
$\phi _{\textit{ref}}$
and fixed parameter values
$ \textit{Pe},\,k$
(and non-dimensionalisation constants
$l, \mathcal{U}, \ldots$
). The corresponding reference pressure drop satisfies
and hence, we may write the condition of fixed pressure as
Therefore, we have a simple relation for the sought scaling
$\chi$
satisfying
\begin{align} \chi &= \int _0^{l} \frac {U_{\textit{ref}}(\boldsymbol{x}^*)}{K(\phi _{\textit{ref}}(\boldsymbol{x}^*))} \,\mathrm{d}x^* \left [\int _0^{l} \frac { U(\boldsymbol{x}^*)}{K(\phi (\boldsymbol{x}^*))} \,\mathrm{d}x^*\right ]^{-1}\\ &=\int _0^{1} \frac {U_{\textit{ref}}(\boldsymbol{x})}{K(\phi _{\textit{ref}}(\boldsymbol{x}))} \,\mathrm{d}x \left [\int _0^{1} \frac { U(\boldsymbol{x})}{K(\phi (\boldsymbol{x}))} \,\mathrm{d}x\right ]^{-1} = \frac {\Delta p_{\textit{ref}}}{\Delta p}.\nonumber \end{align}
Note however that as we use the fixed-flow solution with
$U(-\infty )=1$
and rescaled
$ \textit{Pe},\,k$
, the parameter values have to be rescaled with inverse scaling
$\chi ^{{-1}}$
to reach the fixed reference pressure drop.
In the following examples, we choose the reference point for pressure
$\Delta p_{\textit{ref}}$
as the minimum pressure drop on the
$\phi _{0}=0.7$
branch. To see the variations in pressure drops with varying filter design (still considering the linear gradients parametrised by the slope
$m$
and the average value
$\phi _{0}$
), we plot
$\Delta p/\Delta p_{{\textit{ref}}}$
for the considered filter designs (note that the minimum on branch
$0.7$
is 1) in figure 9. Note that even without invoking extreme values of permeability
$K$
, we can see one order of magnitude difference in pressure drops for fixed fluid flow and, hence, K potentially significantly affects the efficiency metrics.
Numerical results for a two-dimensional square lattice with the parameters
$A=0.6$
,
$ \textit{Pe}=3$
and
$k=1$
are shown. Changes in pressure drop across the filter in the unidirectional filter with linear porosity as a function of the filter design (that is, the slope
$m$
and its average porosity
$\phi _{0}$
). Note that we set
$\Delta p_{\textit{ref}}$
so that it corresponds to the pressure drop with
$\phi (x)=0.7-0.023(x-0.5)$
, that is, the minimum on the
$0.7$
branch. The dependence of pressure drop is nonlinear for
$A\neq 0$
and, hence, assessing the appropriate scaling requires to resort to the shooting method solving iterativelly the filter model equations.

We can see that the difference in the capability of instantaneous filtration given in terms of
$\varLambda$
is more pronounced in the fixed pressure drop when compared with the fixed-flow case, see figure 8(a) versus figure 10(a). Further, the optimality of the total adsorption rate of the whole filter per unit time has shifted towards a more symmetric result with respect to negative and positive slope of the porosity gradient. However, the optimal filter design when viewed from the perspective of
$\overline {T}$
and
$R$
became more sensitive to the porosity profile. In particular, the optimal values of
$m$
for various average porosities are more spread out. Finally, the significance of the non-zero
$A$
, that is, the novel term resulting from the description of the filtration problem as a mixture entailing the non-zero divergence of velocity, is increased for smaller values of porosity, as expected.
Numerically obtained two-dimensional square lattice with
$A_{\textit{ref}}=0.6$
,
$ \textit{Pe}_{\textit{ref}}=3$
and
$k_{\textit{ref}}=1$
) filter efficiency metrics for fixed-pressure drop across the filter (obtained by rescaling the fixed-flow problem): (a) total adsorption rate per unit time
$\varLambda$
; (b) uniformity of time to local blockage
$\overline {T}$
;and (c) filtration capacity per filter lifetime
$R$
for linear porosity (4.57) as a function of the porosity gradient
$m$
. Each curve represents a different mean porosity value
$\phi _0$
, starting from
$\phi _0=0.7$
for the solid curve, up to
$\phi _0=0.9$
(long dashed curve) with steps of
$0.05$
. At the same time,
$m$
is continuously varied to observe the effect of filter design. Red curves correspond to
$A=0$
(divergence-free case), while black curves represent the
$A=0.6$
case. The variation in average porosity
$\phi _{0}$
is depicted using different types of curve styles, as shown in the boxed legend in panel (b). Note that the location of optimal values of
$\overline {T}$
and
$R$
are in a great agreement (with a maximum difference being less than
$3\,\%$
) suggesting their close relation. In particular, the maxima for
$R$
and
$A=0$
are
$-0.348,\,-0.233,\,-0.147,\,-0.082,\,-0.038$
, while for
$A=0.6$
, we have
$-0.380,\,-0.257,\,-0.159,\,-0.088,\,-0.039$
. Note that the significance of the mixture composition represented by
$A\neq 0$
is increasing with decreasing porosity.

6. Discussion and conclusions
In this work, we have developed a generalised macroscopic model for filtration in graded porous media, accounting for non-solenoidal fluid velocity fields arising from solute–solvent coupling. The simplest performance metric considered is the outflux fluid-volume concentration,
$C^{\kern-1pt f}\!(1)$
. While we proposed several measures, this quantity provides the most accessible insight into the influence of individual model parameters.
From the leading-order asymptotic solution, we observe that the concentration
$C^{\kern-1pt f}_{0}\!(1) = C_{0}(1)/\phi (1)$
depends exclusively on the leading-order diffusion coefficient
$\tilde {D}_{0}$
, the average porosity
$\phi _{0}$
and the adsorption rate
$f_{0}$
. Consequently, in the limit of small porosity gradients, the leading-order filtration efficiency remains insensitive to both the specific filter design and the mixture composition (represented by the parameter
$A$
). In this regime, the process is governed primarily by the intrinsic transport and adsorption properties of the medium.
However, the first-order correction reflects the effects of both the composition of the mixture and the porosity gradient
$m=\epsilon$
. In particular, the correction
$C_{1}$
depends on the modified flow field through
$U_{1}$
, which itself depends on
$A$
(see (4.50)). Through this coupling, the composition parameter influences the transport term, and thus modifies the concentration profile and the resulting filtration efficiency. Consequently, even small porosity gradients introduce a weak but systematic dependence of the filtration efficiency on both the filter design and the mixture composition.
We also emphasise that different conclusions may arise depending on the chosen performance metric and on the experimental set-up. Relaxing the assumption of small porosity gradients by the virtue of numerical solution, when considering the total adsorption rate
$\varLambda$
, we find that it is somewhat less than twice as large for the average porosity
$\phi _{0}=0.7$
than for
$\phi _{0}=0.9$
. Moreover, in the former case, the total adsorption rate is more sensitive to the porosity gradient, while the influence of the mixture composition (
$A$
) remains relatively small, typically of the order of a few percent. In the fixed–pressure drop configuration, the situation changes: the total adsorption rate for
$\phi _{0}=0.7$
remains comparable to that in the fixed-flow case; however, it is approaching almost six times the value for
$\phi _{0}=0.9$
. In this regime, the influence of the mixture composition appears nearly negligible within the considered range of porosities.
In contrast, the filtration capacity per lifetime, denoted by
$R$
, exhibits a different trend. In this case, the performance is generally higher for larger porosity. Specifically, the peak value of
$R$
for
$\phi _{0}=0.9$
is approximately
$20\,\%$
larger than that for
$\phi _{0}=0.7$
, while for a given porosity gradient
$m$
,, it can be almost twice as large. For the fixed-pressure drop configuration, the influence of the mixture composition becomes less pronounced, whereas the significance of the filter design on the overall performance increases. These observations illustrate that different optimisation objectives may favour different filter configurations, and that performance measures such as
$\varLambda$
and
$R$
may lead to distinct design recommendations.
It is also instructive to consider the role of a non-zero coupling mixture parameter
$A$
. Recall that the flow velocity in the filter depends strongly on this parameter. In the special case
$A=0$
(velocity field being solenoid), we have
$U=1=U(-\infty )$
, corresponding to a uniform velocity profile. When
$A\neq 0$
, however, the velocity field adjusts in response to the coupled mixture dynamics. In particular, we observe that the velocity at the entrance to the filter is typically reduced below the upstream value
$U(-\infty )$
, with the magnitude of this reduction depending on both the filter parameters and the mixture composition. This observation highlights the importance of imposing physically appropriate boundary conditions in the model that correctly reflect the experimental configuration. In practice, although the upstream flow may be prescribed, the velocity entering the filter is determined by the resistance of the porous medium and the coupled transport processes, and therefore need not coincide with the imposed upstream value.
Another way to interpret the parameter
$A$
is that the filter performance depends on the composition of the mixture being filtered. In the fixed-flow configuration, the resulting differences may reach
$15\,\%$
–
$20\,\%$
for a given filter design (specified by
$\phi _{0}$
and
$m$
), with both increases and decreases possible depending on the parameter regime. In the configuration corresponding to a fixed-pressure drop, the effects of
$A\neq 0$
appear less significant, although this is only partially true. Note that the Péclet number
$ \textit{Pe}$
increases with
$\phi _{0}$
in this set-up, due to the rescaling associated with the imposed pressure drop, and therefore, decreases as the pores gradually close. Consequently, the additional transport contribution arising from the full mixture description, which is proportional to
$A/{Pe}$
, becomes increasingly important as the porosity decreases. This implies that even for arbitrarily small values of
$A$
or
$ \textit{Pe}$
, the contribution of this term eventually becomes non-negligible when the pores become sufficiently small.
Despite the improvements to the filtration model presented here, several limitations remain. While we have addressed the influence of graded porosity on transport, we have not explicitly accounted for the temporal evolution of the internal geometry due to particle accumulation. This phenomenon, known as filter blockage, has been explored in related contexts for periodic media through homogenised models of pore-scale narrowing (Dalwadi et al. Reference Dalwadi, Bruna and Griffiths2016). Incorporating such dynamic feedback into our non-solenoidal framework remains a subject for future research. Furthermore, the analytical insight into the resulting macroscopic filtration problem is inherently constrained by the complexity of the coupled governing equations. While the application of asymptotic methods allowed us to derive approximate solutions that reveal the physical significance of individual parameters, these results are not obtained in closed form and require numerical evaluation of the underlying cell problems.
Overall, our findings underscore the necessity of incorporating physically consistent mixture dynamics and boundary conditions in the modelling of porous filters. The interplay between filter architecture, operating conditions and the coupling effects within the mixture provides a robust foundation for the future optimisation of high-efficiency graded filtration systems.
Declaration of interests
The authors report no conflict of interests.
Appendix A. Dimensionless form of governing equations
For easier manipulation with the derived systems (2.14) and (2.16), we first convert them into a dimensionless form. To achieve this, we introduce new dimensionless variables
$\boldsymbol{x},\boldsymbol{u},t,c$
and
$p$
by relations
where
$l$
is a characteristic length (typically the macroscopic size of the filter),
$\mathcal{U}$
is a characteristic flow velocity and
$c_\infty$
is a characteristic solute concentration, all of appropriate unit dimensions. We assume that the new variables
$\boldsymbol{x},\boldsymbol{u},t,c$
and
$p$
are all of order
$\textit {O}(1)$
with respect to the small parameter
$\delta$
, introduced in § 2. This parameter serves as a basis for asymptotic expansions made later; therefore, all order comparisons are meant with respect to
$\delta \to 0$
. The pressure scaling factor
$ {1}/{\delta ^2}$
is based on a observation that pressure in a capillary is proportional to the inverse square of its radius. Since the pore size in our model is proportional to the parameter
$\delta \ll 1$
, we assume high pressure, specifically
$\tilde {p}\sim ( {1}/{\delta ^2})$
, as follows from the typical scaling of permeability with cross-sectional area of a typical pore. Together with the transformation of the variables
$\tilde {\boldsymbol{x}}$
and
$\tilde {t}$
, we also need to introduce new derivatives of the form
\begin{align} \begin{aligned} \frac {\partial }{\partial {\tilde {t}}}&=\frac {\partial {t}}{\partial {\tilde {t}}}\frac {\partial }{\partial {t}}=\frac {\mathcal{U}}{l}\frac {\partial }{\partial {t}}, \\[5pt] \frac {\partial }{\partial {\tilde {x}_i}}&=\frac {\partial {x_i}}{\partial {\tilde {x}_i}}\frac {\partial }{\partial {x_i}}=\frac {1}{l}\frac {\partial }{\partial {x_i}} \implies \tilde {{\boldsymbol{\nabla }}}=\frac {1}{l}{\boldsymbol{\nabla }}. \end{aligned} \end{align}
We now substitute the transformations (A1) and (A2) into the first set of equations (2.14):
and, after some algebra, we obtain
Next, we define two new parameters: the Péclet number
$ \textit{Pe}= {\mathcal{U}l}/{D}$
and parameter
$k= ({\gamma }/{\delta \mathcal{U}})$
, both assumed to be constant and of order O(1), that is, because we specifically focus on a situation where the adsorption coefficient
$\gamma$
is small with respect to other quantities in (A5), i.e.
$\gamma \sim \delta$
. By this choice of parameters, we obtain a diffusion equation where the size of the individual terms is given only by the explicit appearance of the parameter
$\delta$
. After substitution of the parameters
$ \textit{Pe}$
and
$k$
into (A5), we get a dimensionless form of the diffusion equation with boundary condition
We apply the same approach to the second set of equations (2.16). First, we use the transformations (A1) and (A2):
\begin{align} \frac {1}{l}{\boldsymbol{\nabla }} \,{\boldsymbol{\cdot }}\,(\mathcal{U}\boldsymbol{u})=\left (\frac {1}{\rho _2^T}-\frac {1}{\rho _1^T}\right )\frac {1}{l}{\boldsymbol{\nabla }} \,{\boldsymbol{\cdot }}\,\left (\frac {D}{l}{\boldsymbol{\nabla }}(c_\infty c)\right )&, \hspace {10pt} \boldsymbol{x}\in \varOmega _{\kern-1pt f}, \\[-12pt] \nonumber \end{align}
and after a few amendments, we obtain
\begin{align} {\boldsymbol{\nabla }} \,{\boldsymbol{\cdot }}\,\boldsymbol{u}=\left (\frac {1}{\rho _2^T}-\frac {1}{\rho _1^T}\right )c_\infty {\boldsymbol{\nabla }} \,{\boldsymbol{\cdot }}\,\left (\frac {D}{\mathcal{U}l}{\boldsymbol{\nabla }} c\right )&, \hspace {10pt} \boldsymbol{x}\in \varOmega _{\kern-1pt f}, \\[-12pt] \nonumber \end{align}
We also define a new constant
$A= [( {1}/{\rho _2^T})- ({1}/{\rho _1^T} )]c_\infty$
, which is apparently also dimensionless and of order O(1). Let us also note that
$A$
is generally non-zero, because we assume
$\rho _2^T\neq \rho _1^T$
for our two-component mixture, as described in § 2.2.1. Otherwise, we keep the constant
$A$
general for now. After the substitution of the constants
$A$
and
$ \textit{Pe}$
into (A10), we obtain a dimensionless set of equations for the fluid flow
Here, the term
$ {A}/{{Pe}}$
measures the deviation from the classical incompressibility condition as described in § 2.2.1.
Appendix B. Details of permeability matrix
$\unicode{x1D646}$
calculation
We first establish the property required in the main text without assuming a special cell geometry. Let
$\boldsymbol w^{(j)}=\unicode{x1D646}_{\bullet j}$
and
$\pi ^{(j)}=\varPi _j$
denote the velocity and pressure correctors driven by the unit vector
$\boldsymbol e_j$
. The cell problem (3.28) is equivalently
with no slip on the solid and periodic boundary values on the outer cell boundary. Testing the problem for direction
$j$
by
$\boldsymbol w^{(i)}$
, integrating by parts and using incompressibility, no slip and periodic cancellation gives the reciprocal identity
Consequently,
$(\unicode{x1D646}_{\textit{eff}})_{ji}=(\unicode{x1D646}_{\textit{eff}})_{ij}$
, so the effective permeability is symmetric. Moreover, for any non-zero constant vector
$\boldsymbol a$
,
provided the fluid cell is connected, proving positive definiteness.
The stronger reduction
$\unicode{x1D646}_{\textit{eff}}=K\unicode{x1D644}_d$
follows only when the cell geometry has the corresponding rotational and reflection symmetries. For the two-dimensional square cell with a centred circular obstacle, invariance under interchange of the coordinate axes gives
while reflection symmetry makes the cell average of the off-diagonal entries vanish. Thus, the diagonal cell averages are equal and
$\unicode{x1D646}_{\textit{eff}}=K\unicode{x1D644}_d$
. The same conclusion follows from the symmetries of the centred hexagonal and cubic cells used here.
For the square cell, the system of six unknowns can therefore be reduced computationally to
and
Although the microscopic off-diagonal corrector
$K_{12}$
need not vanish pointwise, its cell average vanishes by reflection symmetry; (3.42) then reduces to the scalar permeability used in the numerical section.
When implementing the above-mentioned system of equations numerically, great care has to be taken to avoid numerical blow up in the pressure relation. The issue lies in the compatibility of the numerical scheme with the property of the continuum system (B5). In particular, if we integrate the first and second equation over
$\omega _{f}$
and employ the periodicity of all the fields, we get
The former compatibility condition cannot be satisfied if there were no spherical obstacle or if there would be zero flux condition at the solid boundary. In other words, the periodicity of fields implies that there has to arise a non-zero flux of
$K_{11}$
such that it counterbalances the term
$|\omega _{f}|$
. In addition,
$p$
is determined up to a constant. Therefore, we implemented the cell problem for permeability tensor
$\unicode{x1D646}$
and vector
${\varPi }$
in terms of (B5) with finite differences, were the periodicity of all fields is directly enforced together with Dirichlet boundary conditions for
$K_{\textit{ij}}$
on
$\partial \omega _{s}$
, fixing
$p_{1}$
free constant (setting the mean to zero) and explicitly enforcing the compatibility conditions via Lagrange multipliers. Only then were we able to acquire results noting that the implementation resulted in at least
$10^5$
degrees of freedom (for the smallest porosity). The resulting linear problem was implemented and solved in MATLAB.


x
ω(x)
x
ϕ∈[1−π/4,1]
𝙆=K𝙄d
Cf=C/ϕ
U=ϕUf
m=−0.3,0,0.3
ϕ0=0.75,A=0.6,Pe=3
k=1
A=0
U=1
A=0
A=0.6
ϕ0=0.75,Pe=3,k=1
m=−0.3,0.3
m=0.3
m=−0.3
A≠0
A≠0
ϕ0=0.75
A=0.6,Pe=3,k=1
m=−0.3,0.3
ϕ0=0.75
A=0.6,Pe=3,k=1,m=−0.3
m=−0.1
λ
Λ
T¯
A=0.6
Pe=3
k=1
Λ
T¯
R
m
ϕ0
ϕ0=0.7
ϕ0=0.9
0.05
m
A=0
A=0.6
ϕ0
A=0.6
Pe=3
k=1
m
ϕ0
Δpref
ϕ(x)=0.7−0.023(x−0.5)
0.7
A≠0
Aref=0.6
Peref=3
kref=1
Λ
T¯
R
m
ϕ0
ϕ0=0.7
ϕ0=0.9
0.05
m
A=0
A=0.6
ϕ0
T¯
R
3%
R
A=0
−0.348,−0.233,−0.147,−0.082,−0.038
A=0.6
−0.380,−0.257,−0.159,−0.088,−0.039
A≠0