Open access peer-reviewed chapter

Optical Methods Applied to Hydrodynamics of Cohesive Sediments

By Juan Antonio Garcia Aragon, Salinas Tapia Humberto, Diaz Palomarez Victor and Klever Izquierdo Ayala

Submitted: March 27th 2017Reviewed: November 9th 2017Published: December 20th 2017

DOI: 10.5772/intechopen.72347

Downloaded: 698


Suspended sediment transport in large rivers is constituted mainly by cohesive sediments, which form aggregates or flocs with primary particles less than 65 μm. The removal of cohesive sediments in aquaculture tanks is a difficult problem. Due to its size, density, and shape, the hydrodynamic behavior of flocs is very different from that of non-cohesive sediments as they depend on the interaction with the water column. This chapter describes the experimental results obtained in sedimentation tanks, reduced models of aquaculture recirculation tanks, and a rotating circular flume with Plexiglas walls, in which optical methods were used to determine flocs’ characteristics. These methods include particle tracking velocimetry (PTV) and digital holography for particle image velocimetry (DHPIV). Fractal models for floc density were successfully developed and validated with PTV experimental results in an aquaculture recirculation tank. Also, a model for the settling velocity of the flocs was validated using a permeable drag coefficient definition. Suspended sediments from Mexico’s two largest rivers, Usumacinta and Grijalva, with a mean flow rate near mouth of 1700 and 650 m3/s, respectively, were analyzed in a rotating circular flume. The shear velocity obtained in the field was reproduced in the circular flume and size and shape of flocs were obtained. This allowed to reproduce suspended sediment concentration profiles of rivers. DHPIV techniques were developed in order to obtain the actual size of the flocs based on Fresnel approximation for the reconstruction of holographic images.


  • floc
  • settling velocity
  • suspended sediments
  • fractal dimension
  • PTV

1. Introduction

Hydrodynamic behavior of cohesive sediments is important in many fields of engineering. A large part of the suspended sediment charge in large rivers is constituted by cohesive sediments as shown in the Amazon River sampling of suspended sediments [1]. A characteristic of cohesive sediments is to form aggregates (flocs) that behave in a very different way that non-cohesive sediments. Measuring in-situflocs settling velocities in rivers is not possible with conventional sediment sampling instruments. Recently, in-situoptical instruments are being used for floc size measurement, particularly in the field of oceanography [2, 3]. Those instruments are very expensive because they use laser illumination and are not used in common river engineering practice. In this chapter, a method based on suspended concentration sampling and laboratory particle size analysis in a rotating annular flume is used to obtain flocs size, and with an appropriate settling velocity model deduce the settling velocity to be used in the Rouse equation. The method is validated with sediments from Usumacinta and Grijalva rivers, the two major rivers in México, whose basins are located in the states of Chiapas and Tabasco near the Guatemalan border.

The settling velocity of cohesive sediments is an important design parameter in aquatic environments such as water treatment plants, storm water ponds, sediment filling in lakes, sedimentation in estuaries, dredging in rivers, and sediment removal in aquaculture devices especially when shortage of water is a concern [4]. The reuse of water is the main characteristic of the latter systems.

The efficient removal of solids is a main concern in these systems because of the accumulation of non-used food and fish excreta. These solids are generally less than 65 μm in diameter and behave as cohesive sediments [5]. These sediments form flocs or aggregates, made of water, inorganic particles, and organic particles [6, 7, 8]. To obtain adequate settling models for these particles is an active field of research [9]. Some researchers include variable fractal dimension functions that depend on a characteristic size of flocs that is difficult to obtain over a large population of flocs [10]. Other authors use geometrical parameters of flocs like floc perimeter, which is not easy to measure in engineering practice [11, 12]. The flocs’ settling velocity model proposed in this study uses parameters that are possible to average, using optical methods with some floc samples.

The tanks most widely used are circular [13, 14]. Water is supplied in these tanks by means of diffusers at the walls. In this project, a small scale circular water recirculation tank was used in order to study the solids behavior in the tank. There is a central settling device in order to remove the solids (Figure 1). The settling device functions according to the hydrociclons principle [15].

Figure 1.

Reduced model of an aquaculture recirculation tank.

Two optical techniques were used in this work, Particle Image Velocimetry (PIV) and Particle Tracking Velocimetry (PTV), to measure fluid and particle velocities, respectively. Polyamide tracers 25 μm in diameter were used to obtain fluid velocities using PIV, and flocs were tracked as particles in the PTV technique. PTV also allowed us to measure particle size and shape. Digital holography for particle image velocimetry (DHPIV) has also been used to determine the size and shape of flocs considering their volumetric nature.

The attempts to model settling velocity as a function of floc size, shape, and density demonstrated that density varies with floc size. Later work demonstrated that floc density depends on the fractal nature of flocs [16]. Recently, the effect of shear rate on floc density was demonstrated [11].

In this study, the results were used to calibrate settling velocity models using fractal theory and by including an adequate definition of the drag coefficient for permeable flocs. The proposed model is shown to provide reproducible results if a calibration of the parameters in the density vs. diameter model is properly done.

Suspended sediment samples obtained near the mouth of the Grijalva and Usumacinta rivers were analyzed in a rotating annular flume using PTV. It was possible to obtain appropriate values of the Rouse parameter ZR, which was shown to be difficult to obtain with classical granulometric and Coulter counter methods used in river studies [1].


2. Methods

2.1. Experiments using PTV and sediments coming from aquaculture recirculation tanks

Initial experiments were performed with fish food in order to have a better control of primary particles. The sediments where sieved and only those passing sieve 200 (0.075 mm), with a mean density of 1430 kg/m3 were used. A Plexiglas settling column was realized in order to allow the use of PIV and PTV optical methods. The set up consisted of a rectangular tank of cross section 15.5 × 15.5 cm and 100 cm height. A laser sheet was introduced from above using a double pulsed Nd:Yag laser (15 mJ), high-speed CCD cameras JAI (250 fps and resolution and 1600 × 1400 pixels) were mounted laterally to the column and synchronized by means of a NI-PCIE-1430 card with laser pulses. Both cameras where equipped with 50 mm NIKKON lenses. The cohesive sediments were introduced manually and images were captured at the 30, 60, and 90 cm marks from the bottom of the tank. The resulting frequency histograms are presented in the following of the paper. For the processing of the images, the software used was PTV-SED v2.1, developed at CIRA to analyze the fall velocity of sedimentary particles in two-phase flows. PTV operation comprises of two sequential procedures. The first procedure implies improving image quality through spatial filtering. The second procedure implies detecting particles in each pulse following the five stages proposed: (i) identify maximum and minimum intensity (black or white) over the particle image to determine its size; (ii) from the intensity of pixels of the evaluated particle, a circular area is formed which can be used to determine the cross-sectional particle area (A), and then the equivalent diameter (d) can be estimated using d=2Aπ1; (iii) from the cross-sectional particle area (A) and pixel intensity, the coordinates (x, y) of the drop centroid are determined; (iv) pairs of double-pulsed particle are identified and the distance separating their centroids (Δx, Δy) is determined; and (v) Particle velocity (vx, vy) is obtained as follows:


Then a small scale water recirculation tank made of Plexiglas 35 cm in depth and with 1.03 m diameter was used in the experiments with the same cohesive sediments from fish food. A complete system for water recirculation (Figure 1) was implemented. Water is obtained by a high rise tank with a constant water level in order to supply a constant flow rate by using gravity. Diffusers at different levels on the tank wall control the flow rate and tank water velocity, together with the generation of the circular flow. A settling device in the center of the tank allows solids removal.

Using this recirculation tank settling velocities and sizes of sediments were obtained from commonly used fish food and excreta coming from experimental station El Zarco, which cultivates trout. It is owned by Semarnap, the Mexican state agency of environment, natural resources, and fisheries, and is located at 2800 masl in Salazar Estado de México, México.

The next stage consisted to analyze suspended cohesive sediments coming from the Usumacinta and Grijalva rivers in México. In order to reproduce hydrodynamic conditions prevailing in the river and to analyze the flocculation process during long range experiments, an annular rotating flume, 1.3 m diameter and 15 × 15 cm flume cross section made of Plexiglas, was used (Figure 2). The cohesive sediments were analyzed using PTV, during 1.5 h. long experiments and images were taken every 15 min. From this experiment floc sizes and settling velocities were obtained.

Figure 2.

Rotating annular flume and PTV set up.

2.2. Theoretical settling velocity models

The greatest challenge in the proposal of a settling velocity model for flocs is the adequate definition of their density. Many models have been formulated for floc density [17], in this research the adopted model is the one proposed by Kranenburg [18], as shown in Eq. (2)


where ρf, ρw, and ρp are densities of floc, water, and primary particles, respectively, Dis the floc diameter and dis the primary particles diameter. Fis the fractal dimension and the model assumes that the floc is constituted of spherical primary particles of equal diameter. The model can be used for non-spherical particles with equivalent diameters.

A balance of drag forces and gravitational forces gives Eq. (3)


where Wsis the floc settling velocity and CDfis the permeable particle drag coefficient. Using Eqs. (2) and (3), the following relationship for the settling velocity is obtained


with Sis the primary particles relative density.

Using Particle Tracking Velocimetry methods (PTV), Garcia Aragon et al. [19] have shown that a useful relationship for the drag coefficient of a permeable floc has the following form:


where the coefficient ndepends on the kind of floc and varies, according to a comparison of results of different authors [20], between 1.1 and 1.25. Repis the particle Reynolds number defined as Rep = WsD/νwhere νis the kinematic viscosity of the fluid.

Replacing the relationship from Eq. (5) in Eq. (4), the following relationship for the settling velocity is obtained:


where Wsis in m/s and Dand din m.

As the fractal dimension changes with floc diameter, in this paper, we used a relationship proposed by Garcia-Aragon et al. [16] that has a form similar to the following:


where αand βare constants that depend on the kind of cohesive sediment. Maggi et al. [21] used flocculated kaolinite minerals in experiments in a settling column and found that the exponent βvaries between −0.092 and −0.112.

2.3. Application to suspended load estimation in large rivers

Authors working with the Mississippi river sediment transport Colby [22, 23], realized that the predicted Rouse number was not equal to the measured Rouse number in a series of sampled vertical profiles of the Mississippi. Also, researchers working in the three Gorges Reservoir in the Yangtze River show that settling velocities calculated with diameters obtained from particle size analyzers do not reproduce observed settling velocities, which indicate the existence of flocculation [24]. The formation of flocs in large rivers is the reason why Rouse equation cannot be used with particle sizes from classical granulometric measurements in conjunction with non-cohesive settling velocity equations. Recently, researchers working in the Amazon River and tributaries made similar observations [1]. Their conclusion was that granulometric measurements performed did not represent the real particle size because cohesive sediments agglomerate to form flocs [5, 6, 9] and after sampling, these flocs are destroyed and could not be measured appropriately in laboratory. On a related note, other researchers have shown that particle sizes in the Amazon River are lower than 70 μm [25, 26], which are in the size range of cohesive sediments.

To estimate the suspended sediment profile in stationary flows, the following Rouse equation is generally accepted [27]


where the Rouse parameter is ZR = Ws/Ku*, C(y) is the suspended sediment concentration at height y above bed, H is flow depth, ais a reference depth above bed, and Kis Von-Karman’s constant that for low sediment concentration is equal to 0.41.

In this project, Eq. (6) is used to estimate the settling velocity Ws, in conjunction with the Rouse Eq. (8) for the evaluation of the suspended sediment profiles in the Grijalva and Usumacinta rivers, the two largest rivers in Mexico.

2.4. Application of digital holography for PIV (DHPIV) for cohesive sediments characterization

Even if there are enormous advances in PIV and PTV techniques, there are shortcomings for 2D applications. The latter is observed in some physical phenomena, for example for the volume determination of a floc, which is only possible with 3D optical techniques. One of these techniques is digital holography for particle image velocimetry (DHPIV). This technique has been shown appropriate, for size distribution, volume determination, and particle velocity in fluids [30].

The DH method consists of specific steps as shown in Figure 3. Most experiments in scientific literature record a hologram following the so called in line system [28, 29, 30]. In this configuration, a coherent and collimated laser beam is sent, this is divided in two beams, one is directed toward the particles suspended in the fluid and is called the reference beam, while the dispersed light is called object beam. The two beams interfere to form a hologram which is recorded by the CCD digital camera (Figure 3). A typical particle hologram contains a succession of circular concentric interference strips which define the object in three dimensions.

Figure 3.

In line digital holographic system.

For application and calibration of a DH optical system, cohesive sediments from a waste water plant were used. A coagulant was added in order to allow floc formation in the rotating annular flume.

The physical components of the digital holographic system used are described in Table 1.

Green light laser diode532 nm wave length, 50 mW power
Microscope objective40×
Pinhole to expand and collimate beam10 and 5 μm
Lens to collimate the wave frontFocal distance f = 75 mm, 7 cm diameter
Polarizing filters
Glass container5 × 5 × 10 cm, glass width 3 mm
Digital camera Lumenera100 fps, pixel size Dx = Dy = 5.2 μm, 1200 × 1400 px
Sample of fluid to analyze

Table 1.

Physical components of digital holographic system.

Holographic images acquired and improved are reconstructed numerically in order to obtain 3D characteristics of flocs. The Fresnel method was used for image reconstruction [31].


3. Results

3.1. Experiments with cohesive sediments coming from food for fish

A first analysis of particles coming from fish food, using a Coulter counter analyzer, which destroys flocs, is shown below. The pellets were previously sieved and only those passing sieve 200 (0.075 mm) were conserved. It is observed (see Figure 4) that an average diameter of primary particles is 28 μm.

Figure 4.

Fish food particle sizes from coulter counter (LS 100Q) analysis.

Using the same fish food sediments optical methods were developed in a sedimentation tank. The following settling velocities were obtained at 60 cm from the top of the sedimentation tank by using PTV. It is observed in Table 2 that the settling velocity increases until a certain value (D = 200 μm) and then decreases for larger floc diameters. This behavior is not reflected in classical settling velocity models.

Floc size75100150200250300350400
Ws (cm/s)0.510.620.680.80.790.740.660.54

Table 2.

Average settling velocities for fish food in a sedimentation tank (cm/s).

3.2. Experiments with real flocs from an aquaculture recirculation tank

Next long-term experiments were performed in a reduced model of an aquaculture recirculation tank (Figure 1), flocs diameters and the corresponding settling velocities were measured for different times using PTV. The sediments used were real flocs coming from a large aquaculture recirculation tank (El Zarco). Some selected samples of the experiments were analyzed by Transmission Electron Microscopy (TEM) (Figure 5), at the beginning of the experiment (t = 0), at 15 min (t = 15), at 45 min (t = 45) and at 1 h (t = 60). An average diameter of primary particles of 28 μm was confirmed. Thus, this result was used in the statistical analysis.

Figure 5.

Representative values of fish food primary particles obtained by TEM.

In the experiments using the reduced model of an aquaculture recirculation tank, Eqs. (6) and (7) were used for the statistical analysis in order to define the parameters n, αand β. These parameters were defined according to the best correlation coefficient in the relationships Wsvs. Dand Fvs. D/d. Figure 6 shows the best fit of Fvs. D/daccording to Eq. (7). Table 3 shows the values of αand βobtained at each time.

Figure 6.

Fractal dimension vs.D/d: (a) at time 0 (upper left), (b) at time 15 min (upper right), (c) at time 45 min (lower left), and (d) at time 60 min (lower right).

Time (min)αβ

Table 3.

Best fit coefficients for the relationship Fvs. D.

The average value for the coefficient αwas 0.077 and the average value of the coefficient βwas 0.726. The latter exponent value is larger than the one obtained by [22] for a similar model, which can be explained with the structure of aquaculture flocs compared to Kaolinite, which is completely different.

Figure 7ad shows the best fit relationship between Wsand Dusing the Fvs. D/drelationship previously obtained. The resulting nvalues at different time steps are specified in Table 4.

Figure 7.

Settling velocity vs.D: (a) at time 0 (upper left), (b) at time 15 min (upper right), (c) at time 45 min (lower left), and (d) at time 60 min (lower right).

Time (min)n

Table 4.

Values of nfor best fit relationship between Wsvs. D.

Table 4 shows that the value of nincreases as the time of the experiment increases. This observation can be related to the increasing loss of density of the floc. As time increases, the flocs are increasing their volume absorbing water. The latter has two implications; the drag coefficient decreases because the floc becomes more porous and its density decreases.

An interesting feature observed in Figure 7ad is that the settling velocity of the flocs increases for values of floc diameter up to 600 μm and then decreases as floc diameter continues to increase. The settling velocity model proposed in this research is able to reproduce this behavior. This behavior has been shown to occur in nature for different kind of flocs, coming from estuaries, waste water treatment plants, and rivers [10, 19]. Most of the settling velocity models for cohesive sediments show an increase of settling velocity for all diameters which is not observed in this research. The larger flocs are formed after a long experimental period. In Figure 7a and b, there are few flocs larger than 600 μm, which is not the case for experimental periods of 45 and 60 min (Figure 7c and d). The practical implication of this phenomenon for aquaculture recirculation tanks is that residence times should not be very long because the larger flocs formed are even more difficult to settle down.

3.3. Experiments with suspended cohesive sediments of Grijalva and Usumacinta rivers

A sampling of suspended cohesive sediments in the Grijalva and Usumacinta rivers was done during high river level on the month of December 2016. The sampling location for the Grijalva was located before the junction with the Usumacinta, and in the Usumacinta, it was located 20 km upstream of the junction with the Grijalva. Samples were obtained at three vertical water columns in each cross section. For the Grijalva River, the samples were obtained at levels varying from 0.5 to 11 m (maximum water depth) each 1 m. At the Usumacinta River, samples were obtained at levels varying from 0.5 to 17 m (maximum water depth) each 1 m. Figures 8 and 9 show the suspended sediment concentration profiles for the Grijalva and Usumacinta Rivers, respectively. In these figures, the vertical axis refers to the level z adimentionized with the flow depth H, while the horizontal axis refers to the ratio of the concentration C to a reference concentration Ca.

Figure 8.

Suspended sediment concentration profiles for the Grijalva River. (a) 55 m from left bank and (b) 90 m from left bank.

Figure 9.

Suspended sediment concentration profiles for Usumacinta river. (a) 25 m from left bank and (b) 140 m from left bank.

An average value of Rouse parameter ZR = 0.214 was obtained in the Grijalva River, which is representative of a small increase of suspended sediment charge near the bottom.

An average value of ZR = 0.069 was obtained in the Usumacinta river. This value is representative of near constant suspended sediment charge in the water column.

Experiments in the rotating annular flume using 50 L samples for the Grijalva and Usumacinta rivers were performed at shear rates similar to those encountered in the field. Table 5 shows the values of shear velocity (u*) obtained in the sampling stations of the Grijalva (width 180 m) and Usumacinta (width of 340 m) rivers. The value of u* was obtained by the horizontal u’ and vertical fluctuating velocities w’ (u2=uw¯),where the over bar indicates an average over the water depth. The velocities were measured the same day of suspended sediment sampling with an Acoustic Doppler Current profiler (ADCP).

RiverDistance from left bank (m)u* (m/s)

Table 5.

Shear velocity in Usumacinta and Grijalva rivers.

Images of flocs after experimental runs of 1.5 h in the Grijalva river samples and 3.5 h in the Usumacinta river samples, in the annular flume using PTV, gave us an average size of flocs of 307 μm in the Grijalva and 209 μm in the Usumacinta. Table 6 shows the statistical values of flocs obtained in large runs at a shear velocity u* = 0.070 m/s (the average value in the Usumacinta river see Table 5) and Table 7 at u* = 0.043 m/s (the average value at the Grijalva river, see Table 5).

Time (min)D (μm)Number of data

Table 6.

Average floc size at the Usumacinta River from PTV experiments in the rotating annular flume.

Time (min)D (μm)Number of data

Table 7.

Average floc size at the Grijalva River from PTV experiments in the rotating annular flume.

Also, microscopic images of some representative flocs were obtained with 40× magnification. An average value of primary particle, after a statistical analysis of 50 flocs images for each river, gave an estimated value of 1.2 μm for the Grijalva river and 3.8 μm for the Usumacinta. Two representative images are shown in Figures 10 and 11.

Figure 10.

Primary particles and flocs representative of the Grijalva river.

Figure 11.

Primary particles and flocs representative of the Usumacinta river.

When Eq. (6) is used along with the already found average values of D and d, the values of settling velocity are obtained for different floc sizes (Table 8) using Eq. (7), with values of α = 0.07 and β = 0.72. The values of S were 1.29 for the Usumacinta river and 1.55 for the Grijalva river. Different values of n (Table 8) were used to show the sensitivity of the model to this compaction index.

nWs (mm/s)ZR

Table 8.

Estimated values of Ws and corresponding values of ZR.

Table 8 shows that the best estimation of ZR for the Usumacinta river is obtained with n = 1.1 because the average measured ZR (see Figure 8) was ZR = 0.069. Similarly, the best estimation of ZR for the Grijalva river is also obtained with n = 1.1 because the average measured ZR (see Figure 9) was ZR = 0.214. The larger concentrations near the bottom for the Grijalva river are explained by the larger size of flocs in this river (307 μm compared to 209 μm for the Usumacinta).

These results indicate that flocs of both rivers are strong flocs (low values of n), which is logical because shear rates at the Usumacinta and Grijalva rivers are high (for comparison u* at Amazon River varies between 0.07 and 0.1 [1]). It is also observed that the value of ZR in the Usumacinta river is more sensitive to changes in the value of n. It was observed that for large depths it is more difficult to define the n value as it can change even in the same cross section of the river at different levels.

3.4. Experiments using digital holography for PIV

Figure 12 shows the hologram reconstruction of a spherical particle of 50 μm. Figure 12a shows the particle’s hologram already filtered, where the different patterns of diffraction are observed; Figure 12b provides greater detail. The relative intensity profile (I/Imax) vs. reconstruction distance (z) is shown in Figure 12c. The maximum intensity is shown where the particle is in focus.

Figure 12.

Results of a reconstruction of hologram process. (a) Originally filtered hologram; (b) one particle hologram; (c) relative intensity profile, and (d) reconstructed particle.

Figure 13a shows the digital hologram of flocs, while Figure 13b shows a preprocess in order to avoid noise in the hologram. Rings of interference are observed in both figures, which define the 3D characteristics of the flocs. Figure 13c shows the reconstruction of the binary image. This image only shows the particles that are in the best focus, i.e., where the shape of the particle is clearly defined. In order to find the position in the plane, the diameter, and shape of the particle, the PTV algorithm for non-spherical particles was applied. Figure 13d shows particles pair detection and its centroid, which allows us to determine particles’ velocity for a sequence of holograms.

Figure 13.

Results of analysis of a digital hologram. (a) Original digital hologram; (b) processed digital hologram; (c) reconstructed hologram, and (d) size and shape of detected particles.

A settling column was used in order to observe the hologram evolution over time. Almost 100 holograms were processed each recording time. The times recorded were t = 0, 10, 20, 30, 45, and 60 min. Figure 14a shows particles distribution for holograms at time t = 0, and it can be observed that maximum size is 160 □m, with a mean diameter of 70 □m.

Figure 14.

Characteristics of flocs in settling column (a) frequency distribution of sizes at t = 0 min; (b) spatial distribution of flocs at t = 0 min; (c) frequency distribution of sizes t = 30 min; (d) spatial distribution of flocs at t = 30 min.

Figure 14c shows the distribution of particles at time 30 min, where an increase in size of flocs is observed attaining a maximum of 180 □m and a mean value of 80 □m. It is also observed that the shape of the distribution is log-normal, similar to theory. Figure 14d shows clearly a non-uniform distribution of particles in a hologram.


4. Conclusions

A model to estimate the floc settling velocity was calibrated for flocs obtained from aquaculture recirculation tanks that cultivate trout. The model was able to reproduce the values of settling velocity which varies between 0.01 and 0.025 m/s. For all the recording times analyzed there is a maximum settling velocity for flocs of diameter of 600 μm.

The representative values of the parameters used to determine fractal dimension are proposed in this research according to the experimental results. These values depend on floc density and vary with experimental time as flocs become more porous. The values found in this research apply to flocs coming from trout cultures in high level locations, i.e., 2800 masl.

The practical findings for aquaculture recirculation tanks design is that residence times should be short in order to minimize the presence of very large flocs. Middle size flocs settle faster. In designing the central settling device, which functions according to the hydrociclons principle, the up flow velocity should be less than 0.01 m/s in order to diminish the flow of sediments toward the recirculation deposit.

A method to obtain the suspended sediment concentration profiles for rivers with mainly cohesive sediments was presented. It is necessary to take some representative samples and using a rotating annular flume defines a steady state of flocculation after long-term runs. The most suitable method to analyze size and settling velocity of flocs are optical methods, PTV and microscopy. This research shows that the settling velocity can be accurately calculated with Eq. (6) in order to obtain an appropriate estimation of the Rouse number ZR. This allows us to properly determine the suspended sediment concentration profiles in rivers carrying a large amount of cohesive sediments.

Non-intrusive optical techniques are a suitable tool to characterize cohesive sediments, because they do not destroy flocs and allow for microscopic analysis. More advanced optical methods, like DHPIV, are showing good results for floc size and shape determination, thus in the future they will be the best method for cohesive sediment analysis.

© 2017 The Author(s). Licensee IntechOpen. This chapter is distributed under the terms of the Creative Commons Attribution 3.0 License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

How to cite and reference

Link to this chapter Copy to clipboard

Cite this chapter Copy to clipboard

Juan Antonio Garcia Aragon, Salinas Tapia Humberto, Diaz Palomarez Victor and Klever Izquierdo Ayala (December 20th 2017). Optical Methods Applied to Hydrodynamics of Cohesive Sediments, Applications in Water Systems Management and Modeling, Daniela Malcangio, IntechOpen, DOI: 10.5772/intechopen.72347. Available from:

chapter statistics

698total chapter downloads

More statistics for editors and authors

Login to your personal dashboard for more detailed statistics on your publications.

Access personal reporting

Related Content

This Book

Next chapter

Introductory Chapter: Applications in Water Systems

By Daniela Malcangio

Related Book

First chapter

Introductory Chapter: Water Sustainability in a Dynamic World

By Prathna Thanjavur Chandrasekaran

We are IntechOpen, the world's leading publisher of Open Access books. Built by scientists, for scientists. Our readership spans scientists, professors, researchers, librarians, and students, as well as business professionals. We share our knowledge and peer-reveiwed research papers with libraries, scientific and engineering societies, and also work with corporate R&D departments and government entities.

More About Us