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Cocomposting of Beet Vinasse and Grape
Marc In Windrows and Static Pile Systems
M.J. Díaza, E. Madejónb, J. Arizaa, R. Lópezb & F. Cabrerab
a Departamento de Ingeniería Química, Química Física y Química
Orgánica, Escuela Politécnica Superior, Universidad de Huelva,
Huelva, Spain
b Instituto de Recursos Naturales y Agrobiología de Sevilla (CSIC),
Sevilla, Spain
Published online: 23 Jul 2013.
To cite this article: M.J. Díaz, E. Madejón, J. Ariza, R. López & F. Cabrera (2002) Cocomposting of
Beet Vinasse and Grape Marc In Windrows and Static Pile Systems, Compost Science & Utilization,
10:3, 258-269, DOI: 10.1080/1065657X.2002.10702088
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Compost Science & Utilization, (2002), Vol. 10, No. 3, 258-269
Cocomposting of Beet Vinasse and Grape Marc
In Windrows and Static Pile Systems
1
2
1
2
2
M.J. Díaz , E. Madejón , J. Ariza , R. López and F. Cabrera
1. Departamento de Ingeniería Química, Química Física y Química
Orgánica, Escuela Politécnica Superior, Universidad de Huelva, Huelva, Spain
2. Instituto de Recursos Naturales y Agrobiología de Sevilla (CSIC),
Sevilla, Spain
Two composts were obtained by cocomposting a concentrated depotassified beet
vinasse and grape marc using an aerated static pile and a windrow system. The com-
posting mixtures comprised grape marc (83%) and vinasse (17%) for the aerated sta-
tic pile system and grape marc (77%), vinasse (20%) and phosphate rock (3%) for the
windrow. Changes in temperature followed a similar path for both mixtures, how-
ever the thermophilic phase was longer in the aerated static pile (25 days) than in the
windrow (10 days). This fact caused differences in both organic matter degradation,
weight losses (21% for static pile and 10% for windrow) and gas losses during the
process. Nevertheless, the composts obtained by the two systems had a high fertiliz-
-1
-1
-1
er nutrient value (18.2 g kg N; 3.1 g kg P; 13.6 g kg K, C/N 16.1 for compost ob-
-1
-1
-1
tained in static pile and 20.6 g kg N; 13.7 g kg P; 13.1 g kg K; C/N 18 for compost
obtained in windrow). A high degree of stability was reached in both composting sys-
tems (124 cmol kg CEC for static pile and 153 cmolc kg CEC for windrow at 80
-1
-1
c
days of composting). The chemical and physical properties of both vinasse composts
suggest their possible use as soil conditioner.
Introduction
Concentrated beet vinasse is a high-density waste from the sugar industry. Vinasse
is usually considered to be highly polluting as it is produced in very large amounts
6
during a short season (10 million metric tons per year in Spain). Moreover, vinasse
presents two main environmental problems: a high organic strength (BOD 61-70 g O2
l-1) and high salinity (EC 250-300 dS m-1) (López et al. 1992).
Considering vinasse from the point of view of its organic matter (350 g kg-1 dw.)
and nutrient content (30 g kg-1 -N; 30 g kg-1 -K dw.), it constitutes a valuable resource
as a fertilizer and a source of nutrients and organic matter. However, the direct appli-
cation of concentrated vinasse on agricultural lands may lead to economical and envi-
ronmental problems due to its high salinity, low P content (0.12 g kg-1 - P2O5) and its
density (1,3 g cm-1) (López et al. 1992; Murillo et al. 1993).
Grape marc, a primary waste of wine production, can be recycled as fertilizer due
to its organic matter and nutrient contents. The direct incorporation of grape marc into
agricultural land, a common practice, has become a serious problem because the degra-
dation products can inhibit root growth (Inbar, et al. 1991). However, grape marc is
well balanced nutritionally, suitable for composting as produced and readily available
in the region (Andalusia, Spain).
To overcome these disadvantages and to recycle both wastes, an alternative is the
cocomposting of vinasse with grape marc. Composting is a low-cost natural way of re-
cycling organic matter.
The aim of this research was to investigate the cocomposting of vinasse and grape
marc using windrow and aerated static pile systems. The differences in control parame-
ters, mass balance and final characteristics of the composts obtained are also discussed.
258 Compost Science & Utilization
Summer 2002

Cocomposting of Beet Vinasse and Grape Marc in Windrows and Static Pile Systems
Materials and Methods
Design and Operation
Two composting piles were established with the following mixtures of grape marc
(GM) and vinasse (V) (dry weight percentages):
Aerated static pile: GM (83%) + V (17%)
Windrow: GM (77%) + V (20%) + PR (3%)
These proportions were mainly based on the vinasse-sorption capacity of the solid
waste, on the optimum moisture content and on the optimum free air space (FAS) of
the mixture for an optimum composting process (Díaz 1998). The windrow mixture
was complemented with phosphate rock (PR) to ensure a C/P ratio lower than 150
(Gray et al. 1971). Characteristics of the raw materials are reported in Table 1.
TABLE 1.
a
Some characteristics of the raw materials used in the composting process
Vinasse
Grape Marc
Average
Phosphate
Rock
b
b
Parameter
Moisture
Units
Average
SD
SD
-1
g kg
600
270
4.7
-
40
5.60
0.22
-
310
720
7.15
4.78
14.2
3.2
23
12.5
0.16
0.56
3.20
0.20
4.31
-
20
c
d
-1
OM (dw )
pH
g kg
-
-
-
e
-1
EC
dS m
-1
N (dw)
P(dw)
g kg
g kg
g kg
25
5.20
0.03
10.9
-
-
-1
-1
0.3
29.9
6
140
1.0
-
K (dw)
C/N
10.0
30
-1
-1
-1
Na (dw)
Ca (dw)
Mg (dw)
Fe (dw)
Cu (dw)
Mn (dw)
Zn (dw)
g kg
g kg
g kg
28
10.0
1.23
1.15
26
4.1
0.52
9.53
0.29
245
21
3.4
300
2.0
-
3.4
5.0
203
6
28.2
4.3
-1
-1
-1
-1
mg kg
mg kg
mg kg
mg kg
2870
90
-
-
10
-
50
11
-
15
4.0
115
13
-
a
e
b
c
d
Each value is the average of three samples; SD, standard deviation; OM, organic matter; dw, dry weight;
EC Electrical conductivity
Both mixtures were formed into trapezoidal piles under cover to avoid rainfall
that can cause a decrease of compost temperature and a reduction of compost activ-
ity (Hay and Kuchenrither 1990). Due to the small dimensions of the experimental
composting plant, each experiment was carried out in a different year. Both com-
posting systems were started in the same month (February) to avoid excessive dif-
ferences in the ambient temperature behavior.
Both piles were set up with the same size 3 m (length) x 3 m (width) x 1,5 m (height).
Physical and chemical characteristics of the initial mixtures are reported in Table 2. It is
interesting to note that both initial mixtures had C/N values lower than the optimum
value for composting (25-35; Gray 1971; Golueke 1972). This fact could lead to excessive
nitrogen losses during the process.
The aerated static pile was centered over three aeration lines consisting of per-
forated pipes (5 cm of diameter) installed in a groove in the concrete floor. Aeration
was provided by a blower which operated in the positive mode (forced aeration). The
pipes were covered to a depth of approximately 150 mm with cured compost to im-
Compost Science & Utilization
Summer 2002 259

M.J. Díaz, E. Madejón, J. Ariza, R. López and F. Cabrera
TABLE 2.
a
Physical and chemical characterization of the two initial mixtures
Aerated Static Pile
Average
Windrow
SD
b
b
Parameter
Units
Average
SD
c
d
-1
OM (dw)
g kg
644
19.2
18.6
3.0
34
721
21.0
19.0
13.4
11.9
8.2
21
-1
N (dw)
g kg
5.26
–
4.26
–
C/N
-1
P (dw)
g kg
0.31
1.04
1.15
5.69
1.36
236
4.20
6.12
12.2
–
1.12
1.26
2.15
3.18
0.95
142
2.36
3.26
10.8
–
-1
K (dw)
g kg
12.6
11.3
30.8
6.3
-1
Na (dw)
Ca (dw)
Mg (dw)
Fe (dw)
g kg
-1
g kg
24.0
4.3
-1
g kg
-1
mg kg
mg kg
mg kg
mg kg
mg kg
2110
39
1510
43
-1
-1
-1
-1
Mn (dw)
Cu (dw)
Zn (dw)
Pb, Cd, Cr, Co, Ni (dw)
Density
65
90
125
<5
136
<5
-3
g cm
%
1.60
70
0.25
4.10
1.57
69
0.08
3.36
Porosity
a
b
c
d
Each value is the average of three samples; SD, standard deviation; OM, organic matter; dw, dry weight
prove air distribution and prevent blocking of the holes in the pipes. The outer part
of the piles was not covered. The timer in the static pile was set in intervals of 15 min-
utes for three hours each day during the thermophilic phase and in intervals of 15
minutes for one hour each day during the mesophilic phase. Aeration design (0.15
3
m per minute per dry metric ton) was based on Haug (1993). Aeration was stopped
during the maturation phase.
The windrow was turned using a front end loader at 10 day intervals the first six
weeks of the process (the more active biooxidative phase). Golueke (1972) recom-
mended that the windrow needed to be turned for a total of seven turns maximum
during thermophilic phase. No turning was performed during the mesophilic phase.
During the thermophilic phase both piles were watered regularly to maintain
moisture contents of around 55% in accordance with a recommended range of 50-60%
(McKinley et al. 1985). No additional water was added during the mesophilic and mat-
uration phases.
Analyses
Temperatures and samples were taken at two depths (0-30 cm) and (40-100 cm) at
three randomized points of each pile. Sampling and temperature measurements were
made three to four times a week during the initial stage (more rapid degradation and
transformation) and weekly during the final stages. The temperature profile was
recorded by means of six replicates. Six subsamples of compost were taken from the
pile at the same times.
Moisture content was measured by drying at 105°C to constant weight. pH and
electrical conductivity (EC) were measured in a 1:5 (w/v) water-compost extract. To-
tal organic matter (OM) was measured at 550°C. Kjeldahl nitrogen determination was
performed according to Hesse (1971). Mineral elements (Na, K, Ca, Mg, Fe, Mn, Cu,
Zn, Ni, Cr, and Pb) were determined after mineralization by atomic spectrophotome-
try (Hesse 1971) and total P was determined by colorimetric method using the phos-
phovanadomolibdic complex (Hesse 1971).
260 Compost Science & Utilization
Summer 2002

Cocomposting of Beet Vinasse and Grape Marc in Windrows and Static Pile Systems
Elemental analysis (C, N, O, H) of the initial mixtures and final composts was per-
formed in a Perkin-Elmer model 240 C Elemental Analyzer (Perkin-Elmer, Norwalk,
Connecticut):
Cation exchange capacity (CEC) of compost samples was determined according to
Harada et al. (1981). In vitro assay of germination and root growth for Lepidium sativum L.
seed was performed using compost water extract (1:10 w/v) (Zucconi et al. 1981 modified
by Díaz Burgos 1990). Germinated seeds and root length were recorded after 48 h, and a
germination index (GI) was obtained for each species by multiplying the germination per-
centage (%G) by the root length percentage divided by 100.
3
Determination of porosity of the mixtures was carried out in tubes (0.07 m ; 1 m
long and 30 cm of diameter). The tubes were filled with compost, then water was slow-
ly added until filling the tube completely, shaking slightly to avoid the formation of
air bubbles inside the compost mass. The difference between the initial and the final
weight is considered as the volume of pores (the volume occupied by the micropores
where the water could not penetrate was assumed to be negligible) (Díaz, 1998).
Density of the mixtures was determined in dry samples by Helium gas pycnome-
try, using a Quantachrome model MVP-1 instrument (Quantachrome, Boynton Beach,
Florida). Three measurements were carried out for each material in the same condi-
tions. (Sacks et al. 1991).
Mass Balance
A schematic mass balance for batch compost systems is shown in Figure 1.
A total mass balance gave:
IS+ IM+ WI+ OI = FS + FM + WO + CO + NH . . . . . . . . . . . . . (1)
2
3
The oxidation of the biodegradable solids in the mass occurs according to equa-
tion 2. It was assumed that in the mass balance initial non-biodegradable solids are
equal to final non-biodegradable solids (Haug 1993).
C H O N + 0.5 (ny + 2s +r -c) O --> n C H O N + s CO2+ r H2O+ (d-nz) NH3 . . (2)
a
b
c
d
2
w
x
y
z
where
r = 0.5 [ b - nx – 3 ( d- nz)] . . . . . . . . . . . . . . . . . . . . . . (3)
and
s= a - nw . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . (4)
Figure 1. Mass balance for batch compost system.
Compost Science & Utilization
Summer 2002 261

M.J. Díaz, E. Madejón, J. Ariza, R. López and F. Cabrera
Throughout these equations carbon dioxide (CO2), ammonia (NH3) and water
(WO) produced for organic decomposition were determined. The stoichiometric oxy-
gen required for decomposition was determined from the organic feed decomposition
(Equations 2, 3, 4). It was assumed nitrogen input was equal to nitrogen output. A to-
tal water balance gave:
IM + WI + WR = WO + FM
Where: WR is the water produced in the stoichiometric reaction.
Results and Discussion
Temperature Changes
Three typical phases of composting were observed during the process (Figure 2).
(i) a short initial mesophilic phase (T<40°C) lasting approximately two days for both
piles. (ii) a thermophilic phase, during which the temperature increased (T>40°C) and
reached a maximum temperature of 58°C at five days of composting for both piles.
(iii) a maturation phase, when the temperature decreased slowly to mesophilic values
above 40°C in both piles.
During the thermophilic phase, slight increases in temperature were observed
in both piles. The thermophilic phase of the static pile was longer (25 days) than
that recorded for in the turned windrow (ten days). The length of the thermophilic
phase depends on the size and shape of piles and the system used (Haug 1993).
Moreover, the compost exposed surface area can have a significant effect on the
rate of heat lost (Haug 1993). It was considered that the higher heat loss in the
windrow was due to the larger exposed surface area to air in this composting sys-
tem during turnings.
Figure 2. Temperature (°C) changes in the piles during composting. The temperatures are the average of the values
recorded at the different depths in the pile (• pile temperature: - Air temperature). The arrows indicate the turning points
in windrow pile.
262 Compost Science & Utilization
Summer 2002

Cocomposting of Beet Vinasse and Grape Marc in Windrows and Static Pile Systems
After 80 days of composting, the temperature remained at 24ºC in aerated sta-
tic pile and 20ºC in windrow. The different aeration systems can result in differ-
ences in the temperature trend of the piles (Hay and Kucherither 1990; Tiquia et
al. 1996).
As the two experiments of composting were performed in different years, slight
variations in ambient temperature profiles were found.
Ammonium and Nitrate Evolution
-
+
NO3 -N and NH4 -N evolution in the compost mass during the composting
process is shown in Figure 3. A similar trend was observed for both piles with re-
-
spect to inorganic nitrogen evolution during the process. A high NO3 -N content
was observed of in both mixtures at the beginning of composting was observed
(1066 mg kg-1 for the aerated static pile and 460 mg kg-1 for the windrow). This fact
could be attributed to an initial nitrogen mineralization of the substrates during
-
their storage. The NO3 -N decreased during the thermophilic phase and then slight-
ly increased during the maturation phase to 599 mg kg-1 for aerated static pile and
411 mg kg-1 for windrow. Bishop and Godfrey (1983) reported that maximum nitri-
fication occurred at mesophilic temperatures. Other authors have reported similar
-
NO3 -N evolution during composting (Bishop and Godfrey 1983; De Bertoldi et al.
1982 Mahimairaja et al. 1994).
+
The NH4 -N content for both piles rapidly increased during the thermophilic
+
phase. The maximum of NH4 -N content was higher and occurred earlier in the
windrow (1580 mg kg-1 at 7 days) than in the aerated static pile (960 mg kg-1 at 10 days).
Studies on composting have shown that ammonification depends on parameters such
as C/N ratio, pH and temperature (Bishop and Godfrey 1983; Bonazzi et al. 1990,
Thambirajah et al. 1995). In this study, the C/N ratio of the composts, and the maxi-
-1
Figure 3. Inorganic nitrogen content (mg kg ) in the piles during composting (• NO -N; ꢀ NH -N). The arrows indicate
3
4
the turning points in windrow pile.
Compost Science & Utilization
Summer 2002 263

M.J. Díaz, E. Madejón, J. Ariza, R. López and F. Cabrera
mum of temperature and pH (8.5 and 8.2 at 10 days for aerated static pile and windrow
respectively) were similar in both systems. However, Nakasaky et al. (1992) showed
+
that turning frequency and the rate of air flow may affect NH4 -N evolution. The turn-
ings performed in the windrow system may have caused higher ammonification than
+
occurred in aerated static pile. After 25 days, the NH4 -N content decreased in both
piles reaching the initial values at the end of the processes. A similar tendency was ob-
served by Díaz Burgos et al. (1987); ), Nakasaky et al. (1992) and Bhanawase et al. (1994).
This decreasing trend guaranteed that ammonification was ending and can be used as
a criteria of compost maturity (Mathur et al. 1993).
Structural Changes
Some structural changes were observed during composting.
Initial porosity was 70% and 57.7% for the aerated static pile and the windrow re-
spectively. At 80 days, values of 69% for aerated static pile and 65.2% for windrow
were recorded. The porosity of the compost mass did not change during composting
using the static pile system whereas a noticeable increase in porosity was observed us-
ing the windrow system. Fulford (1987) did not find changes of porosity in the com-
post mass using the static pile system. However, important increases of porosity of the
compost mass were obtained using the windrow system (Haug 1993).
-3
-3
The density of the compost mass was 1.60 g cm and 1.57 g cm for the aerated sta-
tic pile and the windrow respectively at the beginning of the process. At 80 days, values
-3
-3
of 1.83 g cm for aerated static pile and 1.70 g cm for windrow were recorded. The in-
crease of density in both piles could be due to the organic matter losses and, therefore,
an increase of the inorganic fraction in the compost mass. Density of the inorganic frac-
tion (2 - 4 g cm ) is higher than the organic fraction density (0.4 - 1 g cm ) (Haug 1993).
In aerated static pile, a higher consumption of the organic matter and, consequently, a
greater increase of the inorganic fraction was observed. This fact explains the differences
in the final density, which were higher in the static pile than in the windrow pile.
-3
-3
CEC Evolution
TABLE 3.
The values of CEC during the
Evolution of CEC in compost
process for both piles are given in Table
3. CEC values depend on the starting
material. Its evolution and stabilization
have been proposed as an index of ma-
turity (Estrada et al. 1987; Saharinen
1996). CEC evolution was similar in
both piles and CEC values increased
steadily to reach constant values in the
during the process
Time Days
Aerated Static Pile
Windrow
a
a
CEC
CEC
-1
c mol kg
c
-1
c mol kg
c
1
6
66
68
70
74
nd
83
103
120
142
75
87
103
nd
116
nd
119
125
131
12
24
37
49
63
71
80
maturation phase (142 and 153 cmol
c
kg-1 respectively for aerated static pile
and windrow), in dicating compost sta-
bilization.
a
Volatile solid basis
Phytotoxicity Assay
Table 4 shows the evolution of %G (germination percentage) and GI (germina-
tion index) during composting in both piles. Phytotoxicity decreased during com-
264 Compost Science & Utilization
Summer 2002

Cocomposting of Beet Vinasse and Grape Marc in Windrows and Static Pile Systems
TABLE 4.
posting because toxic substances are
metabolized. As composting continued,
phytotoxicity decreased and finally dis-
appeared completely at the end of com-
posting process. Phytotoxicity disap-
peared at 60 days in the windrow,
whereas for the aerated static pile 80
days of composting were needed to
consider the compost free of phytotoxic
substances. The windrow system
seemed to be more efficient in sup-
pressing toxicity. Nevertheless the val-
ues of GI and %G obtained for both
a
Evolution of germination percentages (G%)
a
and germination index (GI)
in compost during the process.
Time(days)
Aerated Static Pile
Windrow
%G
%G
GI
GI
1
9
6
12
40
67
86
10
38
50
78
40
60
80
26
42
56
32
37
67
a
Values referred to the control
composts at the end of the process indicated the absence of phytotoxicity as indi-
cated by a (GI>60; (Zucconi et al. 1981).
Stoichiometric Data
As composting is considered to be a typical aerobic process, the final products of
the respiration are H2O and CO2. In an elemental analysis of waste for aerobic degra-
dation, only the four basic elements in the process (hydrogen, oxygen, nitrogen and
carbon) are taken into account. Analyses of mixtures are shown in Table 5. The per-
centages of the different elements were very similar for both mixtures. These stoichio-
metric relationships formulae were comparable to those found for other agricultural
residues (Haug 1993).
TABLE 5.
Elemental composition of the initial and final compost mixtures
Aerated Static Pile
Windrow
% Dry Weight
Initial
Final
Initial
Final
Carbon
40.87
4.95
33.61
3.46
44.52
4.96
39.92
4.25
Hydrogen
Oxygen
52.01
2.17
60.63
2.30
48.06
2.47
53.24
2.59
Nitrogen
Stoichiometric formula
C
H
O
N
C
H
O
N
C
H
O
N
C H O N
18 23 18 1
22 32 21
1
17 21 23
1
21 28 17
1
Mass Balance
After the maturation phase, the piles were weighed. From an initial mass of 9034
kg of dry solid, 7139 kg of dry compost was recovered in the aerated static pile. The
losses were 21% of the initial dry weight. In the windrow, from an initial mass of 9151
kg of dry solid, 8198 kg of dry compost were recovered. The losses were 10% of the ini-
tial dry weight.
The mass balance for both piles is shown in Table 6. The total estimated losses of
gases and leachates during the process were 8579 kg for aerated static pile and 4182 kg
for windrow. The estimated main gas losses consisted of carbon dioxide and water that
was evaporated from the compost (54.2% and 39.57% with respect to water input for
aerated static pile and windrow respectively). Ammonium losses were 43 kg for aer-
Compost Science & Utilization
Summer 2002 265

M.J. Díaz, E. Madejón, J. Ariza, R. López and F. Cabrera
TABLE 6.
Mass balance for aerated static pile and windrow
Aerated Static Pile
Inputs (kg)
Outputs (kg)
• Compost
Final solids
Final moisture
• Gases
• Raw material
Initial solids
Initial moisture
• Air
9034
4788
7139
4247
Stoichiometric O
(calculated)
• Water added
3336
987
Stoichiometric CO
(calculated)
Stoichiometric NH
(calculated)
3884
43
2
2
3
Evaporated water and leachates
(estimated)
4652
Total
18145
Total
18145
Windrow
Inputs (kg)
Outputs (kg)
• Raw material
Initial solids
Initial moisture
• Air
•
Compost
9151
3752
Final solids
Final moisture
Gases
8198
4345
•
Stoichiometric O
(calculated)
• Water added
2318
1504
Stoichiometric CO
Stoichiometric NH
(calculated)
2506
21
2
2
3
Evaporated water and leachate
(estimated)
1655
Total
16725
Total
16725
ated static pile (0.47% of the initial dry solids) and 21 kg for windrow (0.23% of the ini-
tial dry solids). Despite of the relative low values of C/N of the initial mixtures, low
N losses were observed in both systems.
In general, the total losses were higher in the aerated static pile system than in the
windrow system. This fact can be explained by the longer thermophilic phase record-
ed for the static pile, which thus caused a higher decomposition rate.
Quality of Compost
The main chemical characteristics of the final products are shown in Table 7.
Results revealed high amounts of macronutrients, particularly N, K and P. A high-
er P content was obtained in compost from windrow, due to the phosphate rock added
to this pile. Adequate C/N and C/P values for final compost were found in both sys-
tems. The low concentration of heavy metals confirms the safety of the original mate-
rials. These heavy metal contents were below the limits established by Spanish legis-
lation (BOE 1998).
The quality of the composts obtained in this study can be considered comparable to
the quality of other composts reported in the literature (Vallini et al. 1984; Zucconi and De
Bertoldi 1987; Tomati et al. 1995). The relative high EC value of the composts could be a
problem for their agricultural use. However, due to the quality of the composts, moder-
ate doses of the compost (15-20 Mg ha-1) should be sufficient to assure the nutritional re-
quirements of the crops without seriously increasing soil salinity (Madejón et al. 2001).
266 Compost Science & Utilization
Summer 2002

Cocomposting of Beet Vinasse and Grape Marc in Windrows and Static Pile Systems
TABLE 7.
a
Physical and chemical characterization of the two composts
Aerated Static Pile
b
Windrow
b
Parameter
Moisture
Units
Average
SD
Average
SD
-1
g kg
c
d
-1
OM (dw)
g kg
532
11.8
18.2
16.1
3.1
15.0
1.52
1.40
-
680
17.5
20.6
18.0
13.7
27.6
13.1
9.8
21.0
2.51
2.32
-
e
-1
EC (1:5)
mS cm
-1
N (dw)
C/N
g kg
-1
P (dw)
g kg
0.48
-
1.72
-
C/P
95.3
13.6
15.1
31.1
6.3
-1
K(dw)
g kg
1.54
1.70
3.25
0.61
210
8.58
5.16
13.2
-
1.70
1.76
4.84
0.12
320
11.0
5.22
21.0
-
-1
Na (dw)
Ca (dw)
Mg (dw)
Fe (dw)
Mn (dw)
Cu (dw)
Zn (dw)
Pb,Cd,Cr,Co,Ni. (dw)
Density
Porosity
a
g kg
-1
g kg
27.8
4.7
-1
g kg
-1
mg kg
mg kg
mg kg
mg kg
mg kg
2580
44
1900
46
-1
-1
-1
-1
53
96
113
<5
138
<5
-3
g cm
%
1.83
69.0
0.09
1.20
1.70
65.2
d
0.04
1.42
b
c
Each value is the average of three samples; SD, standard deviation; OM, organic matter; dw, dry weight;
EC, electrical conductivity.
e
Conclusions
Composting mixtures of vinasse (17-20%) and grape marc is technically feasible
using either windrow or aerated static pile composting systems.
Temperature profiles indicated that the process was successful in both systems. A
longer thermophilic phase was observed in the aerated static pile and thus, higher
weight (21% and 10% for aerated static pile and windrow respectively) and gas losses
were obtained using this composting system.
Changes in ammonium, nitrate and CEC were similar in both systems.
The increase of porosity of the compost was greater during composting in the aer-
ated static pile than that observed in the windrow. However, the evolution of the com-
post density was similar in both systems.
Each of the composts obtained had a high nutrient value, a high level of stability
and an absence of phytotoxicity and could be used to increase soil organic matter con-
tent and thus soil fertility.
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